PEACE RIVER SITE C H YDRO PROJECT
STAGE 2
BASELINE VEGETATION AND WILDLIFE REPORT
Prepared for BC Hydro Site C Project by
Keystone Wildlife Research Ltd.
2008 - 2009
PEACE RIVER SITE C H YDRO PROJECT
STAGE 2
BASELINE VEGETATION AND WILDLIFE REPORT
Prepared for BC Hydro Site C Project by Keystone Wildlife Research Ltd. July 2009
Lead Author: Lauren Simpson and Lorraine Andrusiak
Contributors: Cris Guppy (Butterflies, Dragonflies) (by section) Mandy Kellner (Bats) Curtis Bjork (Plants) Kyle Simpson (Ungulates) Shawn Hilton (Owls) Keith Simpson (Ungulates)
Task Lead Review by: Anré McIntosh
Accepted by:
Site C Hydro Project Stage 2 Vegetation and Wildlife Report
EXECUTIVE SUMMARY
As part of Stage 2, Project Definition and Consultation, BC Hydro engaged Keystone Wildlife Research Ltd. to complete wildlife and terrestrial studies in 2008 and 2009. The scope of the project was to collect baseline data including wildlife species presence, distribution and abundance. Taxa identified in the scope of study that required surveys include raptors and herons (nest sites), amphibians, owls, breeding birds, butterflies, dragonflies, vascular plants, bats, waterfowl, ungulates and rare ecosystems. This report summarizes the baseline data collected in 2008/09, aswell as data from studies completed in 2005 and 2006. This report is not a potential effects assessment.
Raptor/ Heron Nests
A raptor and heron nest survey was completed in May 2008. A follow-up survey was not completed, but the initial survey documented 25 active Bald Eagle nests, 11 of which were within the potential Site C reservoir. No heron nests were observed during surveys.
Review of nest survey data from 2005, 2006 and 2008 indicates that, in any one year, the potential Site C reservoir contains about half of the active large raptor nests present in the Peace River Corridor between Hudson’s Hope and the Alberta border. No evidence of heron nesting has been observed to date.
Other raptor species including Broad-winged Hawk, Northern Goshawk and Northern Harrier have been documented in the area. These species may nest in the river valley within the potential project footprint.
Amphibians
Pond-breeding surveys, auditory surveys and road surveys were completed for amphibians between May and August 2008, in the Peace River Corridor and along the existing transmission line. Species confirmed to be present and breeding in both study areas in 2008 include the western toad, boreal chorus frog and wood frog.
Three years of surveys have resulted in 236 wetland searches and 18.45 hours of auditory surveys in the Peace River Corridor and the existing transmission line. Five species have been July 2009 -i-
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documented and no correlation was observed between species occurrence and habitat type (e.g. marsh, fen, backchannel). Surveys indicate that breeding commences in late April (depending on local environmental conditions) and the timing of breeding overlaps between the different species. Higher activity was detected along the existing transmission line compared to the Peace River Corridor during auditory surveys.
Owls
Call-playback surveys were completed for Great Gray Owls, Great Horned Owls and Boreal Owls in May and June 2008, in the Peace River Corridor and along the existing transmission line. Forty-nine surveys were completed in 94.9 survey hours. Sixty-three owl detections of five species (Barred, Saw-whet, Great Horned, Great Gray and Boreal) were recorded in the Peace River Corridor and 15 owl detections of three species (Barred, Great Gray and Northern Saw- whet) were recorded along the existing transmission line.
Three years of surveys have resulted in 980 call-playbcak survey stations for Boreal, Barred, Northern Saw-whet, Great Gray, Great Horned and Short-Eared Owls. Eight owl species have been recorded in 399 owl detections, with Barred (n=103) and Saw-whet Owls (n=183) accounting for over half of these detections, despite these species not being targeted during most surveys. Surveys indicate that the number of Northern Saw-whet Owls in the Peace River Corridor is approaching the estimated maximum density for this species. Data suggests that Boreal Owls are uncommon in both the Peace River Corridor and the along existing transmission line and that Great Gray Owls and Great Horned Owls are more common in the Peace River Corridor, than along the existing transmission line.
Breeding Birds
Point count surveys were completed for breeding birds in May and June 2008, in the Peace River Corridor and along the existing transmission line. In total, 106 songbird species were detected during 223.7 hours of surveys at 783 stations. Seven Red- or Blue-listed species were detected.
Three years of surveys have resulted in completion of 1,931 point count stations in the Peace River Corridor and along the existing transmission line. In total, 116 songbird species have
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been detected, including 7 Red- or Blue-listed species. Analysis of habitat use for the Black- throated Green Warbler and the Canada Warbler indicates that the habitat used by these species in the study area is consistent with previously documented habitat preferences. Analysis of species diversity indicates that the Peace River Corridor has higher species diversity than the existing transmission line.
Butterflies
Surveys for butterflies were completed between May and August 2008, in the Peace River Corridor and along the existing transmission line. In total, 637 sites were surveyed resulting in the detection of 56 taxa. Eight Blue-listed taxa and five Red-listed taxa were detected.
Three years of sampling has resulted in 788 sites being surveyed in the Peace River Corridor and on the existing transmission line. Sixty-five different taxa have been detected, of which 14 were Red- or Blue-listed. Habitat associations for 10 of the listed taxa have been confirmed within the study area. Four listed species (Alberta arctic, coral hairstreak, striped hairstreak and bronze copper) were detected infrequently and habitat associations were not confirmed. Six species (old-world swallowtail, hudsonianus ssp., checkered skipper, Mead’s sulphur, mountain alpine, white-veined arctic, edwardsi ssp. and red-disked alpine) have not been detected in the study area to date, and should be removed from the list of potential species present in the study area.
Dragonflies
Baseline reconnaissance surveys for dragonflies were completed in conjunction with surveys for butterflies in 2008. In total, 637 sites were surveyed resulting in the detection of 18 species. These species are expected to be more abundant on the existing transmission line based on their known habitat preferences. No Red- or Blue-listed species were detected.
Vascular Plants
Rare plant surveys were completed in July and September 2008, in the Peace River Corridor and along the existing transmission line. Twenty-five transects were completed resulting in 3,751 observations of 588 vascular plant taxa. In total, 59 non-native taxa were detected.
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Twenty-eight Red- or Blue-listed taxa were detected and 14 additional potentially rare taxa (not currently listed and/or previously undescribed) were recorded. Over half of the total vascular plant taxa detected occur in both the Peace River Corridor and the Transmission Line.
Three years of surveys have resulted 466 sites being surveyed for rare plant taxa, resulting in the detection of 42 Red or Blue-listed taxa.
Bats
Mist-netting, acoustic sampling, radio telemetry and assessment of potential hibernacula were completed for bat species in the Peace River Corridor between July and October 2008. In 12 nights of netting, 69 bats of 6 species were captured. Acoustic sampling was completed at 93 sites and thirteen bats were radio-tagged and tracked to 24 roost structures. Hibernacula were assessed and two sites were monitored for 35 and 38 days, recording over 10,000 calls files.
In three years of study, 6 bat species have been confirmed present and reproducing in the Peace River Corridor. A capture rate of 0.24 bats/night was estimated over 3 years with 104 bats captured. The Blue-listed northern myotis accounted for approximately 6% of all captures. Bat activity was greatest in non-forested/riparian and moist forest habitats. One possible hibernaculum was located near Hudson’s Hope.
Waterfowl / Water-Associated Birds
Monthly aerial surveys, boat surveys and/or ground surveys were completed for waterfowl between May and October 2008, in the Peace River Corridor and along the existing transmission line. In total, 265 surveys were completed, documenting 57 species of waterfowl and water-associated birds. Seven Red- or Blue-listed species were detected, with most observations occurring during the spring or fall migration. The Upland Sandpiper is the only listed species known to breed in the area. Comparison between general habitat types in the Peace River Corridor indicated that species diversity was greatest in the main river corridor compared to river backchannels and wetlands. On the existing transmission line, lakes had higher species diversity compared to wetlands.
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In three years, 425 surveys have been completed along the Peace River and in wetlands and lakes in the Peace River Corridor and along the existing transmission line. In total, 61 species of waterfowl and water-associated birds have been detected of which 21 species were detected infrequently (1-3 detections in 1 or more years). Trends in species diversity and seasonal use indicate that the Peace River Corridor provides important stopover habitat for migrating waterfowl.
Ungulates
Winter track counts were completed in the vicinity of the potential Site C dam from January to March, 2009. Over 110 km were surveyed, resulting in the detection of 1816 deer tracks, 1038 moose tracks and 716 elk tracks. Results indicate that warm aspect slopes had the lowest average snow and the highest use by deer and elk compared to cool aspect slopes and flat areas. Flat areas had the highest use by moose.
An aerial block count survey was completed in February 2008. Thirty-two blocks in 4 strata were surveyed from Hudson’s Hope to the Alberta border resulting in an approximate population of 3032 deer, 665 moose and 1101 elk in the Peace River Corridor. Comparing these data with data from 1991 and 2006 surveys indicate that deer numbers have decreased since 1991, moose numbers have remained stable and elk numbers have increased between 1991 and 2009.
Rare Ecosystems
Five rare ecological communities are expected to occur in the Peace River Corridor. Analysis of the ecosystem map indicates that 93% of the habitat in the Peace River Corridor and 95% of the habitat along the transmission line was unlikely to contain a rare ecological community. Regional rarity was assessed by determining the proportion of each habitat type in the TEM mapped area. Over half of the ecosystems units occurred in less than 2% of the total mapped area and wetlands occur in the lowest proportion in the study areas.
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List of Acronyms (standard list for Project)
BC CDC – British Columbia Conservation Data Centre
BCR – Bird Conservation Region
BWBSmw1 – Peace moist, warm Boreal White and Black Spruce (subzone variant)
BCCF – BC Conservation Framework
COSEWIC – Committee on the Status of Endangered Wildlife in Canada
CWS – Canadian Wildlife Service
DPC – Peace Forest District
FSJ – Fort St. John
GIF- Ground Inspection Form
MOE – Ministry of Environment
MU(s) – Management Unit(s) (http://www.env.gov.bc.ca/fw/wildlife/hunting/regulations/)
NAD – North American Datum
PEL – Peace Lowlands (ecosection)
PRC – Peace River Corridor study area
PWWCP – Peace-Williston Wildlife Compensation Program
RIC – Resources Inventory Committee (now RISC)
RISC – Resources Inventory Standards Committee (formerly RIC)
SARA – Species at Risk Act
SCR – potential Site C reservoir
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TEM – Terrestrial Ecosystem Mapping
TL – Transmission Line study area
UTM – Universal Transverse Mercator
VEC – Valued Ecosystem Component
WHA – Wildlife Habitat Area
WHR – Wildlife Habitat Ratings
Glossary
Accreted terrain - A land mass that originated as an island arc or a microcontinent that was later added onto a continent
Anthropogenic – caused by activities of people
Blue List - species and subspecies of special concern (formerly vulnerable) in British Columbia
Bryophyte – non-vascular plant e.g. mosses and liverworts
Coniferous – needle-leaved trees (e.g. white spruce)
Deciduous – broad-leaved trees (e.g. aspen, balsam poplar)
Diurnal – active during the day (opposite of nocturnal)
Emergent vegetation – plants such as rushes, sedges and cattails that grow in water
Herptiles – reptiles and amphibians.
Incidental – refers to observations of a species made outside of formal surveys targeting that species
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Indigenous species – species native to BC that have not been introduced from other areas of the world
Mesic – having a well-balanced or moderate moisture supply, well-drained but usually moist throughout the growing season.
Non-vascular plants – includes mosses and liverworts
Passerine – songbird (thrushes, warblers, vireos, flycatchers, swallows, sparrows, blackbirds, crows, jays, nuthatches, wrens, finches, chickadees, tanagers, orioles, grosbeaks, waxwings, starlings, catbirds, creepers, pipits, weavers, shrike, kinglet and larks).
Protected Area – federal and provincial parks, and ecological reserves
Raptor – bird of prey.
Red List – includes taxa considered to have- or are candidates for- official Extirpated, Endangered or Threatened Status in BC
Seral – describes an intermediate stage found in ecological succession. In the Peace River Valley, it often indicates a deciduous-dominated forest.
Structural stage – numerical scale used in Terrestrial Ecosystem Mapping describing forest structure and how it changes with age. Structural stages include 1 (non-vegetated/sparse), 2 (herb), 3 (shrub), 4 (pole-sapling), 5 (young forest), 6 (mature forest) and 7 (old forest).
Subnivean – under the snow
Taxa - Plural of ‘taxon’
Taxon – refers to either a species or subspecies unit
Taxonomy – the system of classification and naming of organisms
Transect – a linear sampling unit
Ungulate – hoofed animal of the deer family (deer, moose, elk and sheep)
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Vagrant – species found outside of its normal range
Vascular Plants – includes ferns, trees, and flowering plants
Voucher – refers to a collected specimen of an organism that is difficult to identify to species in the field and must be confirmed through laboratory review. Especially relevant for plant species that may be previously undescribed.
Yellow List – includes taxa of wildlife and plants that are not considered to be at risk in BC.
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TABLE OF CONTENTS 1.0 INTRODUCTION...... 1
1.1 PROJECT DESCRIPTION AND DESIGN ...... 2
1.2 REPORT INTRODUCTION ...... 3
1.2.1 Permits ...... 3
1.2.2 Assumptions...... 3
1.2.3 VEC Selection and Methods ...... 4
1.3 STUDY AREA ...... 6
1.3.1 Study Area Description...... 11
1.3.2 Mapping...... 12
2.0 SPECIES GROUP SUMMARIES...... 14
2.1 RAPTORS / HERONS ...... 14
2.1.1 Introduction...... 14
2.1.2 Background ...... 15
2.1.3 Methods...... 18
2.1.4 Results...... 19
2.1.5 Summary ...... 25
2.2 AMPHIBIANS ...... 26
2.2.1 Introduction...... 26
2.2.2 Background ...... 26
2.2.3 Methods...... 28
2.2.4 Results...... 32
2.2.5 Summary ...... 45
2.3 OWLS ...... 45
2.3.1 Introduction...... 45
2.3.2 Background ...... 47
2.3.3 Methods...... 49
2.3.4 Results...... 52
2.3.5 Summary ...... 62
2.4 SONGBIRDS ...... 62
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2.4.1 Introduction...... 63
2.4.2 Background ...... 63
2.4.3 Methods...... 70
2.4.4 Results...... 73
2.4.5 Summary ...... 92
2.5 BUTTERFLIES ...... 92
2.5.1 Introduction...... 93
2.5.2 Background ...... 94
2.5.3 Methods...... 98
2.5.4 Results...... 100
2.5.5 Summary ...... 109
2.6 DRAGONFLIES ...... 109
2.6.1 Introduction...... 110
2.6.2 Background ...... 110
2.6.3 Methods...... 111
2.6.4 Results...... 112
2.6.5 Summary ...... 115
2.7 RARE VASCULAR PLANTS ...... 115
2.7.1 Introduction...... 116
2.7.2 Background ...... 116
2.7.3 Methods...... 116
2.7.4 Results...... 118
2.7.5 Summary ...... 130
2.8 BATS ...... 130
2.8.1 Introduction...... 131
2.8.2 Background ...... 133
2.8.3 Methods...... 139
2.8.4 Results...... 149
2.8.5 Summary ...... 181
2.9 WATERFOWL / W ATER -ASSOCIATED BIRDS ...... 182 July 2009 -xi-
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2.9.1 Introduction...... 183
2.9.2 Background ...... 183
2.9.3 Methods...... 187
2.9.4 Results...... 189
2.9.5 Summary ...... 198
2.10 UNGULATES ...... 199
2.10.1 Introduction...... 199
2.10.2 Background ...... 199
2.10.3 Methods...... 204
2.10.4 Results...... 207
2.10.5 Summary ...... 219
2.11 RARE ECOSYSTEMS ...... 220
2.11.1 Introduction...... 220
2.11.2 Background ...... 221
2.11.3 Methods...... 223
2.11.4 Results...... 224
2.11.5 Summary ...... 229
3.0 CONCLUSION ...... 229 4.0 REFERENCES...... 230 5.0 PERSONAL COMMUNICATIONS...... 252 6.0 APPENDICES ...... 253
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LIST OF TABLES
Table 2.1.1a. Diurnal raptor species known to occur in the study area...... 15 Table 2.1.4.2a. Bald Eagle nests observed in the Peace River Corridor in 2005, 2006 and 2008, including incidentals...... 24 Table 2.1.4.2b. Diurnal raptor species detections during surveys in 2005, 2006 and 2008, including incidentals...... 25 Table 2.2.1a. Amphibian species known to occur in the study area...... 26 Table 2.2.4.1a. Summary of auditory frog survey effort in the Peace River Corridor in 2008...... 37 Table 2.2.4.1b. Summary of auditory frog survey effort along the Transmission Line in 2008...... 38 Table 2.2.4.1c. Number of each amphibian species detected during auditory surveys in 2008...... 38 Table 2.2.4.1d. Summary of amphibian road survey effort in 2008...... 39 Table 2.2.4.1e. Number of amphibian species detected during road surveys in 2008..... 40 Table 2.2.4.1f. Number of amphibians detected incidentally during surveys in 2008. .... 40 Table 2.2.4.2a. Total pond-breeding amphibian survey effort completed 2005, 2006 and 2008...... 41 Table 2.2.4.2b. Total auditory amphibian survey effort completed in 2006 and 2008...... 41 Table 2.2.4.2c. Number of habitat types at which amphibian species were detected during surveys completed in 2006 and 2008...... 42 Table 2.2.4.2d. Survey sites where egg masses were observed during pond-breeding amphibian surveys completed in 2006 and 2008...... 43 Table 2.2.4.2e. Survey sites where tadpoles were observed during pond-breeding amphibian surveys completed in 2006 and 2008...... 44 Table 2.3.1a. Owl species known to occur in the study area...... 46 Table 2.3.4.1a. Summary of owl surveys effort completed in 2008...... 55 Table 2.3.4.1b. Number of owls detections recorded during call-playback surveys completed in 2008...... 55 Table 2.3.4.1c. Incidental observations of owl species recorded during surveys in 2008...... 57
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Table 2.3.4.2a. Total owl survey effort for each target species, completed in 2005, 2006 and 2008...... 58 Table 2.3.4.2b. Number of owl detections recorded during surveys in 2005, 2006 and 2008, including incidentals...... 59 Table 2.3.4.2c. Summary of data from owl surveys in 2006 and 2008 used to determine territories for each species...... 59 Table 2.4.1a. Red- or Blue-listed passerines known to occur in the study area...... 63 Table 2.4.4.1a. Summary of breeding bird survey effort in the PRC study area in 2008. 77 Table 2.4.4.1b. Summary of breeding bird survey effort in the TL study area in 2008..... 78 Table 2.4.4.1c. Number of Red- or Blue-listed songbirds detections during point count surveys completed in the PRC study area in 2008...... 79 Table 2.4.4.1d. Number of Red- or Blue-listed songbird detections during point count surveys completed in the TL study area in 2008...... 80 Table 2.4.4.1e. Percentage of point count stations visited in 2008 at which Red- or Blue- listed species were detected (does not include incidental detections). . 80 Table 2.4.4.1f. Summary of wetland surveys for Yellow Rail and American Bittern completed in the TL study area in 2008...... 81 Table 2.4.4.2a. Total breeding bird survey effort completed in 2005, 2006 and 2008. .... 82 Table 2.4.4.2b. Number of Red- or Blue-listed songbird detections in each TEM habitat unit surveyed in 2006 and 2008...... 86 Table 2.4.4.2c. Bird diversity values for each study area...... 91 Table 2.4.4.2d. Number of songbird point count survey stations in each TEM habitat type surveyed in 2006 and 2008...... 91 Table 2.5.1a. Rare butterflies potentially present in the Peace River study area...... 93 Table 2.5.4.1a. Number of TEM polygons surveyed in each study area in 2008...... 101 Table 2.5.4.1b. Number of butterfly survey sample stations completed in 2008...... 104 Table 2.5.4.1c. Red- or Blue-listed butterfly taxa detected during surveys in 2008...... 105 Table 2.5.4.2a. Summary of butterfly survey effort in each study area in 2005, 2006 and 2008...... 106 Table 2.5.4.2b. Summary of the reported occurrence of Red- or Blue-listed butterflies in the Peace River Study Area in 2005, 2006 and 2008...... 106
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Table 2.5.4.2c. Number of Red- or Blue-listed butterfly taxa detected in TEM polygons sampled in 2006 and 2008...... 108 Table 2.5.4.2d. Presence of rare butterfly taxa by TEM habitat units during surveys completed in 2006 and 2008...... 108 Table 2.6.1a. Blue-listed damselflies and dragonflies potentially present in the study area...... 110 Table 2.6.4a. Dragonfly and damselfly species captured during surveys completed in 2008...... 115 Table 2.7.4.1a. Summary of rare plant transects completed and the number of taxa detected in 2008...... 122 Table 2.7.4.1b. Number of rare plant populations recorded during rare plant surveys in 2008...... 123 Table 2.7.4.1c. Previously undescribed vascular plants located in the study area in 2008...... 124 Table 2.7.4.1d. Vascular plants located in the study area in 2008 that appear to be locally rare but are not listed provincially (includes species previously undescribed)...... 125 Table 2.7.4.1e. Summary of habitat types and rare species detections...... 127 Table 2.7.4.2a. Summary of rare plant surveys completed in 2005, 2006 and 2008..... 128 Table 2.7.4.2b. Rare vascular plant taxa detected in 2005, 2006 and 2008...... 129 Table 2.8.1a. Bat species potentially present in the study area...... 131 Table 2.8.3.3a. Habitat groupings for analysis of relative activity of bats in the Peace River Valley...... 145 Table 2.8.4.1a. Summary of sampling effort and capture rates for each sampling site in the Peace River Corridor in July 2008...... 153 Table 2.8.4.1b. Bat species captured in mist-nets along the Peace River Corridor in 2008...... 154 Table 2.8.4.1c. Number of Anabat call sequences analyzed and number of sites sampled for activity of hoary bats in 2008...... 155 Table 2.8.4.1d. Species, gender, reproductive condition, duration of tracking, and minimum number of roosts used by 13 bats radio-tagged in the Peace River Corridor in 2008...... 155
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Table 2.8.4.1e. Detector site labels, dates that detectors were deployed, and numbers of files generated by remote Anabat detectors, at 2 potential hibernacula in 2008...... 157 Table 2.8.4.2a. Summary of bat species captured during four survey periods in 2005, 2006, and 2008...... 158 Table 2.8.4.2b. Capture location and date, suspected species, age, gender, and measurements of long-eared bats captured from 2005-2008...... 160 Table 2.9.4.2c. Earliest and latest calendar dates for captures of pregnant, lactating, and post-lactating female bats, by species, in 2005, 2006, and 2008...... 161 Table 2.8.4.2d. The number of sites successfully sampled for two hours post-sunset, within each of the grouped habitat types...... 163 Table 2.8.4.2e. The number of bats in each species/reproductive group used for analysis, the number of roost sites identified and the maximum commuting distance for each group...... 169 Table 2.8.4.2f. Quantitative characteristics of live (appearance class < 3) and dead trees (appearance class >= 3) used as roosts by bats...... 173 Table 2.9.4.1a. Numbers of waterfowl surveys completed in each stratum in 2008...... 192 Table 2.9.4.1b. Numbers of Red or Blue-listed waterfowl and water-associated bird species detected in 2008 (including incidentals)...... 193 Table 2.9.4.2a. Summary of waterfowl surveys completed in 2005, 2006 and 2008..... 196 Table 2.9.4.2b. Number of waterfowl surveys completed in 2005, 2006 and 2008...... 197 Table 2.9.4.2c. Numbers of Red- or Blue-listed species observed in the PRC study area in 2005, 2006 and 2008...... 197 Table 2.10.4.1a. Survey effort and snow conditions during the winter track counts in 2008...... 213 Table 2.10.4.1b. Pooled results (tracks/day/50 m±std dev) of winter track counts completed in 2008...... 214 Table 2.10.4.2a. Numbers of ungulates counted in each stratum and number of blocks surveyed during the three aerial censuses (1991, 2006, and 2009). .. 216 Table 2.10.4.2b. Ungulate population estimates (± 90%) for the Peace River study area for 1991, 2006 and 2009...... 217
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Table 2.11.1a. Red- or Blue-listed ecological communities potentially occurring in the BWBSmw1 (BC CDC 2009)...... 221 Table 2.11.3a. Ranking assigned to site series and structural stage combinations in the TEM map area...... 224 Table 2.11.4.1a. Summary of area (ha) and percentage area in each study area of rare ecological community probabilities...... 225 Table 2.11.4.3a. Summary of percent occurrence of forested units occurring in the TEM map area...... 228 Table 2.11.4.3b. Summary of percent occurrence of stand types occurring in the VRI data of the area...... 229
LIST OF FIGURES
Figure 2.4.4.2a. Bird species accumulation curve for all point counts conducted in the Peace River Corridor...... 83 Figure 2.4.4.2b. Bird species accumulation curve for point counts conducted in the potential Site C reservoir...... 84 Figure 2.4.4.2c. Bird species accumulation curve for point counts conducted along the transmission line...... 85 Figure 2.4.4.2d. Black-throated Green Warbler detections in the PRC (2006, 2008) in relation to map unit (Appendix 3a)...... 87 Figure 2.4.4.2e. Black-throated Green Warbler detections in the PRC (2006, 2008) in relation to structural stage (Appendix 3b)...... 88 Figure 2.4.4.2f. Canada Warbler detections in the PRC (2006, 2008) in relation to map unit (Appendix 3a)...... 89 Figure 2.4.4.2g. Canada Warbler detections in the PRC (2006, 2008) in relation to structural stage (Appendix 3b)...... 90 Figure 2.8.4.2a. Numbers of adult and juvenile bats captured, by species, in 34 nights of netting completed in 2005, 2006 and 2008...... 158 Figure 2.8.4.2b. Numbers of female and male bats captured, by species, in 34 nights of netting completed in 2005, 2006 and 2008...... 159
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Figure 2.8.4.2c. Bat activity recorded over 5 minute intervals between 22:00 and 2:30, within 9 forested and 4 riparian sites sampled on July 15-17, 2008.... 162 Figure 2.8.4.2d. Average number of bat calls recorded in 2 hours of sampling, at 9 grouped habitat types, for a) Myotis bats and b) big bats...... 164 Figure 2.8.4.2e. The number of calls recorded in 2 hours from a) Myotis and b) big bats in forested and non-forested/riparian habitats...... 165 Figure 2.8.4.2f. Activity of a) Myotis and b) big bats at forested sites of varying moisture regime...... 166 Figure 2.8.4.2g. Activity of a) Myotis and b) big bats at moist forested sites that were dominated by coniferous trees or deciduous trees...... 167 Figure 2.8.4.2h. The average number of bat calls per grouped habitat type, in 2 hours of sampling, for habitat types sampled in both session 1 (late July) and 2 (late August) in 2008...... 168 Figure 2.8.4.2i. Number and type of roost structure used by 12 reproductive female bats (34 roosts) and 6 non-reproductive bats (13 roosts) radio-tracked in the Peace River Corridor in 2006 and 2008...... 170 Figure 2.8.4.2j. Type of structures used as roosts by different species of reproductive female bats...... 171 Figure 2.8.4.2k. Type of structures used as roosts by different species of non-reproductive female and male bats...... 172 Figure 2.8.4.2l. Appearance classes of 36 trees used as roosts by 17 bats radio-tracked during 2006 and 2008. Classes are from DEIF...... 173 Figure 2.8.4.2m. TEM habitat units used for roosting by 12 reproductive female bats (34 roosts) and 6 non-reproductive bats (13 roosts)...... 175 Figure 2.8.4.2n. Mapped TEM units used for roosting by different species of reproductive female bats...... 176 Figure 2.8.4.2o. TEM habitat units used for roosting by different species of non- reproductive female and male bats...... 177 Figure 2.8.4.2p. Total number of call files recoded per night at two potential hibernacula (sites B-121 and B-122) (top) and nightly temperature at sunset in Fort St. John (bottom)...... 179 Figure 2.8.4.2q. Timing of bat activity on August 31, 2008 at site B-122...... 180
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Figure 2.9.4.1a. Number of species detected each month in the River, Backchannel and Wetland strata in the PRC...... 194 Figure 2.9.4.1b. Number of species detected each month in the Wetland and Lake strata in the TL...... 195 Figure 2.9.4.2a. Summary of the number of waterfowl and water-associated bird species observed in the Peace River Corridor during surveys completed in 2005, 2006 and 2008...... 198 Figure 2.10.4.1a. Relative occurrence of ungulate tracks by 5 cm snow depth intervals.. 215 Figure 2.10.4.2a. Deer Winter Severity Index using data from the Fort St John airport for the previous 30 years...... 219
LIST OF MAPS
Map 1.3a. The study area...... 8 Map 1.3b. The study area...... 9 Map 1.3c. Biophysical mapping...... 10 Map 2.1.4a. Raptor nests...... 21 Map 2.1.4b. Raptor nests...... 22 Map 2.2.4a. Amphibian surveys...... 34 Map 2.2.4b. Amphibian surveys...... 35 Map 2.2.4c. Amphibian road surveys...... 36 Map 2.3.4a. Owl call-playback surveys...... 53 Map 2.3.4b. Owl call-playback surveys...... 54 Map 2.4.4a. Songbird survey locations...... 75 Map 2.4.4b. Songbird survey locations...... 76 Map 2.5.4a. Butterfly survey locations...... 102 Map 2.5.4b. Butterfly survey locations...... 103 Map 2.6.4a. Dragonfly survey locations...... 113 Map 2.6.4b. Dragonfly survey locations...... 114 Map 2.7.4a. Rare plant survey locations...... 120 Map 2.7.4b. Rare plant survey locations...... 121 Map 2.8.4a. Bat survey locations...... 150
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Map 2.8.4b. Bat survey locations...... 151 Map 2.9.4a. Waterfowl survey locations...... 190 Map 2.9.4b. Waterfowl survey locations...... 191 Map 2.10.4a. Ungulate Winter Range areas...... 208 Map 2.10.4b. Ungulate Winter Range areas...... 209 Map 2.10.4c. Ungulate transect locations...... 210 Map 2.10.4d. Ungulate aerial census block areas...... 211 Map 2.10.4e. Ungulate aerial census block areas...... 212 Map 2.11.4a. Areas potentially supporting rare ecosystems...... 226 Map 2.11.4b. Areas potentially supporting rare ecosystems...... 227
LIST OF APPENDICES
Appendix 1. Summary of proposal for 2008 wildlife and plant surveys in the Peace River area...... 254 Appendix 2. Potential VEC list for terrestrial wildlife in the Peace River Valley...... 255 Appendix 3a. TEM map legend for the Peace River Corridor and the Transmission Line (Keystone Wildlife Research Ltd. 2008a)...... 257 Appendix 3b. Structural stage definitions (RIC 1998a)...... 258 Appendix 4a. Summary of pond-breeding amphibian survey effort in the Peace River Corridor in 2008...... 259 Appendix 4b. Summary of pond-breeding amphibian survey effort on the Transmission Line in 2008...... 259 Appendix 4c. Amphibian species detected during wetland surveys in the Peace River Corridor in 2008...... 261 Appendix 4d. Amphibian species detected during wetland surveys in the Transmission Line study area in 2008...... 261 Appendix 5a. Owl survey transects completed in 2008...... 263 Appendix 5b. Results of owl surveys completed in the PRC in 2008...... 264 Appendix 5c. Results of owl surveys completed in the TL in 2008...... 265 Appendix 6a. Detailed summary of breeding bird survey effort in the Peace River Corridor in 2008...... 266 July 2009 -xx-
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Appendix 6b. Detailed summary of breeding bird survey effort for the Transmission Line in 2008...... 267 Appendix 6c. Passerine and upland game bird species detected during 2005, 2006 and 2008 wildlife surveys...... 268 Appendix 7. Butterfly taxa detected during butterfly surveys in 2005, 2006 and 2008...... 272 Appendix 8a. Rare vascular plant taxa potentially present in the study area...... 275 Appendix 8b. Complete list of vascular plant species detected during rare plant surveys in 2008...... 279 Appendix 8c. Descriptions of rare plant taxa located in the study area in 2008...... 303 Appendix 9a. Bat capture sampling effort...... 342 Appendix 9b. Bat acoustic sampling...... 343 Appendix 9c. Radio-telemetry...... 345 Appendix 10a. Number of waterfowl surveys completed in the Peace River Corridor study area in 2008...... 347 Appendix 10b. Number of waterfowl surveys completed in the transmission line study area in 2008...... 348 Appendix 10c. Number of waterfowl and water-associated birds detected during waterfowl surveys in 2008, in the PRC and TL study areas...... 349 Appendix 10d. Number of waterfowl and water-associated bird species detected incidentally during surveys in 2008...... 351 Appendix 10e. Number of waterfowl and water-associated birds observed in each stratum in 2008, in the PRC study area...... 352 Appendix 10f. Number of waterfowl and water-associated birds observed by stratum in 2008, in the TL study area...... 353 Appendix 10g. Summary of waterfowl and water-associated species occurrence in the Peace River Corridor during surveys completed in 2005, 2006 and 2008*...... 354 Appendix 11. Ungulate block counts from the three aerial censuses (1991, 2006, 2009)...... 356 Appendix 12. Summary of percent occurrence of TEM habitat units (Appendix 3a) and structural stage (Appendix 3b) in the TEM mapped area...... 358
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1.0 INTRODUCTION
The BC Energy Plan called for BC Hydro and the provincial government to "enter into initial discussions with First Nations, the Province of Alberta and communities to discuss Site C to ensure that communications regarding the potential project and the processes being followed are well known." No decision has been made to build Site C, but large projects like Site C have a long lead time, and require early evaluation and study. To preserve Site C as an option for the future, significant work needs to take place now to understand the project's impacts and benefits from a technical, financial and environmental perspective. For that reason, there are a number of studies and comprehensive consultation planned to update the project.
BC Hydro is taking a Stage-by-Stage approach to the evaluation of Site C as a potential resource option for meeting B.C.'s future electricity needs. At the end of each Stage of review, BC Hydro will make a recommendation to government for a decision on whether to proceed to the next Stage of project planning and development. BC Hydro is currently in Stage 2, Project Definition and Consultation.
The Stage 1 review of the Site C project was completed in December 2007. That review was mainly a compilation of existing knowledge from previous studies of the Site C project. Potential valued ecosystem components (VECs) that were known to be present in the project area and that could be affected by the project were identified. The information available for each potential VEC was assessed to determine if the information was adequate to be used in a formal environmental assessment process (BCEA, CEA). Based on the project analysis in Stage 1, it was determined that Site C should be preserved as an option to meet B.C.’s growing electricity gap and that the project should be taken into the Stage 2 evaluation, which is consultation and project definition.
Stage 2 involves public consultation and extensive engineering, environmental and technical work to further define the project, to update decades-old studies, and to conduct new studies and technical work. Stage 2 work focused on filling information gaps and consulting with stakeholders to ensure that all issues of concern had been identified and that sufficient data was available to support a potential future comprehensive environmental assessment should the project advance to Stage 3 (Appendix 1). Wildlife and plant taxa at risk and regionally
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This report provides a record of the Stage 2 surveys and data compilations that have been completed. The potential VECs are classified into taxonomic groups that each include multiple species of concern. The taxonomic groups include raptors/herons, amphibians, owls, songbirds, butterflies, dragonflies, rare vascular plants, bats, waterfowl/shorebirds, ungulates and rare ecosystems. As the federal and provincial lists of species at risk are dynamic in nature, the VEC list will require revision should the project proceed to Stage 3. This report summarizes the current wildlife baseline data, which is comprised of data collected in 2005, 2006 and 2008/09.
1.1 PROJECT DESCRIPTION AND DESIGN
Site C is one of several options being considered to help meet B.C.'s future electricity needs. The potential Site C dam would be located about seven kilometres southwest of Fort St. John on the Peace River, downstream of the confluence of the Moberly River and the Peace River. It would provide about 900 megawatts of capacity, and produce approximately 4,600 gigawatt hours of electricity each year—enough to power about 460,000 homes. The reservoir would be 83 kilometres long, on average two to three times the width of the current river, and would flood approximately 5,340 hectares.
As the third dam and generating station on the Peace River, Site C would gain significant efficiencies by taking advantage of water already stored in the Williston Reservoir and used to generate electricity upstream at the existing W.A.C. Bennett and Peace Canyon dams. In fact, it would produce about 30% of the electricity at the W.A.C. Bennett Dam, with 5% of the reservoir area.
As currently designed, the earthfill Site C dam would be 1,100 metres long, with 300 metres of concrete structures located on the right bank for the spillway and power intakes. If built, Site C would be a mid-size facility with a significant upfront capital cost, a long operating life and low operating costs.
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1.2 REPORT INTRODUCTION
The 2008 field program was designed to update existing information and conduct new studies on wildlife and plant resources. Taxa identified in the scope of study that required surveys include butterflies, passerines (especially warblers), raptors/herons (nest sites), waterfowl, herptiles, plants, owls, ungulates, fisher and bats. Assessment of some species requires specialist knowledge, and all require that survey sites be located appropriately.
The methodology included a map-based evaluation of wildlife habitat suitability for focal species, field review and confirmation of habitat suitability, and targeted wildlife surveys for particular species/species groups. The focus of the surveys was on critical habitats, as identified in the draft habitat suitability models (Keystone Wildlife Research Ltd. 2008b), for rare or endangered species. Information was collected in a form that will allow a future quantitative analysis of the potential effects of the Site C project in the Peace River area, should the project proceed to Stage 3.
The objectives of the 2008/2009 field program were to:
• Determine the presence, and relative abundance where possible, of target taxa within the study area;
• Develop habitat suitability ratings for previously unidentified target taxa (species that have recently been re-classified as at risk by the CDC or COSEWIC) and confirm their reliability through habitat assessment and wildlife inventory surveys;
• Determine the presence of rare plants and rare plant communities within the study area.
1.2.1 Permits
Bat capture was conducted under wildlife permit FJ08-44000 (live trap and radio tagging). Baiting of fisher hair-snagging stations with road-killed ungulates was carried out under permit FJ08-48888 (possess and dispose of dead wildlife).
1.2.2 Assumptions
Fieldwork was completed according to the following assumptions:
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Terrestrial Ecosystem Mapping (TEM) is an accurate representation of the study area;
Habitat mapping based on the TEM will provide sufficient data to analyze and quantify the potential impacts of the Site C project for VECS should the project proceed to Stage 3;
Access to private properties, First Nation lands, and shared roads will be permitted during the appropriate times of the year to complete species-specific surveys.
1.2.3 VEC Selection and Methods
Species/ecosystems at risk in BC are placed on provincial lists according to their degree of endangerment. The Red List includes “ecological communities, and indigenous species and subspecies that are extirpated, endangered or threatened in British Columbia”. The Blue List includes “ecological communities, and indigenous species and subspecies of special concern (formerly vulnerable) in British Columbia” (BC CDC 2007). Taxa that are not considered at risk are placed on the Yellow List. Red-listed species and sub-species have or are candidates for official Extirpated, Endangered or Threatened Status in BC. Not all Red-listed taxa will necessarily become formally designated. Placing taxa on these lists flags them as being at risk and requiring investigation (BC CDC 2007). Taxa may be transferred from one list to another list because of an actual change in their ecological circumstance (change in risk), or because new data is available on their range, taxonomy, population trend or numbers to justify a change in status. The latter situation is especially relevant for taxa that have been little surveyed (e.g. invertebrates) and for which even basic life history information may be sparse or lacking.
The Committee on the Status of Endangered Wildlife in Canada (COSEWIC) is an independent advisory organization that evaluates the situation of species in Canada and grants them status as endangered, threatened, of special concern or not at risk. The committee is composed of private and government agency (provincial, territorial and federal) scientists, as well as conservation representatives. While the status granted by COSEWIC has no legal authority, the Canadian government considers these evaluations when adding species to the List of Wildlife Species at Risk.
Federally listed species are included on Schedules 1, 2 or 3 of the Species at Risk Act (SARA). Taxa designated as ‘at risk’ in Canada are placed on Schedule 1. Taxa that were designated as
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'at risk' by COSEWIC (the Committee on the Status of Endangered Wildlife in Canada) before SARA was proclaimed in June 2003, must be reassessed according to the new criteria of the Act before they can be listed on Schedule 1. Those taxa are included on Schedules 2 and 3, and are not yet officially protected under SARA.
A draft list of potential Valued Ecosystem Components (VECs) was produced for the potential Site C project in 2005 (Keystone Wildlife Research Ltd. 2005). Potential wildlife and plant VECs were selected based on a number of criteria, including:
• Provincial and federal status as species at risk;
• Known presence (especially as breeders) within the study area;
• Perceived vulnerability to potential effects of the Project;
• Lack of data (knowledge gaps) regarding species presence and distribution within the study area;
• Economic importance.
The potential VEC list will be refined if the project proceeds to Stage 3.
Although landbird conservation planning is not yet fully implemented in Bird Conservation Region 6 (Boreal Taiga Plains), the Canadian Wildlife Service (CWS) has identified a draft list of priority bird species for conservation planning in three conservation regions (Schonewille et al. 2007). That report contains vetted lists of priority species, priority populations, population objectives, and priority habitat for species within the Prairie and Northern Region of Canada. The Peace River Valley occurs within Conservation Region 6. ‘High’ priority species are those for which there is either continental or regional concern and immediate action is recommended. ‘Medium’ priority species are defined based on a combination of the species’ status and the proportion of the species’ breeding distribution included within the region under consideration. Species that are particularly abundant within the region but may require monitoring to fill data gaps are assigned ‘stewardship’ priority. The CWS conservation priority ranking listed for Bird Conservation Region (BCR) 6 has been included in species tables within this document, where applicable.
The province of BC released its Conservation Framework (BCCF) in July 2008, which was established to contribute to global efforts for species and ecosystem conservation, to prevent
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1.3 STUDY AREA
The two main components of the potential Site C project include the reservoir area and the related transmission line. Two main study areas were defined based on these project components: the Peace River Corridor and the Transmission Line.
The Peace River Corridor (PRC) study area includes a 150 km long section of the Peace River from the Peace Canyon Dam downstream to the Alberta border (Maps 1.3a and 1.3b). Geographically, the core river corridor refers to the entire river valley (62,000 ha), including the floodplain and the ascending valley slopes extending approximately 2 km on either side of the Peace River, creating a 4 km wide corridor. The study area was expanded past the 4 km wide corridor at Cache Creek, Moberly River and Halfway River, to include the potential Site C reservoir (SCR), which extends into those drainages. The study area also includes areas downstream of the potential Site C dam in order to determine the distribution of species at a broader scale in the Peace River Valley and to identify any species unique to the potential reservoir area.
The potential Site C reservoir (SCR) would inundate habitat between the Moberly River and Hudson's Hope (~5340 ha flooded land). This area is included within the PRC study area. Where appropriate, survey results have been reported within the potential Site C reservoir.
The related transmission line (TL) study area extends from the potential Site C dam site to the Peace Canyon Dam switchyard adjacent to the existing transmission line on the south side of the river. It includes a 500 m buffer on either side of the existing transmission line centreline (Map 1.3a).
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An expanded study area was established based on the extent of existing 1:50,000 biophysical mapping for the area (Lea and Lacelle 1989 and Thompson et al. 1980). That study area is bounded by seven adjacent 1:50,000 NTS map sheets (518,000 ha, 094A/01-07) (Map 1.3c). The map units in the biophysical mapping have been correlated with the TEM habitat units and can be used to identify suitable habitat for target species outside of the PRC and TL study areas. This mapping is over 20 years old and updates are required to ensure that the map units and age classification reflect present-day conditions. Updates can be completed using existing provincial VRI mapping and GIS software.
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Map 1.3a. The study area.
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Map 1.3b. The study area.
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Map 1.3c. Biophysical mapping.
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1.3.1 Study Area Description
The study area is within the Peace Forest District in the Northern Interior Forest Region and within Management Units (MUs) 7-31, 7-32, 7-33, 7-34 and 7-35, and includes portions of 25 1:20,000 mapsheets.
Both study areas fall within the Peace River Basin ecoregion. The Peace River Basin is a wide plain that lies between rolling uplands to the north and south, and is dissected by the Peace River and its tributaries (Demarchi 1996). The study area lies within the Peace Lowlands (PEL) ecosection. The Peace Lowlands Ecosection is a blocky mountain area on the east side of the Rocky Mountains, with strong rainshadows (Demarchi 1996).
The Peace River lowland, along with the main ranges of the Rocky Mountains and the rest of northeast British Columbia occupies the ancestral North American landmass, while the remainder of the province was formed of accreted terrains that docked onto North America from the Pacific Ocean (Cannings and Cannings 1999). The bedrock types throughout the project area are shale and sandstone (Valentine et al. 1978), which are generally high in pH, and rich in macronutrients important to lichens and plants. The area was covered in a glacial lake toward the end of the last glacial maximum (Cannings and Cannings 1999). Some higher elevation areas around the Peace Lowland may have experienced neither flooding nor permanent ice cover during the last ice age, and so have had an opportunity for some cold-grassland or peat land vegetation continuity from before the last ice age to the present. The contemporary landscape of the Peace Lowland is of plains dissected by deeply cut drainages, sloping away gradually to the east and north.
The climate is moderate and continental, with moderately warm summers and relatively cold winters (Farstad et al. 1965). The climate of the Peace River Lowland is of a continental type, as there is a wide temperature spread between summer and winter, and peak precipitation occurs in summer. The winter is relatively dry with less precipitation, low humidity, and drying winds. Dominant vegetation of the Peace Lowland is largely that of boreal forest. A single biogeoclimatic subzone variant is present in the study area, the Boreal White and Black Spruce moist, warm Peace variant (BWBSmw1). The BWBSmw1 variant covers the rolling plains that extend from near where the Rocky Mountains cross the Alberta border, north to near the Beatton River (Delong 1990). Elevations within the variant range from 750 to 1050 m.
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Trembling aspen ( Populus tremuloides ) is the dominant tree cover in most of the variant due to past history of frequent fires and other anthropogenic disturbance. Balsam poplar ( Populus balsamifera ) occurs on wetter depressional sites. White spruce ( Picea glauca ) is present on moist to wetter sites where there has been limited fire history. Lodgepole pine ( Pinus contorta ) occurs as a seral species on drier and poorer sites. Black spruce ( Picea mariana ) forests, often with a minor component of tamarack ( Larix laricina ), are present on organic soils in muskeg forest. Less widespread upland vegetation types include grassland and mixed grassland-shrub thicket-aspen forest mosaics. Much of the original lowland habitat along the river has been converted to agricultural crops (Delong 1990).
1.3.2 Mapping
Terrestrial Ecosystem Mapping (TEM) is a method of mapping that uses both terrain and vegetation characteristics to classify a landscape into map polygons. TEM is a provincial standard method of mapping terrestrial ecosystems. It has two components, bioterrain and ecosystems. Bioterrain characteristics include surficial materials, terrain expression (e.g. gullying) and drainage. Ecosystems are defined as sites with distinct vegetation communities and physical characteristics such as slope, aspect and moisture. TEM mapping can be used to provide quantitative information about the physical and vegetation characteristics for any area of interest, and to assess the potential impacts of various land management scenarios.
TEM at 1:20,000 scale was completed in 2007 for the core study area (Keystone Wildlife Research Ltd. 2008a) following methodology described in Terrain Classification System for British Columbia (Howes and Kenk 1997), Guidelines and Standards for Terrain Mapping in British Columbia (RIC 1996) and Standard for Terrestrial Ecosystem Mapping in British Columbia (RIC 1998a). Aerial photographs were viewed in stereo by a qualified bioterrain mapper, who added polygons corresponding to bioterrain characteristics. The photos were then viewed by qualified ecosystem mappers, who subdivided the bioterrain polygons according to the characteristics of the ecosystems within them. The ecosystems were mapped according to the descriptions provided in the regional field guide for the BWBSmw1 (Delong 1990), the draft seral guide (BC MoF 2002) and the current list of provincial mapcodes (RIC 2003). Ecosystem units are labelled with a site series and a structural stage that corresponds to the TEM map unit (Appendix 3a, 3b).
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The polygons on the aerial photographs were transferred to digital format and each polygon was numbered and matched with its corresponding bioterrain and ecosystem classification to produce a draft map. The draft map was field-truthed in 2006 and 2007. Field crews assessed ecosystem and bioterrain characteristics at plots throughout the Peace River Corridor and Transmission Line study areas. The data from the field-truthing were used to revise the map where required, and a final map was then produced.
Much of the surrounding regional study area had been mapped at 1:50,000 scale in the 1980’s using a system called biophysical mapping (Lea and Lacelle 1989; Thompson et al. 1980). The linework for those mapping projects was digitised and the older map units were reclassified into the map units used in the TEM, to produce an expanded map coverage of the regional study area.
Wildlife habitat suitability mapping is a provincial standard method of habitat assessment that can be used to prepare spatial summaries of habitat quality and quantity for wildlife species (RIC 1999a). Draft wildlife habitat ratings (WHR) were completed for selected VECs (Valued Ecosystem Components), using the methodology described in British Columbia Wildlife Habitat Ratings Standards (RIC 1999a). A draft species model was prepared for each VEC considered (Keystone Wildlife Research Ltd. 2008b), using existing information on its habitat use and biology obtained through literature review. The information within the species model was used to assign a habitat suitability rating for each ecosystem unit on the map.
Habitat suitability ratings reflect the ability of a given habitat to provide the elements required for a particular life requisite of a particular species. Life requisites may range from the general (e.g. ‘Living’) to the specific (e.g. ‘Birthing’), and are chosen based on seasonal use of the study area by the species, by the life requisites that are considered to be most limiting for the species, and the amount of knowledge available regarding the species’ use of habitat. For example, the ratings created for the migrant Canada Warbler ( Wilsonia canadensis ) were for the Reproducing-eggs life requisite in the growing season, and the ratings created for mule deer (Odocoileus hemionus ) were for food and for security-thermal cover life requisites in the winter and for Reproducing-birthing in the growing season.
Draft habitat suitability ratings tables have been prepared in digital form and can be applied to the TEM map to produce a map of habitat suitability for a given species in a given season. The
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2.0 SPECIES GROUP SUMMARIES
The 2008 wildlife program was designed to address data gaps identified at the conclusion of the 2006 field program. Wildlife baseline inventories were required for butterflies, passerines, raptors/herons, waterfowl, herptiles, owls, ungulates, bats and rare plants.
RISC standards were used where available for all survey types. Some species require specialist knowledge and all required that survey sites be located appropriately relative to mapped habitat units and suitable habitat. Habitat stratification was completed prior to surveys to ensure that representative sites, within the study areas, were selected. Surveys focused on critical habitats for rare or endangered species.
2.1 RAPTORS / HERONS
Diurnal predatory birds or raptors (eagles, Osprey, hawks, and falcons) and herons are potential species of concern for the study area. Stick nests of eagles and herons are protected under Section 34 of the BC Wildlife Act, whether the nest is active or inactive and large stick nests (most constructed by eagles) are prominent features along the Peace River. Follow-up nest searches were required in 2008 to:
• confirm the location and occupancy of large stick nests in the project area;
• identify potential Broad-winged Hawk nest sites in the potential Site C reservoir;
• locate possible Great Blue Heron colonies.
2.1.1 Introduction
Fourteen raptor species potentially occur in the study area (Table 2.1.1a). Four species are listed provincially. The Blue-listed Great Blue Heron also potentially occurs in the study area, but nesting has not been confirmed.
Raptors and herons associated with riparian habitats include the Osprey ( Pandion haliaetus ), the Bald Eagle ( Haliaeetus leucocephalus ) and the Great Blue Heron ( Ardea herodias ). These
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Table 2.1.1a. Diurnal raptor species known to occur in the study area.
COSEWIC Provincial CWS Priority BCCF English Name Scientific Name Status* Status Region 6 Priority
Osprey Pandion haliaetus Yellow 6 Haliaeetus Bald Eagle leucocephalus NAR Yellow 6 Golden Eagle Aquila chrysaetos NAR Yellow Accipiter gentilis Northern Goshawk atricapillus NAR Yellow medium 2 Broad-winged Hawk Buteo platypterus Blue medium 4 Northern Harrier Circus cyaneus NAR Yellow high 2 Red-tailed Hawk Buteo jamaicensis NAR Yellow 6 Merlin Falco columbarius NAR Yellow stewardship 6 Cooper’s Hawk Accipiter cooperii NAR Yellow Rough-legged Hawk Buteo lagopus NAR Blue 2 Sharp-shinned Hawk Accipiter striatus NAR Yellow Swainson’s Hawk Buteo swainsoni Red 2 Peregrine Falcon, Falco peregrinus anatum subspecies anatum SC (Apr 2007) Red medium 2 American Kestrel Falco sparverius Yellow 2 *NAR =Not At Risk, SC =Special Concern.
2.1.2 Background
Raptors and herons have been documented in the Peace River Valley since the 1970’s, during species-specific surveys and as incidental observations during other surveys (e.g. waterfowl). Historical data was collected by Thurber (1976), Ryder (1975), Blood (1979), Robertson (1999), Robertson and Hawkes (2000), Phinney (1998), Tera Environmental and Troughton (2000), Smith (2002), Hemmera (2006) and Lambie (2004, 2005, 2006, 2007, 2008).
Thurber (1976) recorded Red-tailed Hawk, Bald Eagle, Northern Harrier, Merlin, American Kestrel, Northern Goshawk, Sharp-shinned Hawk, Swainson’s Hawk and Golden Eagle in the Peace River area during waterfowl surveys between 1973 and 1974. Eleven Bald Eagles and two active eagle nests were also recorded during this period (Thurber 1976). In 1975, Osprey and Sharp-shinned Hawks were observed at the Peace River (Ryder 1975). Blood (1979) recorded 11 raptor species as casual observations between 1974 and 1977, and determined
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Systematic aerial surveys for aquatic birds were conducted in February 1996 and August 1999, with ground surveys in 1999, from the W.A.C. Bennett Dam to the Alberta border (Robertson 1999; Robertson and Hawkes 2000). Surveys in 1999 recorded 25 Bald Eagles, 1 Northern Goshawk, 1 Red-tailed Hawk and 1 American Kestrel in the Peace River Corridor (Robertson 1999).
Phinney (1998) compiled bird-sighting data from the area around Dawson Creek (45 km west; 35 km north; 40 km southwest; and east to the Alberta border) during five field seasons from 1991 to 1995. Provincially-listed raptors and herons recorded included the Peregrine Falcon, Broad-winged Hawk and Great Blue Heron.
During avian surveys in 2000 near the proposed Dunvegan Hydroelectric Project, on the Peace River in Alberta, the following raptors were observed: Golden Eagle, Bald Eagle, Northern Harrier, Sharp-shinned Hawk, Cooper’s Hawk, Broad-winged Hawk, Red-tailed Hawk, American Kestrel, Merlin and Prairie Falcon (Tera Environmental and Troughton 2000).
A boat survey was conducted in November 2001 from 15 km upstream of Taylor to the town of Peace River, AB (Smith 2002). During that survey, 16 stick nests were observed along the Peace River. All stick nests were found in balsam poplar or aspen stands and 63% of them were located on river islands. Ten stick nests were observed between Clayhurst and Taylor.
Northern Goshawk call-playback surveys and spring and fall migration watches were conducted in 2006 on Bear Mountain, 14.5 km southwest of Dawson Creek (Hemmera 2006). Sharp- shinned Hawk, Red-tailed Hawk, Broad-winged Hawk, Northern Harrier, Rough-legged Hawk and Northern Goshawk were observed during these surveys.
The Mackenzie Bird Banding Station records birds seen each day at Mugaha Marsh (14 km NW of Mackenzie) from mid-July to late September (Lambie 2004, 2005, 2006, 2007, 2008). In 2005, a Lakewatch was started along Williston Lake from mid August to late September and this has continued yearly. This lakewatch documents birds on migration (Lambie 2005, 2006, 2007, 2008). Species recorded at the station are described below.
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Broad-winged Hawk
Broad-winged Hawks were first recorded in the Dawson Creek area in 1974 and over the next 12 years there were at least 24 more records (Phinney 1998). This raptor is considered a very rare summer visitant and breeding behaviour has been observed in the area. Phinney (1998) observed Broad-winged Hawks on 5 occasions between 1993 and 1995, and one hawk was seen carrying nesting material near Halfmoon Creek on May 18, 1993.
In 2000, a Broad-winged Hawk that was thought to breed in the area was observed near the Dunvegan Hydroelectric Project (Tera Environmental and Troughton 2000). One Broad-winged Hawk was heard near the Mackenzie Nature Observatory on August 26, 2004 (Lambie 2004). Two Broad-winged Hawks were observed on September 2, 2006 at Mugaha Marsh (Lambie 2006) and two Broad-winged Hawks were observed on Bear Mountain in 2006 (Hemmera 2006).
Peregrine Falcon
Phinney (1998) observed five Peregrine Falcons on three occasions between 1993 and 1995. This raptor is considered a very rare migrant by Phinney (1998) and is not expected to breed in the area. Peregrines were observed during fall migration at the Mackenzie Nature Observatory on September 18, 2004 and September 10, 2007 (Lambie 2004, 2007) and at the Mugaha Marsh station on September 21, 2006 and September 14, 2008 (Lambie 2006, 2008).
Swainson’s Hawk
Swainson’s Hawks have not been observed in the area by Phinney (1998) or Lambie (2004, 2005, 2006, 2007, 2008). Blood (1979) indicated that Swainson’s Hawks probably nest in the extensive agricultural areas on the uplands, but not in the Peace River Corridor (Blood 1979). Thurber (1976) observed Swainson’s Hawks in the Peace River valley during surveys conducted between 1973 and 1974.
Great Blue Heron
Phinney (1998) observed one adult and two juvenile or young of the year Great Blue Herons over Dawson Creek in 1993 and considers the occurrence of this species in the area to be accidental. There were few observations of Great Blue Heron in the Peace Region prior to July 2009 -17-
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1990, but one heron was seen on in the Peace River floodplain on two occasions in August 1999 (Robertson and Hawkes 2000). A possible heron colony was also reported by local bird expert, Chris Siddle, near the confluence of the Pine River with the Peace (Robertson and Hawkes 2000). At Mugaha Marsh, Great Blue Herons passed through on July 27, 2006 and were present throughout the banding season in 2007 (Lambie 2006, 2007).
2.1.3 Methods
Inventory methods used in 2008 followed the BC Resource Inventory Standards Committee’s (RISC) Inventory Methods for Raptors (RIC 2001) and Inventory Methods for Colonial- nesting Freshwater Birds: Eared Grebe, Red-Necked Grebe, Western Grebe, American White Pelican, and Great Blue Heron (RIC 1998b). Methods for this species group included nest surveys to locate and quantify the number of nests and breeding adults present in the river corridor and habitat suitability mapping for the listed species.
Draft habitat suitability mapping for target species was completed according to British Columbia Wildlife Habitat Ratings Standards (RIC 1999a).
2.1.3.1. Inventory Methods
A helicopter survey was conducted between the Alberta border and the Peace Canyon Dam (PRC) to locate nests built in previous years by conspicuous nesting raptors. The entire river shoreline, including islands and backchannels, was surveyed for evidence of nesting.
The methodology requires two surveys: a reconnaissance winter survey that is completed prior to spring leaf-out when last year’s nests are still easily visible and a follow-up spring survey to determine nesting activity and locate any newly constructed nests. The winter survey locates nests that may be concealed by foliage later in the season and spring surveys determine breeding activity at each nest site.
Ozi Explorer software was used to navigate, record nest locations and to record the flight route. This program provides real time tracking on digital survey maps using a GPS (Global Positioning System) signal. The system allows surveyors to locate previously identified nests and to accurately georeference current nest locations. Two observers, as well as the pilot, were used on all surveys. Field data associated with the nest locations were recorded digitally and on hard copy forms.
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Winter surveys involved a systematic search of the study area, but surveyors also visited nest sites recorded in previous years. A database of potential nest locations was compiled from surveys completed in 2006. All sites were marked on survey maps and each site was visually inspected from the air to determine if a nest was present. The location of any new nests was also recorded. When a nest was observed, the location was digitally recorded in Ozi Explorer and marked on hard-copy survey maps. Each nest was also classified as active (early breeders) or indeterminate. All nest structures documented during winter surveys were marked to be re-surveyed in the spring.
During spring surveys, each nest structure was to be visually assessed from the air to determine its breeding status and probable species. A nest would be termed active if an adult was on or near the nest, or if chicks or eggs were present. Nests would be classified as inactive if the nest had no sign of recent use. If no raptors were present at the nest site, then the potential species was deduced based on the size of the nest and its position in the tree. Information recorded for each nest included breeding species, presence of chicks, tree species, position of the nest on the tree and the relative size of the nest.
2.1.3.2. Habitat Suitability Mapping
Draft species models and standard wildlife habitat ratings were prepared for Great Blue Heron and Broad-winged Hawk (Keystone Wildlife Research Ltd. 2008b). The life requisite rated for Broad-winged Hawk was Reproducing-Eggs and highest-rated habitats include dry seral forests in structural stages 5 and 6, which were rated up to High. The life requisite rated for Great Blue Heron was Food during the Growing Season and highest-rated habitats were River, Lake, Pond, Open Water and non-forested wetlands, which were rated up to Moderate. The models and ratings tables are still draft and have not yet been revised with field data.
2.1.4 Results
Results of 2008 surveys and a compilation of data from surveys completed between 2005 and 2008 are reported below. Data from previous surveys is included when available from original databases or reports. Nest locations are presented in Maps 2.1.4a and 2.1.4b.
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2.1.4.1. 2008 Inventory Surveys
A stick nest survey was completed on May 1, 2008. Thirty-nine previously documented nest sites were investigated in the Peace River Corridor (PRC) on islands and in the forest adjacent to the river (Maps 2.1.4a and 2.1.4b). Thirty-eight new nests were observed on May 1, 2008, and two additional nests were found incidentally in 2008. Activity was confirmed at twenty-six nests during 2008, 11 of which were within the potential Site C reservoir (SCR). No inclement weather conditions were experienced during raptor nest surveys completed in 2008.
Twenty-five nests were active (11 in the potential Site C reservoir), with an adult Bald Eagle present on the nest. All eagle nests were in large balsam poplar trees in close proximity to the river corridor. One American Kestrel was observed nesting in an aspen. The status of 53 sites, 26 of which were within the potential Site C reservoir, could not be determined (no nest observed or no activity observed at the time of the survey).
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Map 2.1.4a. Raptor nests.
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Map 2.1.4b. Raptor nests.
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A follow-up survey was scheduled for June 2 to 4, 2008, in order to confirm activity. Unfortunately, helicopter flight restrictions prevented this flight and the survey was not completed. Since the status was not confirmed at 53 sites, the number of breeding large raptors in the river corridor could not be accurately estimated from 2008 data.
No heron nests were observed during surveys. Two juvenile herons were observed in the PRC study area during other surveys completed in June and August 2008.
Incidental Observations
Other raptor species observed incidentally in 2008 included American Kestrel, Broad-winged Hawk, Golden Eagle, Merlin, Northern Goshawk, Northern Harrier, Osprey, Peregrine Falcon, Red-tailed Hawk, Rough-legged Hawk and Sharp-shined Hawk. Two adult Broad-winged Hawks were observed in the TL study area in June. Five Northern Goshawks were observed in 2008, two in the PRC study area in June and August and three in the TL study area in May, August and September. One Peregrine Falcon (likely on migration) was observed flying over the river during waterfowl surveys in September. Twenty observations of Northern Harriers were recorded in 2008, 14 in the PRC study area in May, June, September and October and 6 in the TL study area in May and September.
2.1.4.2. Multiple Year Data Analysis
Hawkes et al. (2006) conducted an aerial survey to search for large nests on the Peace River on July 4, 2005. Twenty-one active Bald Eagle nests and 23 Bald Eagles were observed, as well as one Red-tailed Hawk nest, three Red-tailed Hawks, two American Kestrels and three Broad-winged Hawks (Table 2.1.4.2a, 2.1.4.2b). Boat surveys of the river were completed between June 15 and July 18, 2005 (Hawkes et al. 2006). Those surveys resulted in observations of 33 adult Bald Eagles and 12 active Bald Eagle nests, and observations of American Kestrels, Red-tailed Hawks and a Merlin.
Keystone Wildlife Research Ltd. (2006b) completed aerial surveys for raptor and heron nests in February and May, 2006. Thirty-nine nests were recorded, 19 of which were within the potential Site C reservoir (Table 2.1.4.2a, 2.1.4.2b). Seventeen active Bald Eagle nests were documented, with 10 in the potential Site C reservoir. The estimated linear density of nests in the Peace River Corridor was 10.6 active Bald Eagle nests per 100 km of shoreline. Other
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Table 2.1.4.2a. Bald Eagle nests observed in the Peace River Corridor in 2005, 2006 and 2008, including incidentals.
Peace River Corridor Year Total Nests Active Inactive 2005 21 (14) 1 (1) 25 2006 17 (10) 22 (9) 39 2008 25 (11) n/a 25 () in the potential Site C Reservoir.
One site near the BCR Bridge had five nests and was thought to be a potential heron colony. An eagle pair was observed on a nest at the location of the potential heron colony during the follow-up survey. Bald Eagles and Great Blue Herons may occasionally nest in close proximity, but eagles predate heron eggs, nestlings and fledglings (Butler 1995; Koonz 1980).
The BC Ministry of Environment (BC MoE) provided location data for known Northern Goshawk nests in the Omineca-Peace Region. Two of these nest sites are near the river corridor but neither occurs within the study area. Two draft Wildlife Habitat Areas (WHAs) have been delineated around both nest sites. These data have not been included on Maps 2.1.4a/b because the nest locations are sensitive. No call-playback surveys have been completed for Northern Goshawks to date and no nests were detected in 2005, 2006 or 2008.
A summary of raptor species observed in each study area by year is presented in Table 2.1.4.2b.
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Table 2.1.4.2b. Diurnal raptor species detections during surveys in 2005, 2006 and 2008, including incidentals.
Core* Periphery* PRC PRC TL Species Total 2005 2005 2006 2008 2008 American Kestrel 70 46 55 68 1 240 Bald Eagle 144 1 168 607 8 928 Broad-winged Hawk 9 10 2 21 Cooper's Hawk 2 1 3 Golden Eagle 1 1 4 6 Merlin 18 10 11 15 2 56 Northern Goshawk 1 1 9 2 3 16 Northern Harrier 3 6 22 14 6 51 Osprey 1 2 1 6 10 Peregrine Falcon 4 1 5 Red-tailed Hawk 18 28 60 47 5 158 Rough-legged Hawk 1 1 2 Sharp-shinned Hawk 11 20 12 43 Total 278 95 362 777 27 1539 *numbers from Hawkes et al. 2006, ‘Core’ refers to Peace River Corridor and ‘Periphery’ refers to the uplands outside of the core area.
2.1.5 Summary
Thirteen raptor species have been confirmed in the Peace River Corridor. Raptors and herons associated with riparian habitats include the Ospre, the Bald Eagle and the Great Blue Heron. The Blue-listed Broad-winged Hawk also occurs in the study area but is expected to nest in upland habitats above the potential Site C reservoir.
Bald Eagles are common breeders in the PRC study area and about half of the nests recorded during annual surveys were located within the potential Site C reservoir. The Great Blue Heron and Osprey are rare visitants to the study area (vagrants) and breeding is not expected to occur in the Peace River Corridor. The Broad-winged Hawk is rare in the study area, but breeding likely occurs in the region, outside of the Peace River Corridor. No Broad-winged Hawk nest sites have been identified in the Peace River Corridor to date.
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2.2 AMPHIBIANS
Amphibians are dependent on water for reproduction, and as such are potentially vulnerable to changes in water use and/or hydroelectric development. Systematic surveys for the western toads (SARA-listed as Special Concern) were required in 2008 to:
• determine relative abundance (if possible);
• identify potential breeding habitat.
2.2.1 Introduction
Amphibian species known to occur in the study area are summarized in Table 2.2.1a. None of these species are provincially at risk but the western toad is listed under Schedule 1 of SARA as a species of special concern (BC CDC 2009). Although, surveys focused on western toads, effort was made to document all amphibian species present in the study areas to provide a complete baseline.
Table 2.2.1a. Amphibian species known to occur in the study area.
COSEWIC SARA Provincial BCCF English Name Scientific Name Status* Schedule Status priority Boreal Chorus Frog Pseudacris maculata Yellow 3 Columbia Spotted Frog Rana luteiventris NAR Yellow 1 Wood Frog Rana sylvatica Yellow 2 Western Toad Bufo boreas SC 1 Yellow 2 Long-Toed Salamander Ambystoma macrodactylum Yellow 4 *NAR=Not at Risk, SC=Special Concern.
2.2.2 Background
Amphibians have been documented in the Peace River Valley since the 1970’s. Historical data was collected by Ryder (1975), Blood (1979), Walsh (1998), Fraker and Hawkes (2000), Hengeveld (2000) and Phinney (2007).
Blood (1979) recorded incidental observations of amphibians during inventory surveys completed between 1974 and 1976. Western toads, wood frogs and spotted frogs were observed.
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Hengeveld (2000) surveyed amphibian occurrences throughout the Williston and Dinosaur Reservoir watersheds between 1998 and 1999. Thirty-three breeding sites were identified in the Williston and Dinosaur Reservoir watersheds for western toads, wood frogs, Columbia spotted frogs and long-toed salamanders. Wood frogs and spotted frogs were observed in the Parsnip, Peace and Finlay regions of the Williston watershed.
Fraker and Hawkes (2000) searched backchannels, ponds and wetlands along the Peace River during the late summer and early fall of 1999. Western toads and wood frogs were detected during these surveys.
Phinney (2007) conducted RISC (RIC 1998c) standard auditory surveys, road surveys and pond searches from May 6 to June 23, 2007 in the Dawson Creek TSA. Eight transects were completed 3 times along forestry roads. During auditory surveys, 798 wood frogs, 1268 boreal chorus frogs and 3 western toads were detected. Road surveys detected 38 western toads and 1 wood frog. Seventy percent of frogs observed during road surveys were found along the Moberly Lake and Septimus transects. Adults and eggs were primarily found in ponds surveyed in May while hatchlings and tadpoles were found during surveys completed in June and July.
Western Toad
Blood (1979) indicated that western toads were common near rivers in the Peace River area and breeding may occur in cut-off river channels. Fraker and Hawkes (2000) found western toads throughout the Peace River Valley and surrounding wetlands during surveys. Phinney (2007) documented western toads in ponds along the Bear Mountain, Del Rio and North Monias transects.
Wood Frog
Blood (1979) reported that wood frogs were present in moist woods, ponds and backchannels in the Peace River area. Fraker and Hawkes (2000) detected wood frogs in the Peace River Valley but none were observed on islands or on the north bank of the Peace River. During pond breeding surveys in the Dawson Creek TSA, wood frog egg masses were observed the most frequently (Phinney 2007).
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Boreal Chorus Frog
The boreal chorus frog was the species detected the most frequently during auditory surveys in the Dawson Creek TSA (Phinney 2007).
Long-toed Salamander
Walsh (1998) reported the long-toed salamander in northern Alberta, which was an extension to the known range for this species. Ryder (1975) recorded a long-toed salamander east of Taylor in the Peace River Corridor in 1975. In 2007, long-toed salamanders were found in ponds on Septimus and Moberly Lake transects (Phinney 2007).
2.2.3 Methods
Inventory methods used in 2008 followed the BC Resource Inventory Standards Committee’s Inventory Methods for Pond-Breeding Amphibians and Painted Turtle (RIC 1998c). The survey methodology for amphibians included a map-based evaluation of habitat suitability for western toads, field review and confirmation of habitat suitability, and field surveys.
Draft habitat suitability mapping for western toad was completed according to British Columbia Wildlife Habitat Ratings Standards (RIC 1999a).
2.2.3.1. Inventory Methods
Amphibian surveys were completed in the PRC and TL. Habitat maps were used to identify potentially suitable breeding sites for amphibians including wetlands, ponds, lakes and other habitats with standing water. Accessible sites were surveyed during the appropriate time of year (spring thaw to August) to determine the presence of amphibians, their breeding status and the suitability of the habitat. Western toads were the target species for wetland searches and road transects, but all species observed were recorded.
Survey methods for amphibians included systematic wetland searches, auditory surveys and road transects. Auditory surveys are recommended for vocal species such as the wood and chorus frog and indicate the presence of male frogs, but are unlikely to detect western toads. Systematic wetland searches include searches for egg masses and give a direct indication of the number of breeding females present in an area. Road transects can be used to identify
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Amphibians expected to lay eggs in the early spring (February - March) include long-toed salamanders, boreal chorus frogs, Columbia spotted frogs and wood frogs. Wood and chorus frogs will also be actively vocalizing at this time. Due to the northern location of the study area and annual weather patterns, breeding is believed to begin in late April, which typically coincides with the spring snowmelt. Western toads are expected to start gathering at breeding sites in the mid-spring (April to May). The rate of development of eggs and tadpoles depends largely on water temperature but generally, froglets and toadlets will disperse from breeding areas in the late summer (July to September).
General survey conditions were recorded at the start and end of all surveys, including cloud cover, ambient air temperature, precipitation and wind speed.
Pond Breeding Surveys
Suitable amphibian breeding sites identified during field reconnaissance in 2006 (Keystone Wildlife Research Ltd. 2006b) were revisited to confirm breeding activity for western toads. Additional, potentially suitable breeding sites identified on the TEM mapping, or incidentally encountered during other field surveys (including river backchannels), were also surveyed.
The shoreline and shallow sections of each wetland were surveyed for egg masses, tadpoles and adult amphibians. Information collected at each site included UTM (NAD 83) location, habitat type (marsh, fen, swamp, shallow water, backchannel), size of water body, percent open water, percent solar exposure, duration of habitat, water condition (turbidity), air and water temperature and percentage of the wetland surveyed.
Habitat attributes were recorded at the end of the wetland survey and were representative of the entire wetland. Larger wetland complexes were divided into smaller areas based on areas with continuous open water.
All amphibians detected were recorded, including species, development stage, count, aggregate (egg mass) size, length of species (tadpoles and adults), water depth of observation, distance from shore to observation, average water depth, water drop (slope from pond edge to deeper
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Auditory Surveys
Auditory surveys were conducted for the wood frog and boreal chorus frog along transects in proximity to wetlands and backchannels. Auditory surveys are not suitable for spotted frog or western toad. Nocturnal surveys began a half-hour before dusk and continued until midnight.
Each transect consisted of four to seven listening stations, spaced 500 m apart. At each listening station, observers waited for one minute after leaving the vehicle or arriving at the wetland, then listened for three minutes for frog calls. Observers listened for up to two additional minutes if ambient noise (from traffic, etc.) interfered with the ability to hear calls. Total listening time at each station was four to six minutes. All species seen or heard were recorded, and the direction and distance to the calling frog(s) was estimated. Inclement weather conditions (i.e. rain, strong wind) can affect the number of frogs calling and the ability of surveyors to detect them. If these conditions were experienced along a transect, not all stations may have been completed.
Stations were revisited several times during the breeding season, unless the habitat was unsuitable (e.g. cultivated fields) and no frogs were heard on the initial visit. Transect starting points were varied between visits to sample listening stations at different times. The UTM location (NAD 83) and start/end time of each station was recorded at each station.
Observations were recorded on a standard data sheet using the call index recommended by Gartshore et al. (1992). This index includes a 4-code scheme for recording frog calls: 0- no calls detected, 1- individuals can be counted (no overlapping calls), 2- calls of individuals are distinguishable, but some calls overlap, 3- full chorus, or continuous calls, where individuals cannot be distinguished. All observations were noted on standard RISC datasheets customized for the project.
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Amphibian Road Surveys
Road surveys were conducted along roads in proximity to suitable wetlands in order to detect migration routes for western toads. Following metamorphosis, juvenile western toads can often be found migrating, en masse, away from the breeding sites (Matsuda et al. 2006), making them particularly easy to locate with road surveys in suitable conditions. Surveys began at dusk and continued for 2 to 5 hours. Two surveyors travelled in a motor vehicle at 35 to 55 km/hr or on foot, using low beam headlights or headlamps to detect road kills and amphibians moving across the road. The UTM location (NAD 83), time, species, condition (live or road-killed), development stage, size and number observed were recorded for all animals detected along each transect. Weather conditions were recorded at the start and end of each transect. The occurrence of rainfall in the last 12 or 24 hours was also recorded since this can affect survey results. All observations were noted on standard RISC datasheets customized for the project.
Analysis
Comparative analyses were conducted for egg and tadpole observations during pond-breeding surveys conducted in 2006 and 2008, in order to determine the timing of breeding for each species. The egg-mass and tadpole data were separated for the analysis because they are not directly comparable ( i.e., one egg mass does not equal a specific number of tadpoles at a later date). Data from 2005 (Hawkes et al. 2006) were excluded from this analysis because they did not include information on developmental stage of amphibians observed during surveys.
Auditory frog data from 2006 and 2008 were compiled and analyzed to determine the difference in relative abundance of calling males between the two study areas (PRC, TL) and the potential Site C reservoir (RIC 1998c). Auditory observations were recorded using the call index recommended by Gartshore et al. (1992) and this index was used as a measure of relative abundance. This analysis focused on the level of activity at “active” sites, in order to compare the level of activity in different areas. Therefore, visual detections and survey sites with no detections were excluded from this analysis. A Kruskal-Wallis test was performed to determine if the level of auditory activity differed between the two study areas and the potential Site C reservoir, followed by Mann-Whitney tests to identify which ones were different (Zar 1999). These tests are non-parametric statistical tests for comparing groups of data to see if they differ.
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Assumptions of the analysis include:
• the proportion of total males at each station that emit auditory calls is the same at all stations;
• relative activity is a representative measure of relative abundance.
2.2.3.2. Habitat Suitability Mapping
A draft species model and ratings table (Keystone Wildlife Research Ltd. 2008b) was prepared for western toad, the only amphibian species classified as at-risk (SARA Schedule 1 Special Concern). Ratings were created for Reproducing-Eggs, and habitats rated the highest included waterbodies (lakes, rivers, ponds, open water), wetlands, and forested floodplain habitats where small, temporary waterbodies are likely. Those ecosystems were rated up to High.
2.2.4 Results
Results of 2008 surveys and a compilation of data from surveys completed between 2005 and 2008 are reported below. Data from previous surveys are included when available from original databases or reports. The location of amphibian surveys completed in 2005, 2006 and 2008 are show on Map 2.2.4a, 2.2.4b and 2.2.4c.
2.2.4.1. 2008 Inventory Surveys
The onset of spring was delayed in 2008, with cold weather persisting into May. Consequently, surveys did not begin until early May when some suitable wetlands had thawed and open water was present. Surveys were completed in the Peace River Corridor (PRC) and the transmission line (TL) study areas. Effort was focused in the transmission line study area, which had not been previously surveyed for amphibians and has a large amount of suitable habitat.
Pond-Breeding Amphibian Surveys
Surveys were completed during three survey periods: May 6 to May 27, June 1 to June 28, and July 27 to August 16, 2008. No inclement weather conditions were experienced during pond- breeding amphibian searches completed in 2008. Surveys in May and June identified egg masses and surveys in July and August were completed to determine the development stage of tadpoles and their potential to disperse. Nine wetland complexes and backchannels were surveyed 1-3 times in the PRC study area and 43 wetlands were surveyed 1-7 times in the TL
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Species detected during wetland surveys in 2008 include the western toad, boreal chorus frog and wood frog (Appendix 4c, 4d). The Columbia spotted frog and long-toed salamander were not detected during 2008 wetland surveys. Breeding of the western toad, boreal chorus frog and wood frog was confirmed during surveys with the observation of egg masses and tadpoles (Appendix 4c, 4d). A summary of the habitat types in which species were detected is included in section 2.2.4.2.
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Map 2.2.4a. Amphibian surveys.
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Map 2.2.4b. Amphibian surveys.
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Map 2.2.4c. Amphibian road surveys.
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Western toads were confirmed to be breeding in three backchannels and two wetlands in the PRC study area and in three wetlands in the TL study area. All three backchannels are within the potential Site C reservoir. Adult and juvenile toads were observed in an additional six wetlands in the TL study area. Adult chorus frogs were observed in 2 wetlands in the PRC study area and 18 wetlands in the TL study area. Breeding was confirmed in 1 of the 18 wetlands surveyed in the TL study area. Adult and juvenile wood frogs were observed in five backchannels and one wetland in the PRC study area and breeding was confirmed in the wetland. Three of the five backchannels are within the potential Site C reservoir. In the TL study area, breeding wood frogs were observed in 13 wetlands and adults or juveniles were observed in an additional 15 wetlands.
Auditory Surveys
Auditory surveys for amphibians were completed during owl survey transects prior to broadcasting owl calls or in the afternoon or evening after other field surveys. Transects were completed during two survey periods: May 5 to May 18 and May 26 to June 10, 2008.
Eight transects were established in the study area, five in the PRC study area and three in the TL study area. Each transect was visited 1 to 6 times, with 1 to 7 stations per visit. In total, 25 surveys were completed, 18 in PRC study area (Table 2.2.4.1a) and 8 in the TL study area (Table 2.2.4.1b). Search effort in 2008 totalled 5.25 hours in the PRC study area and 2.93 hours in the TL study area.
Table 2.2.4.1a. Summary of auditory frog survey effort in the Peace River Corridor in 2008.
Total Survey Time Transect Label Visit Date Total Stations Surveyed (hrs:min) 14-May-08 5 0:45 15-May-08 6 0:25 0* 8-Jun-08 4 0:12 9-Jun-08 4 0:14 10-Jun-08 4 0:08 1* 16-May-08 5 0:16 17-May-08 4 0:14 18-May-08 4 0:12 29-May-08 6 0:23 30-May-08 4 0:05
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Total Survey Time Transect Label Visit Date Total Stations Surveyed (hrs:min) 31-May-08 5 0:19 17-May-08 4 0:16 5* 26-May-08 4 0:18 13-May-08 1 0:03 6* 14-May-08 5 0:14 15-May-08 6 0:20 5-May-08 4 0:20 7 6-May-08 5 0:31 Total 80 5:15 *transect stations are wholly or partially within the potential Site C reservoir.
Table 2.2.4.1b. Summary of auditory frog survey effort along the Transmission Line in 2008.
Total Survey Time Transect Label Visit Date Total Stations Surveyed (hrs:min) 7-May-08 6 0:22 2 8-May-08 3 0:12 9-May-08 7 0:21 8 10-May-08 7 0:27 7-May-08 6 0:26 10 8-May-08 7 0:35 TC_2 11-May-08 7 0:21 TC_3 12-May-08 4 0:12 Total 47 2:56
Boreal chorus frogs were detected on all auditory surveys in both study areas (Table 2.2.4.1c). Wood frogs were only detected in the TL study area. Ten western toads were seen during auditory surveys in the PRC study area.
Table 2.2.4.1c. Number of each amphibian species detected during auditory surveys in 2008.
Boreal Chorus Study Area Transect Label Western Toad* Wood Frog Frog 0 10* 8 Peace River 1 23 Corridor 6 5 7 7 Transmission Line 2 13 1 8 32 10 1 3
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Boreal Chorus Study Area Transect Label Western Toad* Wood Frog Frog TC_2 45 6 TC_3 12 4 Total 10 146 14 *visual observation.
Amphibian Road Surveys
Roads in proximity to the project footprint that would likely have higher use during the construction or operation of the potential Site C project were targeted. Three amphibian road survey transects were established in the study area, one in the PRC study area (Johnson Road) and two in the TL study area (Del Rio Road East and West). Each transect included 4 to 17 segments over 10 to 49 km. Transects were completed during two survey periods: July 26 to 27 and August 11 to 15, 2008 (Table 2.2.4.1d).
Table 2.2.4.1d. Summary of amphibian road survey effort in 2008.
Total Survey Time Transect Label Visit Date Total Stations Surveyed (hrs:min) DRE 27-Jul-08 4 4:10 DRE 12-Aug-08 11 7:27 DRW 26-Jul-08 7 4:12 DRW 11-Aug-08 17 7:46 JR 15-Aug-08 4 3:05 Total 43 26:40
Adult and juvenile western toads were observed on the road during all surveys (Table 2.2.4.1e). Wood frogs and boreal chorus frogs were also detected during surveys but were less frequently encountered. Multiple occurrences of wood frogs were observed in a small area at the western end of the Del Rio West transect, indicating proximity to suitable breeding habitat (Map 2.2.4c). Recently-killed toads were also recorded on all transects, with notable concentrations on Johnson Road at the west end near Highway 97 and in the middle of the Del Rio West transect.
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Table 2.2.4.1e. Number of amphibian species detected during road surveys in 2008.
Western Toad Boreal Chorus Frog Wood Frog Transect Sub Sub Sub Total Label Adult Juvenile Tadpole Adult Juvenile Tadpole adult adult adult DRE 52 87 60 1 1 201 DRW 154 29 55 2 1 5 7 253 JR 35 1 1 1 38 Total 241 117 115 1 1 4 1 5 7 492
Approximately half of all western toads observed were adults, a quarter were juveniles and the remainder were sub adults. The majority of juvenile observations were recorded from one area on the Del Rio East transect indicating proximity to suitable breeding habitat for western toads.
Incidental Observations Western toads, boreal chorus frogs and wood frogs were all detected incidentally in both the PRC and the TL study areas (Table 2.2.4.1f). Many western toad tadpoles were observed in the transmission line study area.
Table 2.2.4.1f. Number of amphibians detected incidentally during surveys in 2008.
PRC TL Developmental Species Number of Number of Total Stage Count Count Observations Observations Adult 12 20 17 20 40 Western Toad Tadpole 8 148 5 1005 1153 Unknown 1 1 1 1 2 Boreal Chorus Adult 12 23 7 15 38 Frog Adult 6 8 25 70 78 Wood Frog Tadpole 7 12 12 16 28 Total 46 212 67 1127 1339
2.2.4.2. Multiple Year Data Analysis
Hawkes et al. (2006) conducted RISC standard wetland searches for amphibians in the Peace River Corridor (core) and in the surrounding uplands (periphery) (Table 2.2.4.2a). Wood frogs, western toads and long-toed salamanders were detected.
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Keystone Wildlife Research Ltd. (2006b) completed RISC standard time-constrained wetland searches for pond-breeding amphibians and auditory frog surveys in the Peace River Corridor (PRC) in 2006 (Table 2.2.4.2a, 2.2.4.2b). At least one amphibian species was documented at 31 sites surveyed during pond-breeding amphibian surveys, with western toads detected the most frequently. During auditory surveys, wood frogs were detected the most frequently.
Table 2.2.4.2a. Total pond-breeding amphibian survey effort completed 2005, 2006 and 2008.
Number of Wetland Number of sites Total Survey Time Study Area Year Searches* sampled (hrs:min) Core June 4 to July 24, 50 42 11:56 Periphery 2005 47 41 19:18 April 23 to June 21, 50 Peace River 63 19:10 2006 Corridor May 6 to August 16, 15 9 22:34 Transmission Line 2008 61 43 51:58 Total 236 185 124:56 *Number of wetland searches includes replicates.
Table 2.2.4.2b. Total auditory amphibian survey effort completed in 2006 and 2008.
Number of auditory Total Survey Time Study Area Year surveys (hrs:min) May 19 to April 31, 2006 51 10:16 Peace River Corridor 80 5:15 May 6 to August 16, 2008 Transmission Line 47 2:56 Total 178 18:27
Ten different habitats types were surveyed in 2006 and 2008 (Table 2.2.4.2c). Western toads, wood frogs and boreal chorus frogs were all found in a wide range of habitats in the PRC and TL study areas. No correlation was observed between the presence of amphibian species and habitat type.
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Table 2.2.4.2c. Number of habitat types at which amphibian species were detected during surveys completed in 2006 and 2008.
Number of sites at which species detected* No Boreal Columbia Study Amphibian Long-toed Western Chorus Spotted Wood Unknown Area Habitat Type Detected Salamander Toad Frog Frog Frog Frog Ditch 1 Gravel Bar 1 1 River Backchannel 1 River 1 Puddle 1 PRC Shallow Water 1 1 1 Bog 1 Fen 1 1 1 Marsh 8 2 3 4 Swamp 1 PRC Total 12 1 4 3 3 8 Ditch 2 River Backchannel 6 2 1 2 Shallow SCR Water 2 3 Bog 2 1 Fen 3 Marsh 2 1 Swamp 1 SCR Total 16 4 2 5 1 Ditch 2 2 5 Puddle 1 1 Lake 2 1 2 TL Shallow Water 2 3 5 7 1 Bog 1 1 2 Fen 3 1 2 Marsh 6 3 8 16 2 TL Total 12 12 19 33 3 Total 40 1 20 24 3 46 4 *Due to overlaps in transects and multiple habitats types present in complex wetland sites, numbers of sites may not correlate to those provided in Table 2.2.4.2a.
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Pond Breeding Surveys
During surveys in 2006, egg masses were observed between April 30 and May 28 and tadpoles were first observed on May 31. In 2008, egg masses were observed between May 10 and 12 and tadpoles were first observed on May 19.
Boreal chorus frog, Columbia spotted frog, western toad and wood frog egg masses were observed during 17 surveys completed prior to May 31 (Table 2.2.4.2d). Wood frog egg masses were found the most frequently. There are insufficient observations of egg masses to make comparisons between species.
Table 2.2.4.2d. Survey sites where egg masses were observed during pond- breeding amphibian surveys completed in 2006 and 2008.
Study Pond Breeding Boreal Columbia Western Wood Area Survey Label Date Chorus Frog Spotted Frog Toad Frog PRC RB19 28-May-06 0 0 1 4 PRC RB29 23-Apr-06 0 0 0 20 PRC WE 27-Apr-06 0 0 0 30 PRC WG 28-May-06 0 0 0 27 PRC WH 30-Apr-06 0 14 0 0 PRC WK 30-Apr-06 0 16 0 0 PRC WX 27-Apr-06 0 0 0 63 SCR WO 27-May-06 8 0 0 0 TL TC 1a 10-May-08 0 0 0 3 TL TC 1b 10-May-08 1 0 0 11 TL TC 2 10-May-08 0 0 0 1 TL TC 5 10-May-08 0 0 0 15 TL TC 10 11-May-08 0 0 0 1 TL TC 12 11-May-08 0 0 0 15 TL TC 13 11-May-08 0 0 0 3 TL TC 19 11-May-08 0 0 0 13 TL TC 21 12-May-08 0 0 0 10
Western toad or wood frog tadpoles were observed during 22 of the tadpole surveys between May 15 and July 31, with estimated tadpole abundances ranging from 1 to 30,000 (Table 2.2.4.2e). Western toad tadpoles were observed between May 27 and July 28, while wood frog tadpoles were observed from May 19 to July 28.
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Table 2.2.4.2e. Survey sites where tadpoles were observed during pond- breeding amphibian surveys completed in 2006 and 2008.
Pond Breeding Survey Study Area Date Western Toad Wood Frog Label Peace River Corridor WBF 27-May-08 10000 0 Peace River Corridor WR 1-Jun-06 9 0 Peace River Corridor WR 27-May-08 1 0 Peace River Corridor WS 1-Jun-06 0 100 Peace River Corridor WS 11-Jun-08 0 102 Reservoir RB9 21-Jun-08 700 0 Reservoir RB9 2-Jun-06 310 0 Reservoir RB23 23-Jun-08 20113 0 Reservoir RB27a 31-May-06 397 0 Reservoir RB27a 9-Jun-08 257 0 Reservoir RB27b 21-Jun-06 20 0 Transmission Line TC_9 19-May-08 0 5000 Transmission Line TC_9 28-Jun-08 0 1 Transmission Line TC_37 12-Jun-08 0 2 Transmission Line TC_38 13-Jun-08 30000 0 Transmission Line TC_40 27-Jun-08 15100 0 Transmission Line TC_40 28-Jun-08 2 0 Transmission Line TC_41 28-Jun-08 0 50 Transmission Line TC_42 3-Jun-08 0 20 Transmission Line TC_42 28-Jun-08 0 100 Transmission Line TC_42 28-Jul-08 0 2 Transmission Line TC_43 27-Jul-08 3 0
Insufficient data are available to make comparisons between species, but differences in breeding timing between species has been observed in other areas of the province (Matsuda et al. 2006). Generally, western toads are expected to breed later in the season than the other amphibians found in the study area (Corkran and Thoms 1996). During surveys in 2006 and 2008, western toad eggs and/or tadpoles were found during the same period as wood frog and chorus frog eggs and/or tadpoles.
Auditory Surveys
Sample sites with breeding amphibians in the Transmission Line study area were found to be significantly more active than breeding sites in the Peace River Corridor (p<0.001). No other comparisons of study areas showed significant differences in activity (p>0.05), although weak trends were observed with the Peace River Corridor having lower activity levels than the
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2.2.5 Summary
Breeding was confirmed for four species at 29 different sites in the study areas. Western toads were observed breeding in both study areas and in the potential Site C reservoir. Wood frogs were not observed in the potential Site C reservoir, boreal chorus frogs were not observed in the PRC study area, and Columbia spotted frogs were only observed in the PRC study area, but not in the potential Site C reservoir. Auditory surveys indicate higher activity in the TL study area than in the PRC.
Western toads are common in the study area and breed in all habitat types. Overlap in the timing of breeding was observed between wood frogs, boreal chorus frogs and western toads in the study area in both 2006 and 2008. The onset of breeding is dependent upon the local conditions but is generally expected to occur in late April or early May.
2.3 OWLS
Great Horned and Great Gray Owls rely mainly on large stick nests constructed by other species. Boreal Owls nest in existing woodpecker cavities in spruce ( Picea spp.), aspen (Populus ssp.), birch ( Betula spp.) and cottonwood ( Populus balsamifera ) trees (Hayward et al. 1993). Large trees capable of supporting large stick nests and cavities are most prevalent in balsam poplar riparian habitats in the Peace River Corridor.
Nesting habitat for owls is believed to be a limiting life requisite. Additional surveys in 2008 were required to:
• confirm species presence;
• determine the use of balsam poplar floodplains by nesting owls.
2.3.1 Introduction
Nine owl species occur in the study area (Table 2.3.1a). Species of particular concern include the Great Gray Owl, the Great Horned Owl, the Boreal Owl due to their nesting habitat requirements. The Short-eared Owl is provincially Blue-listed and is a SARA species of Special
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Concern which nests on the ground in large patches of tall, dense, ungrazed grassland (Wiggins et al. 2006). No species-specific surveys were completed for the Short-eared Owl in 2008 due the lack of suitable nesting habitat in riparian areas that may be affected by the potential Site C project.
Table 2.3.1a. Owl species known to occur in the study area.
CWS COSEWIC SARA Provincial Priority BCCF English Name Scientific Name Status* Schedule Status Region 6** Priority Barred Owl Strix varia Yellow 6 Boreal Owl Aegolius funereus NAR Yellow S 3 Great Gray Owl Strix nebulosa NAR Yellow M 4 Great Horned Owl Bubo virginianus Yellow 6 Long-eared Owl Asio otus Yellow 4 NAR (May Northern Hawk Owl Surnia ulula 1992) Yellow M 5 Northern Saw-whet Owl Aegolius acadicus Yellow 5 Northern Pygmy- Owl Glaucidium gnoma Yellow 1 Short-eared Owl Asio flammeu s SC (Mar 2008) 3 Blue H 2 *NAR =Not At Risk, SC =Special Concern; **H =High, M =Medium, S =Stewardship .
All owls are predators of small mammals, although birds and invertebrates are also taken. The Short-eared Owl nests on the ground and the remaining species nest in tree cavities or in abandoned stick nests built by other birds.
Owls are secretive birds that are typically active at night over sometimes large home ranges, therefore a considerable amount of survey effort is often required to document occurrence. Broadcasting territorial calls during the breeding season in potentially suitable habitat increases the chance of detecting owls, especially if surveys are repeated. Surveying during the breeding season is critical since most owls are territorial and will defend areas associated with nesting sites. In addition to increasing the survey effort, repeating surveys ensure that factors that may reduce owl response rates (e.g., possible lunar cycle or inclement weather) do not occur during the entire search period. Repeated observations in the same area on different days can also indicate that owls are resident rather than transient, and that the survey is within the owls’ home range.
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Territorial owls may move considerable distances to defend a territory from a possible intruder. Some owl species (e.g., Barred and Northern Spotted Owls) have crossed valleys and followed surveyors for a number of stations within an established territory, while others will simply respond to call playback surveys from a distance (S. Hilton, pers. comm. 2009). Therefore, a survey may cover a large area, providing there is no physical barrier to owl movement or other factors (ambient noises) that may limit an observer’s ability to detect an owl.
Due to the size of the study area and the number of owl species present, it is not feasible to census each owl species to determine the total number of territories within the study area. The goal of surveys was to collect data to provide an estimate of the relative abundance of individual territories for different species within the study area and compare the outcome with abundance estimates for other areas of the province.
2.3.2 Background
Owls have been documented in the Peace River Valley since the 1970’s. Historical data were collected by Blood (1979), Merkens and Booth (1996), Booth and Harrison (1997), Phinney (1998), Robertson and Hawkes (2000), Hemmera (2006), Phinney (2007) and Lambie (2004, 2005, 2006, 2007, 2008).
Booth and Harrison (1997) completed call-playback surveys between March 17 and April 14, 2007, to determine the occurrence and abundance of owl species in aspen and mixed forest stands in the Dawson Creek Forest District. Transects were completed in aspen forests in the Del Rio area and in mixed woods stands near Coldstream Creek, Boudreau Lake and the A1 road northeast of Chetwynd. Surveys targeted Northern Saw-whet Owl, Boreal Owl, Great Horned Owl and Barred Owl. Most owls were detected during the first two weeks in April.
Hemmera (2006) completed owl call-playback surveys between March and April 2006, on Bear Mountain, 14.5 km southwest of Dawson Creek. Those surveys targeted Northern Saw-whet Owl, Boreal Owl, Barred Owl and Great Horned Owl. Observers detected one Northern Pygmy Owl, two Boreal Owls, three Northern Saw-whet Owls, one Great Horned Owl and four Barred Owls.
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The Mackenzie Bird Banding Station recorded birds seen from mid-July to late September (Lambie 2004, 2005, 2006, 2007, 2008) at Mugaha Marsh (14 km NW of Mackenzie). Owl species observed were recorded and some species were banded.
Barred Owl
Barred Owls first appeared in the province in 1943 (Grant 1966), arriving from the east through the boreal forests in Saskatchewan and Alberta. They are now found in most areas of the province, Alaska (Gibson and Kessel 1992), and south to California (Dark et al. 1998). Their increasing numbers and expanding range has led to a number of concerns regarding inter- specific competition and possible declines in the populations of other owl species (Taylor and Forsman 1976; Dunbar et al. 1991; COSEWIC 2002).
Barred Owls were considered uncommon breeders to rare residents in the Peace River Corridor from the 1970s to the late 1990’s in the Peace River area (Blood 1979; Phinney 1998). Phinney (1998) noted that Barred Owls might be more widespread than records indicate due to the nocturnal nature of this species. Booth and Harrison (1997) detected 12 Barred Owls in the mixed wood stands during call-playback surveys, but no Barred Owls were recorded in the Del Rio aspen forest surveyed. They could not account for the absence of Barred Owls in the Del Rio area. Phinney (1998) recorded Barred Owls between Bear Mountain and Bissette Creek in late April of 1994 and 1995.
Boreal Owl
In 2004, Boreal Owls were targeted for banding at the Mackenzie Nature Observatory (Lambie 2004). Twelve Boreal Owls were banded in 2004 and 2006 (Lambie 2004, 2006). Booth and Harrison (1997) did not detect Boreal Owls during call-playback surveys completed for this species in the Dawson Creek Forest District.
Great Gray Owl
Phinney (1998) observed a pair of Great Gray Owls nesting in mature mixed forest at Sunset Hill in 1992. Merkens and Booth (1996) observed one adult Great Gray and three juveniles in the Del Rio study area in 1995. Booth and Harrison (1997) detected six Great Gray Owls in the Del Rio area during call-playback surveys in 1997 and found this species to be associated with
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Great Horned Owl
Blood (1979) considered Great Horned Owls to be common breeders in the Peace Region. Phinney (1998) reported the species as an uncommon resident and observed two flightless juveniles leaving a nest May 18, 1991, and adults feeding a recently fledged juvenile June 30, 1995. Booth and Harrison (1997) detected 13 Great Horned Owls in a variety of habitats during call-playback surveys in 1997. They found that Great Horned Owls were most often detected before midnight. Robertson and Hawkes (2000) noted a Great Horned Owl near the Moberly River in 2003. A Great Horned Owl was reported on the Christmas bird count in Mackenzie in 2005 (Lambie 2005).
Northern Saw-whet Owl
In 2004, Northern Saw-whet Owls were targeted for banding at the Mackenzie Nature Observatory and 53 were banded (Lambie 2004). Between 2005 and 2007, 164 Northern Saw- whet Owls were captured at Mackenzie Nature Observatory (Lambie 2005, 2006, 2007). Booth and Harrison (1997) detected one Northern Saw-whet Owl during call-playback surveys in mixed woods.
Short-eared Owl
The early arrival date for Short-eared Owls in the Peace Region was April 18, 1994 (Phinney 1998). Two juveniles were observed in a field west of Charlie Lake on June 19, 1995 and two birds were seen hunting over a field 1.25 km east of Bessborough on June 21, 1997 (BC CDC 2009). One Short-eared Owl was seen hunting at the Mackenzie Airport on November 16, 2005 (Lambie 2005).
2.3.3 Methods
Inventory methods used in 2008 followed the BC Resource Inventory Standards Committee’s (RISC) Inventory Methods for Raptors (RIC 2001) and Inventory Methods for Owl Surveys (Hausleitner 2006). Species targeted in 2008 surveys included the Great Horned Owl, the Great Gray Owl and the Boreal Owl.
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Draft habitat suitability mapping for target species was completed according to British Columbia Wildlife Habitat Ratings Standards (RIC 1999a).
2.3.3.1. Inventory Methods
Owl surveys were completed in the PRC and TL study areas. Habitat suitability maps were used to identify potentially suitable nesting habitat for Great Horned Owl, Great Gray Owl and Boreal Owl. Transects were laid out in accessible areas with suitable habitat, that could be safely traversed at night. Eight owl transects were established in the study area and each transect was surveyed up to three times (May and June) for each target species. Target species for each transect were identified based on the availability of suitable habitat, therefore not all species were surveyed on all transects.
Species-specific call-playback surveys were conducted for Great Horned Owls, Great Gray Owls and Boreal Owls. One species call was broadcast per transect per night, resulting in multiple surveys of each transect (1 species/night/transect). Surveys were conducted between ½ hour after dusk and ½ hour before sunrise. Each call-playback station was 15 minutes long, with pre-recorded owl calls broadcast 3 times, for up to 1 minute, at 5-minute intervals. The listening time at a call station was extended if ambient noise interfered with the surveyor’s ability to detect owls. The standards recommend an inter-station distance of 600 m for Great Horned Owls, 700 m for Boreal Owls and 800 for Great Gray Owls (Hausleitner 2006 and RIC 2001). These distances were used unless specific circumstances indicated that the distance should be altered (e.g. if the same owl was heard at consecutive stations the inter-station distance would be increased). After playing pre-recorded calls, observers listened and watched for owls responding vocally or approaching observers. Any owl species detected were recorded.
Information was recorded on RISC standard data forms modified for this project. Specific data recorded at each station included: UTM location (NAD 83), start and stop time and weather conditions. When an owl was detected, the minimum information recorded included the species and number observed. Additional information that was collected when possible included time of response, time elapsed, call type, distance and direction to owl, detection duration, call type, age class, sex and a description of the owl’s activity (hunting, territorial behaviour).
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Ground-based nest searches were also performed if an owl pair was located during a nocturnal survey. This involved searching the area of the detection for sign such as whitewash, prey pluckings and pellets.
2.3.3.2. Habitat Suitability Mapping
Draft species models and habitat suitability ratings were prepared for Barred Owl, Boreal Owl, Great Gray Owl, Great Horned Owl, Northern Saw-whet Owl and Short-eared Owl (Keystone Wildlife Research Ltd. 2008b). The life requisite rated for all species except the Short-eared Owl was Reproducing-Eggs. Habitats for Short-eared Owls were rated for Living in All seasons, and cultivated fields and wetlands were given the highest rating (up to Moderate). Moist to wet forests were rated highest (up to Moderate) for Northern Saw-whet Owls, on the assumption that these ecosystems would likely have the greatest abundance of trees with suitable cavities (primarily balsam poplar and aspen). Mesic to moist forests capable of producing large trees and snags were rated highest for Great Horned Owl (up to Moderate), Great Gray Owl (up to High), Boreal Owl (up to High) and Barred Owl (up to High).
2.3.3.3. Analysis
Data from 2006 and 2008 were used in species-specific territory analyses. Surveys completed in 2005 (Hawkes et al. 2006) were excluded since specific locations for owl detections were not available.
The location of each detected owl was mapped based on the detection distance and direction from the transect station. The distance to detection was corrected if it was apparent, based on the topography, observer range and broadcasting capabilities of the species, that the distance was overestimated. Generally, the maximum detection distance was 1 km, unless the intervening habitat included large open areas like fields or lakes (S. Hilton. pers. comm. 2009). If no direction and/or distance were recorded then it was assumed that the detection occurred within a 1 km radius of the call station.
The mapped owl detections were viewed and clustered into territories by a biologist. Territories were centred around clustered observations based on: 1) detection of paired adults 2) detection of young 3) multiple detections in a single year 4) single detections in multiple years 5) a single detection in a single year 6) a single incidental detection. Professional judgement was used to determine territories by clustering observations in relation to known breeding home range sizes. July 2009 -51-
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The home range sizes of Boreal, Great Horned and Northern Saw-whet Owls were assumed to be similar to those described in Inventory Methods for Owl Surveys (Hausleitner 2006). The Great Gray Owl home range size was based on other published literature (Bull et al. 1998 cited in Ulev 2007; van Riper and van Wagtendonk 2006). This method may overestimate the number of established territories.
2.3.4 Results
Results of 2008 surveys and a compilation of data from surveys completed between 2005 and 2008 are reported below. Data from previous surveys are included when available from original databases or reports. The locations of owl surveys completed in 2005, 2006 and 2008 are shown on Map 2.3.4a and 2.3.4b.
2.3.4.1. 2008 Inventory Surveys
Eight owl transects were surveyed in 2008, five in the Peace River Corridor (PRC) study area and three in the transmission line (TL) study area (Table 2.3.4.1a; Appendix 5a). Transects were completed during three survey periods: May 5 to May 18, May 26 to June 10, and June 12 to 27, 2008. Total time spent surveying for owls in 2008 was 94.87 hours. Forty-nine owl surveys were completed, 31 in Peace River Corridor and 18 along the related transmission line. Transects were repeated two to three times for each target owl species, except when inclement weather was experienced (transect 6). Species-specific surveys completed include 23 Boreal Owl surveys, 19 Great Gray Owl surveys and 7 Great Horned Owl surveys. No surveys for Great Horned Owl were completed in the TL study area due to lack of habitat for this species, as determined from the draft habitat suitability mapping.
Inclement weather may influence owl behaviour and responsiveness and can adversely influence owl detections (Hausleitner 2006). Surveys should not be completed when wind speeds exceed 19 km/hr or in steady or heavy rain. In 2008, wind speeds exceeding 19 km/hr were recorded on 3 of 6 call-playback stations during one survey on June 22. No owls were detected on this survey.
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Map 2.3.4a. Owl call-playback surveys.
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Map 2.3.4b. Owl call-playback surveys.
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Table 2.3.4.1a. Summary of owl surveys effort completed in 2008.
Study Transect Survey Time Number of Call Number of Repeat Target Species Area Label (hrs:min) Stations Surveys Boreal Owl 6:44 9 3 0* Great Gray Owl 4:00 8 2 Great Horned Owl 5:12 10 2 Boreal Owl 6:12 8-9 3 1* Great Gray Owl 4:02 8 2 Great Horned Owl 4:47 9 2 Boreal Owl 5:46 7-8 3 PRC 5* Great Gray Owl 3:45 7-8 2 Great Horned Owl 4:14 8-9 2 Boreal Owl 4:04 8 2 6* Great Gray Owl 1:44 7 1 Great Horned Owl 2:22 9 1 Boreal Owl 4:56 5-8 3 7 Great Gray Owl 5:36 6-8 3 Boreal Owl 4:39 6-7 3 2 Great Gray Owl 4:47 6-7 3 Boreal Owl 6:19 7-9 3 TL 8 Great Gray Owl 5:01 5-8 3 Boreal Owl 5:26 6-8 3 10 Great Gray Owl 5:16 7 3 Total 94:52 375** 49 *transect was wholly or partially in the potential Site C reservoir; **total for all surveys.
Seventy-eight owl detections were recorded in 2008, with 63 in the PRC study area and 15 in the TL study area (Table 2.3.4.1b; Appendix 5b, 5c). Five species were detected in the PRC study area (Great Gray Owl, Great Horned Owl, Barred Owl, Boreal Owl, and Northern Saw- whet Owl) and three species were detected in the TL study area (Barred Owl, Great Gray Owl and Northern Saw-whet Owl). The Barred Owl was detected the most frequently in the PRC study area and the Northern Saw-whet Owl was detected the most frequently in the TL study area, despite these species not being targeted.
Table 2.3.4.1b. Number of owls detections recorded during call-playback surveys completed in 2008.
Northern Study Transect Barred Boreal Great Gray Great Unknown Saw-whet Total Area Label Owl Owl Owl Horned Owl Owl Owl PRC 0 9 1(1) 1(1) 11 1 15 2(2) 3 20 5 5 1(1) 3(2) 1(1) 1 11 6 4 1(1) 1(0) 6 July 2009 -55-
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Northern Study Transect Barred Boreal Great Gray Great Unknown Saw-whet Total Area Label Owl Owl Owl Horned Owl Owl Owl 7 1 3(3) 6(0) 4 1 15 2 2 n/a 6 8 TL 8 1(1) n/a 1 10 3 n/a 3 6 Total 39 1 9(8) 11(4) 16 2 78 () number of detections occurring during targeted surveys for that species.
The Boreal Owl was detected only once in the PRC study area. The Great Gray Owl was detected in both study areas, but most detections were in the PRC study area. The Great Horned Owl was detected only in the PRC study area, but targeted surveys were not completed for this species in the TL study area due to a lack of suitable habitat. No owl species at risk were recorded. The number of detections recorded is not equivalent to the number of owls present, as the same owl may have been recorded at multiple stations.
Northern Saw-whet Owls, Barred Owls and Great Horned Owls called in response to playbacks of all three target species’ calls (Boreal Owl, Great Gray Owl and Great Horned Owl). The Boreal Owl responded only to calls of its own species. The Great Gray Owl responded primarily to calls of its own species, with eight of the nine detections recorded in response to Great Gray Owls calls.
Response rates declined in June and consequently the survey effort during the final survey period was redirected to search for active nests at sites where a response was detected during a previous survey. Pairs were detected in a number of areas but no nest trees were located. Nocturnal surveys for Boreal Owls were also repeated on each transect to increase the survey effort for this species since it had the lowest response rate.
Incidental Observations
Six owl species were detected incidentally during other species-specific surveys and outside of the standard survey time during owl surveys (Table 2.3.4.1c). Owl observations were recorded during breeding bird surveys, amphibian surveys and opportunistically by field personnel camping within the study area. Owl observations were also recorded incidentally while travelling to or from owl survey transects. One notable observation includes the detection of an additional Boreal Owl in the TL study area.
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Table 2.3.4.1c. Incidental observations of owl species recorded during surveys in 2008.
Species Project Area Date Survey PRC 17-May-08 Owl Barred Owl PRC 22-Jun-08 Breeding Bird TL 18-Jun-08 Owl Boreal Owl TL 10-May-08 Owl PRC 28-May-08 Breeding Bird Great Gray Owl TL 12-Jun-08 Owl PRC 8-May-08 Owl TL 9-May-08 Owl PRC 27-May-08 Camp Great Horned Owl TL 15-Jun-08 Owl PRC 20-Jul-08 Rare Plant PRC 16-Sep-08 Camp PRC 17-Sep-08 Camp PRC 18-Sep-08 Camp PRC 18-Sep-08 Camp Northern Pygmy-owl PRC 26-May-08 Breeding Bird PRC 19-Jun-08 Breeding Bird PRC 21-Jun-08 Breeding Bird Northern Saw-whet Owl TL 9-May-08 Owl TL 10-May-08 Auditory Amphibian
2.3.4.2. Multiple Year Data Analysis
Hawkes et al. (2006) completed nine call-playback surveys between June 13 and July 23, 2005 in the Peace River Corridor (core) and in the surrounding uplands (periphery) (Table 2.3.4.2a). They broadcast calls for Boreal Owls, Barred Owls, Great Gray Owls and Northern Saw-whet Owls at one or more stations. Responses were recorded from one Barred Owl and two Saw- whet Owls (Table 2.3.4.2b). They noted that the timing of their surveys was not optimal and owls would likely be more responsive in the spring. They also reported a single detection of the Northern Pygmy-owl in the river corridor in 2005.
Keystone Wildlife Research Ltd. (2006b) completed owl surveys in the Peace River corridor (PRC) in 2006 (Table 2.3.4.2a). Surveys were completed according to RIC standards (RIC 2001) for Great Horned Owl, Great Gray Owl, Northern Saw-whet Owl, Boreal Owl, and Short- eared Owl. Six species of owls were documented during nocturnal call-playback surveys in April, May and June, 2006. The Northern Saw-whet Owl was detected the most frequently and
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Table 2.3.4.2a. Total owl survey effort for each target species, completed in 2005, 2006 and 2008.
Year Total Number Total Survey Time Target Species Study Area of Stations (hrs:min) Periphery 2005 4 1:00* 2006 Peace River Corridor 140 35:37 Boreal Owl Peace River Corridor 2008 110 27:42 Transmission Line 2008 66 16:24 Boreal Owl Total 320 80:43 Core 2005 5 1:15* Barred Owl Periphery 2005 1 0:15* Barred Owl Total 6 1:30 Barred Owl and Northern Saw- Core 2005 17 4:36* whet Owl Barred Owl and Northern Saw- Periphery 2005 12 4:02* whet Owl Barred Owl and Northern Saw-whet Owl Total 29 8:38 Periphery 2005 2 0:30* Peace River Corridor 2006 141 34:06 Great Gray Owl Peace River Corridor 2008 75 19:07 Transmission Line 2008 60 15:04 Great Gray Owl Total 278 68:47 Northern Saw-whet Owl Peace River Corridor 2006 117 24:50 Northern Saw-whet Owl Total 117 24:50 Peace River Corridor 2006 122 27:57 Great Horned Owl Peace River Corridor 2008 64 16:35 Great Horned Owl Total 186 44:32 Short Eared Owl Peace River Corridor 2006 44 6:58 Short Eared Owl Total 44 6:58 Total for all surveys 980 235:58 *Time is estimated based on an assumed 15 min station.
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Table 2.3.4.2b. Number of owl detections recorded during surveys in 2005, 2006 and 2008, including incidentals.
Peace River Core Periphery Peace River Transmission Species Corridor Total 2005 2005 Corridor 2008 Line 2008 2006 Barred Owl 1 60 36 6 103 Boreal Owl 2 (2) 1 (1) 1 4 Great Gray Owl 3 9 (7) 2 (1) 14 Great Horned Owl 60 (41) 18 (4) 3 81 Long-eared Owl 2 2 Northern Pygmy Owl 1 4 5 Northern Saw-whet 1 2 162 (54) 7 11 183 Owl Short-eared Owl 1 1 Unknown Owl 4 2 6 Total 3 2 294 77 23 399 () number of detections occurring during targeted surveys for that species.
Territory Analysis The number of territories detected during surveys in 2006 and 2008 was estimated for Boreal Owls, Great Gray Owl and Great Horned Owls in the Peace River Corridor (PRC) and transmission line (TL) study areas. The number of Northern Saw-whet and Barred Owls in the study area was considered in terms of provincial density. Data used in this analysis are summarised in Table 2.3.4.2c.
Table 2.3.4.2c. Summary of data from owl surveys in 2006 and 2008 used to determine territories for each species.
Study Number of Total Number of Detections during Species Area Transects Detections Targeted Surveys PRC 8 (6) 3 (2) 3 Boreal Owl TL 3 1 0 PRC 8 (6) 12 (4) 7 Great Gray Owl TL 3 2 1 PRC 7 (6) 78 (33) 45 Great Horned Owl TL 0 3 0 Northern Saw-whet PRC 3 (2) 169 (46) 54 Owl TL 0 11 0 PRC n/a 96 (55) 0 Barred Owl TL n/a 6 0 () transect in potential Site C Reservoir.
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Boreal Owl
There is limited published information available on the home range size of Boreal Owls in BC. The species is not believed to be highly territorial and only defends the vicinity of the nest cavity (Hayward and Verner 1994). Nesting males in Idaho rarely roosted close to the nest and were commonly documented roosting over 1 km away. In contrast, radio-marked females remained within 200 m of the nest tree. Individual nest cavities are not re-used from year to year by breeding pairs (Hayward et al. 1993). In Minnesota, males have been observed vocalizing for mates in late winter and early spring from perches generally located within 100 m from potential nest trees (Belmonte 2005).
Three Boreal Owls were detected during call-playback surveys in the PRC study area. One Boreal Owl was detected incidentally in the TL study area. No Boreal Owls were detected during call-playback surveys for other owl species. The three detections in the PRC study area were separated by at least 20 kilometres. The results indicate that three Boreal Owl territories were in the PRC study, of which two were also in the SRC. One territory was in the TL study area.
Great Gray Owl
Home ranges for male Great Gray Owls have been found to average 450 ha (range 130 to 650 ha) in Oregon (Bull et al. 1998, cited in Ulev 2007), and 19.89 ha and 61.47 ha in California for males and females, respectively (van Riper and van Wagtendonk 2006). In Yosemite National Park in California, the home range size of Great Gray Owls differed significantly between the breeding and non-breeding seasons (van Riper and van Wagtendonk 2006). Great Gray Owls do not display a high degree of intra-specific territoriality and active nest sites have been observed as close as 430 m (Bull and Henjum 1990).
Fourteen Great Grey Owls were detected during surveys, eight of which were detected during targeted surveys for this species. The results indicate that the 14 detections represented 10 separate territories. Eight territories were in the PRC study area, five of which were within the SCR. Two territories were in the TL study.
The number of territories may have been underestimated since the species is known to have a reduced intra-specific territoriality response and can nest in close proximity to conspecifics. In
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Great Horned Owl
The reported density for Great Horned Owls varies in different areas, but is usually about 1 pair per 5 to 20 km 2 (BC CDC 2009). Territorial owls in the Yukon were restricted in their movements and rarely moved more than 3 km between weekly relocations, with defended territories estimated to be 5.26 to 5.56 km 2 (Rohner 1997).
Eighty-one Great Horned Owl detections were recorded during surveys, 45 of which were recorded during targeted surveys for this species. The results indicate that these 81 detections represented 22 separate Great Horned Owl territories. Twenty territories were in the PRC, with 14 in the SCR and 2 in the TL.
Northern Saw-whet Owl
Northern Saw-whet Owls were the most abundant species detected in the study areas. During surveys in 2006 and 2008, 180 detections were recorded, 54 of which were recorded during targeted surveys for this species.
Saw-whets were detected at most stations during call-playback surveys for this species in 2006, although some of the detections were likely the same individual recorded at multiple stations. The distribution of detections was generally uniform along the three survey transects, although tighter clusters were observed (e.g. around Watson Slough). This made it difficult to determine individual territories. The number of detections indicate that Northern Saw-whet Owl densities in the PRC and SCR are approaching an estimated maximum density of 1 pair/km 2 (Cannings 1993). This density is much higher than anticipated for the area, based on other accounts (Campbell et al. 1990).
Barred Owls
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Owl detections (56%) were clumped in a 12-kilometre stretch along transect B in 2006 and transect 1 in 2008 (Map 2.3.4a). Another 14% of the detections were clumped into a 2.5 kilometre linear segment in transect 0 in 2008 (Map 2.3.4a). Only four Barred Owl detections were recorded along the TL during surveys. The remaining detections (43%) were distributed fairly uniformly along the Peace River Corridor.
While detailed surveys were not completed for the species, the incidental records indicate that a healthy population exists within the Peace River study areas.
2.3.5 Summary
Survey results indicate that Boreal Owls are rare in the study area (5 detections in over 80 hours of targeted surveys). Great Gray Owls are also not abundant in the area, but occurrence in the PRC study area was higher than in the TL study area despite a similar level of effort. Targeted surveys were not completed for this species in the TL study area as assessment of the draft suitability habitat indicates that little suitable nesting habitat is available.
Incidental data collected indicate that Great Horned Owls may be more abundant in the PRC study area than in the TL study area, although targeted surveys were not completed for this species in the TL study area. Assessment of the draft habitat suitability maps for the Great Horned Owl indicate that there is little suitable nesting habitat in the TL study area, so owls may use that area for foraging rather than nesting.
2.4 SONGBIRDS
There are a number of provincially-listed passerine species known to occur in the Peace River Corridor. Species associated with riparian habitats may be at risk due to habitat alteration and inundation associated with the potential Site C project. Cumulative loss of mature riparian habitat has increased the value of the remaining habitat in the Peace Region. Additional surveys were required in 2008 to:
• confirm species presence and habitat use;
• determine the use of riparian habitats by listed species;
• determine habitat associations for listed species.
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2.4.1 Introduction
Passerines are defined as birds that have feet specialized for holding onto a horizontal branch (three toes pointing forward and one pointing back). This species group includes thrushes, warblers, vireos, flycatchers, swallows, sparrows, blackbirds, crows, jays, nuthatches, wrens, finches, chickadees, tanagers, orioles, grosbeaks, waxwings, starlings, catbirds, creepers, pipits, weavers, shrikes, kinglets and larks. Non-passerine species including woodpeckers, hummingbirds, kingfishers, nighthawks, doves, swifts and upland gamebirds are also reported in this section. Ten Red- or Blue-listed songbird species are known to occur in the Peace River Corridor (Table 2.4.1a).
Table 2.4.1a. Red- or Blue-listed passerines known to occur in the study area.
CWS COSEWIC SARA Provincial Priority BCCF English Name Scientific Name Status* Schedule Status Region Priority 6** Black-throated Dendroica virens Blue H 2 Green Warbler Wilsonia Canada Warbler T Blue H 2 canadensis Connecticut Oporornis agilis Red M 2 Warbler Bay-breasted Dendroica Red H 2 Warbler castanea Cape May Warbler Dendroica tigrina Red M 2 Rusty Blackbird Euphagus carolinus SC 1 Blue H 2 Barn Swallow Hirundo rustica Blue M 2 Le Conte’s Ammodramus Blue M 4 Sparrow leconteii Nelson’s Sharp- Ammodramus NAR Red H 2 tailed Sparrow nelsoni Olive-sided Contopus cooperi T Blue H 2 Flycatcher *T =Threatened, SC =Special Concern, NAR =Not At Risk; ** H =High, M =Medium.
2.4.2 Background
Songbird data have been collected in the Peace River Valley since the 1970’s. Historical data was collected by Ryder (1975), Thurber (1976), Blood (1979), Enns and Siddle (1996), Bennett and Enns (1996), Campbell et al. (1997), Wright (1997), Phinney (1998), Tera Environmental
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Thurber (1976) completed breeding bird surveys to locate territorial males in May and June 1974, in the Peace River Valley. Three study areas 14.7 – 19.25 ha in size were surveyed by a single observer walking each plot at dawn or dusk for a total of eight days. Sites were located on a floodplain 6.5 miles from the Alberta border, on an island 7.5 miles from the border, and on another island 42.5 miles from the border. Eighty species of passerine were recorded, and 84% of these species were found to breed.
Blood (1979) completed counts of vocalizing territorial male songbirds at three sites in the Peace River Valley in June of 1977. An estimated 17,000 to 30,000 breeding songbirds were expected to occur in the potential Site C reservoir with approximately 300 to 550 breeding territories per km 2.
Hemmera (2006) completed songbird surveys on Bear Mountain, 14.5 km southwest of Dawson Creek. Breeding bird surveys were conducted from May to June according to RIC standards (RIC 1999b). Ninety-nine bird species were detected during these surveys including 6 waterfowl, 6 shorebirds, 12 raptors, 2 game birds, 68 passerines and 6 woodpecker species. Four listed songbird species were recorded during these surveys.
Birds were monitored in TFL 48, in the Dawson TSA, as part of a long-term project designed to determine the presence and relative abundance of bird species within different managed forest habitats (Preston 2008). Seventy-five bird species were recorded during the breeding bird survey, with a yearly total of 118 species. Swainson’s Thrush was the most common bird and 21 of the most common bird species comprised 82% of the bird community.
Phinney (1998) compiled bird-sighting data from the area around Dawson Creek (45 km west; 35 km north; 40 km southwest; and east to the Alberta border) during five field seasons from 1991 to 1995. Listed songbirds recorded included the Barn Swallow, Black-throated Green Warbler, Canada Warbler, Le Conte’s Sparrow, Nelson’s Sharp-tailed Sparrow, Bobolink, Rusty Blackbird, Common Nighthawk, Connecticut Warbler and Olive-sided Flycatcher.
The Mackenzie Bird Banding Station recorded birds seen during fall migration, from mid-July to late September (Lambie 2004, 2005, 2006, 2007, 2008) at Mugaha Marsh (14 km NW of
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Mackenzie). In 2005, a Lakewatch was started along Williston Lake from mid August to late September and this has continued yearly. This lakewatch documents birds on migration (Lambie 2005, 2006, 2007, 2008). Their results are described below by species.
Barn Swallow
The Barn Swallow is a Blue-listed songbird that feeds on the wing on flying insects, often over water bodies or open fields. The first record of Barn Swallows in the Peace Region was in the Toms Lake area in 1947, reported by Phinney (1998), who listed the species as a common migrant and summer visitant . Barn Swallows were next reported from the Peace River area in 1975 (Ryder 1975; Thurber 1976). Nests were found in the Dawson Creek area in 1993 and 1994 (Phinney 1998). The Timberline Trail and Nature Club of Dawson Creek documented a Barn Swallow near the beaver pond on the Clayhurst Ecological Reserve on June 19, 2005 (S. Kinsey, pers. comm. 2008). Ten Barn Swallows were seen flying over Williston Lake on August 30, 2005 (Lambie 2005). Twelve Barn Swallows were seen at Mugaha Marsh on August 7, 2007 (Lambie 2007) and one Barn Swallow was captured and banded at the Mackenzie Nature Observatory in 2008 (Lambie 2008).
Bay-breasted Warbler
Bay-breasted Warblers are found in mature, closed canopy white spruce forest, in pure or mixed stands (aspen, birch and balsam poplar) (Enns and Siddle 1996). In 1975, a Bay-breasted Warbler still in breeding plumage (August) was seen on an island 4 km east of Taylor Bridge (Ryder 1975). From 1981 to 1990, Bay-breasted Warblers were reported at Beatton Provincial Park, on the east side of Charlie Lake, and a nest containing four Bay-breasted Warbler nestlings was found in a spruce tree on July 7, 1983 (BC CDC 2009). One Bay-breasted Warbler was observed during surveys on Bear Mountain (Hemmera 2006). Bennett and Enns (1996) documented 55 Bay-breasted Warblers in the Liard River Valley in 1996, mostly in mature riparian cover along the valley bottom. The first Bay-breasted Warbler was banded at Mackenzie Nature Observatory on August 7, 2008 (Lambie 2008). The number of individuals within the Peace River Corridor is expected to be small since their abundance is linked to spruce budworm outbreaks.
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Black-throated Green Warbler
The first record of Black-throated Green Warbler in British Columbia was a male collected near Chetwynd on June 25, 1965 (Phinney 1998). Thurber (1976) found three male Black-throated Green Warblers during breeding bird surveys in mature poplar and spruce islands along the Peace River in 1974.
Two adults with recently fledged young were seen in Kiskatinaw Park on June 30, 1981 and several more were observed between the Moberly and Pine Rivers in May and June of 1994 (BC CDC 2009). In June 1992, approximately 20 male Black-throated Green Warblers were heard singing in the Peace River Area (BC CDC 2009). Birds have also been heard south of Hudson Hope, around Beatton River, at Boundary Lake, St. John Creek, Stoddart Creek, near Taylor and at Peace Island Park (BC CDC 2009).
One Black-throated Green Warbler was observed in a coniferous forest habitat on a long floodplain island 2.5 km east of Taylor Bridge in 1999 (Robertson and Hawkes 2000). In 2006, 64 Black-throated Green Warblers were recorded during breeding bird surveys on Bear Mountain (Hemmera 2006). They were found to prefer mature and old growth mixed forests (Hemmera 2006). Phinney (2003) tested habitat preferences of 262 Black-throated Green Warbler locations collected over 14 years in the Dawson Creek area and found that statistically they were more likely to be found away from riparian areas. Preston (2008) documented ten Black-throated Green Warblers during breeding bird surveys in TFL 48 in 2007.
Canada Warbler
Canada Warblers are generally found along steep slopes with unstable banks and an abundance of shrubby undergrowth (Enns and Siddle 1996; Campbell et al. 2001). Sites can be wet or dry, but most slopes in the Peace area are associated with streams and rivers (Enns and Siddle 1996).
One Canada Warbler was seen near the mouth of the Halfway River during reconnaissance surveys for the Birds of BC Project in 1975 (Ryder 1975). Between June 19 and July 21, 1992, Canada Warblers were recorded near Taylor, along Peace Island Parkway, along the Peace River close to Farrell Creek and along the Beatton River (BC CDC 2009). On July 21, 1992, several adults were seen feeding juveniles along the Peace River, east and southwest of Farrell
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Creek (BC CDC 2009). Two males were also heard singing in the Peace River bottomlands, 5.5 km south of Clayhurst on June 28, 1992 (BC CDC 2009).
One Canada Warbler was reported at Hines Creek and South Road on the Peace River in Alberta (Tera Environmental and Troughton 2000). Hemmera (2006) recorded 27 Canada Warblers during breeding bird surveys on Bear Mountain in 2006. During a bird inventory in the Liard River Valley, 23 Canada Warblers were observed and most were found in mixed and deciduous aspen stands with an understorey of prickly rose ( Rosa acicularis ), high-bush cranberry ( Viburnum edule ) and alders ( Alnus sp.) (Bennett and Enns 1996). The first Canada Warbler for the area was banded at Mugaha Marsh in 2004 (Lambie 2004). Five Canada Warblers were detected during 2007 breeding bird surveys in TFL 48 (Preston 2008).
Cape May Warbler
Cape May Warblers are found in mature, closed canopy white spruce forest, in either pure or mixed stands (aspen, birch, and balsam poplar) (Enns and Siddle 1996). During a bird inventory along the Liard River, 21 Cape May Warblers were found mostly in coniferous upslope habitat (Bennett and Enns 1996). One singing male was heard in Beatton Provincial Park on June 1992 in an open white spruce forest near a large lake (BC CDC 2009).
Common Nighthawk
The Common nighthawk can be found foraging in any open or semi-open habitat with abundant flying insects (Campbell et al . 2006). Nesting occurs in a diverse array of habitats including open, mixed and pure forested habitats and grasslands on hillsides (Campbell et al . 2006). Thurber (1976) reported the Common Nighthawk as a common summer breeder throughout the Peace River valley. Common Nighthawks were heard throughout the banding season at Mugaha Marsh in 2008 (Lambie 2008).
Connecticut Warbler
Connecticut Warblers are associated with mature and old growth, deciduous-dominated forests with rich understories. They have been documented in both pure deciduous and mixed-wood stands, but they are most common in pure aspen stands. Ryder (1975) observed a Connecticut Warbler near the mouth of Halfway River in 1975. One Connecticut Warbler was observed in
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June 1974 on a mixed balsam poplar and white spruce island, 67 km west of the Alberta border and two were observed on a floodplain dominated by balsam poplar, 10 km west of the Alberta border (Thurber 1976). On July 22, 1992, one juvenile was seen along the Kiskatinaw River, 4 km north of Sunrise Valley (BC CDC 2009). Phinney (1998) recorded the early arrival date for Connecticut Warbler in the Peace Region as May 22 in 1994. In June 1994, two Connecticut Warblers were observed in a mature aspen stand south of the Moberly River (BC CDC 2009). Five Connecticut Warblers were found in aspen forests on Bear Mountain in 2006 (Hemmera 2006).
LeConte’s Sparrow
LeConte’s Sparrows are found in open, level uplands and lowlands, with tall, thick herbaceous vegetation and thick litter. Penner (1976) lists LeConte’s Sparrow as rare in the Peace River valley. Thurber (1976) recorded a LeConte’s Sparrow approximately 8 km west of the Alberta border on the Peace River, on June 2, 1974. One male was heard singing July 3, 1978, at the north end of Cecil Lake (BC CDC 2009). Phinney (1998) reported that LeConte’s Sparrow arrived in the Dawson Creek area on May 15, 1991. Between June 9 and July 20, 1992, several sightings of singing males, one pair and an adult carrying food were recorded at McQueen Slough (BC CDC 2009). One male was heard singing in a sedge slough at Valley View June 16, 1993 (BC CDC 2009). Surveys in the Peace River study area in 2006 recorded 13 detections (S. Kinsey, pers. comm. 2008).
Nelsons’ Sharp-tailed Sparrow
Nelson’s Sharp-tailed Sparrow is a small passerine that feeds on invertebrates and is found in freshwater wetlands with dense, emergent vegetation, or damp areas with dense grasses. Nelson’s Sharp-tailed Sparrow has a small and localized breeding distribution, restricted to the Peace Lowlands and Kiskatinaw Plateau. Campbell et al. (2001) reports only two nesting records, one at Boundary Lake east of Fort St. John and the other at the south end of Swan Lake. No nesting has been recorded in the project area but nesting was suspected at Charlie Lake in 1938 (Campbell et al. 2001).
One breeding pair was found in a sedge meadow at McQueen’s Slough on June 24, 1992 and a bird was heard singing there on July 4 and 6, 1995 (Phinney 1998). Phinney (1998) also
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Olive-sided Flycatcher
The Olive-sided Flycatcher is found in a variety of habitats. The species winters in central and South America and breeds across most of forested BC (Campbell et al. 1997). Recent declines in numbers across the species’ range have prompted it’s listing as a species of conservation concern in a number of jurisdictions (Wright 1997), although the reasons for its decline are currently unknown (Campbell et al. 1997). The Olive-sided Flycatcher breeds in diverse habitats including old-growth forest, young second-growth forest, in burns and recent cutblocks (as long as snags and stubs remain) (Campbell et al. 1997) and open forest and woodland with a mixture of wetlands, meadows, ponds and streams (Wright 1997). The presence of tall, mature trees to use as perch sites for flycatching is also considered an important habitat component (Campbell et al. 1997).
Olive-sided Flycatchers were observed on May 9, 1974 and in 1975 in the Peace River (Thurber 1976; Ryder 1975). One Olive-sided Flycatcher that was suspected to be breeding was observed in the Peace River valley near the proposed Dunvegan Hydroelectric Project in 2000 (Tera Environmental and Troughton 2000). An Olive-sided Flycatcher was seen on August 7, 2007 at Mackenzie Nature Observatory (Lambie 2007). On August 11, 2008, one hatch-year bird was caught and banded at the Mackenzie Nature Observatory (Lambie 2008). Seven Olive-sided Flycatchers were observed during 2007 breeding bird surveys in TFL 48 (Preston 2008).
Rusty Blackbird
The Rusty Blackbird breeds mainly in wooded wetlands in boreal forests. Ryder (1975) observed a Rusty Blackbird in 1975 in the Peace River Valley. One nest was found in the Dawson Creek area on May 17, 1992 (Phinney 1998). At Mugaha Marsh, 32 blackbirds were seen on September 18, 2004 (Lambie 2004) and 26 were seen in September 2005 (Lambie 2005). Thirteen were seen on August 6, 2006, at the Mackenzie Nature Observatory (Lambie
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2006). In 2007, 28 were seen in late August at Mugaha Marsh and 29 were reported on September 20 at Williston Lake (Lambie 2007). One Rusty Blackbird was detected during 2007 breeding bird surveys in TFL 48 (Preston 2008).
Grouse
In April and May of 1975, grouse surveys were conducted to locate drumming males in the Peace River valley (Thurber 1976). Ruffed Grouse were common in mixed and deciduous forest and tall shrub communities. Spruce Grouse were not observed. Sharp-tailed Grouse were not found in the river valley but were observed on the river breaks and uplands adjacent to south-facing slopes of the Peace River. They may over-winter on the south-facing slopes along the Peace River.
Blood (1979) surveyed grouse in the Peace River in 1977 and estimated populations of Ruffed Grouse in the potential Site C reservoir to be 1000 in the spring and 3000 in the fall. They estimated seven grouse per km 2 in the Site C area and determined that Spruce Grouse and Sharp-tailed Grouse also occur in the general area, but are rare in the Peace River Valley.
2.4.3 Methods
Inventory methods used in 2008 followed the BC Resource Inventory Standards Committee’s (RISC) Inventory Methods for Forest and Grassland Songbirds (RIC 1999b). Listed species were targeted for surveys.
Draft habitat suitability mapping for target species was completed according to British Columbia Wildlife Habitat Ratings Standards (RIC 1999a).
2.4.3.1. Inventory Methods
Breeding bird surveys were completed in the PRC and TL study areas. Draft habitat suitability maps and existing biophysical habitat maps were used to identify suitable habitat for the Black- throated Green Warbler, Canada Warbler, Connecticut Warbler, Bay-breasted Warbler, Cape May Warbler, Barn Swallow, Nelson’s Sharp-tailed Sparrow, LeConte’s Sparrow, and Rusty Blackbird. Survey transects were selected based on presence of suitable habitat for priority bird species, accessibility, and location in the study area. Some transects completed in 2006 were also repeated (Keystone Wildlife Research 2006b). Each breeding bird transect was visited up
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Surveys occurred in the morning, in the first 4 hours after sunrise when birds are the most active. At each station, surveyors listened for 5 minutes and all bird species identified by sight or sound were recorded. Inclement weather conditions (e.g. rain, strong wind) affect the number of birds calling and the ability of surveyors to detect them. If these conditions were experienced during a survey, not all point count stations may have been completed. If unsuitable conditions persisted, then the entire transect may not have been completed.
A handheld GPS, survey map and compass were used to determine the geographical location (UTM co-ordinates) of each point count station and the direction to the observed species. All observations were recorded on standard RISC datasheets customized for the project. Information collected at each point count station included UTM location (NAD 83), bird species observed, habitat attributes (subzone, site unit, structural stage) and the map polygon number. Specific information recorded at the start and end of each transect included: start and stop time and weather conditions (temperature, wind speed, cloud cover and precipitation). Birds heard while travelling between point count stations were also recorded, if those species had not been detected during the previous point count station. If a Red- or Blue-listed species was detected, the exact location of the bird was determined and the habitat type at the bird’s location was recorded.
Nelson’s Sharp-tailed Sparrow, American Bittern and Yellow Rail are difficult to survey using standard point-count methodology. Surveys for these species took place in suitable habitat shortly after sunset. Surveyors listened for free-calling sparrows at suitable wetlands. Call playbacks were completed for American Bittern and Yellow Rail in apparently suitable wetlands.
Any significant incidental bird observations made while travelling to and from transects were also recorded. Locations, descriptions and photographs (if possible) of any nests found were noted.
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2.4.3.2. Habitat Suitability Mapping
Draft species models and habitat suitability ratings have been prepared for Black-throated Green Warbler, Canada Warbler, Connecticut Warbler, Bay-breasted Warbler, Cape May Warbler, Barn Swallow, Nelson’s Sharp-tailed Sparrow, LeConte’s Sparrow and Rusty Blackbird (Keystone Wildlife Research Ltd. 2008b). The life requisite rated was Reproducing-Eggs for all species. Rural and Urban habitat was rated up to Moderate for Barn Swallow. Non-forested wetlands were rated up to High for LeConte’s Sparrow and Nelson’s Sharp-tailed Sparrow breeding habitat. Wetlands and black spruce bogs were rated up to Moderate for breeding habitat for Rusty Blackbird. Mesic to moist mature and old coniferous forests were rated up to Moderate for Bay-breasted Warbler. Old and mature spruce forests were rated up to High for Black-throated Green Warbler breeding habitat. Mesic and wetter mature and old coniferous and seral forests were rated up to High for Canada Warbler. Mesic and drier forests dominated by aspen, in structural stages 5 and 6, are rated up to High for Connecticut Warbler. The highest-rated habitats for Cape May Warbler were mature and old, moist to wet coniferous forests, which were rated up to High. A species model has not been completed for the Olive- sided Flycatcher, which was added to the province’s Blue list in 2008.
2.4.3.3. Analysis
Species Accumulation
Analysis to determine rate of avian species accumulation was completed using the point count data from 2006 and 2008. Data from 2005 were not available for inclusion in this analysis. The rate at which new species were encountered was compared with the number of point counts conducted to create a species accumulation curve for the PRC and TL study areas, and for point counts completed within the potential Site C reservoir. This analysis was completed to determine if there has been adequate survey effort to detect most of the passerine species present in the study areas. The assumptions of the analysis include:
• each point count is assumed to be independent, including replicates between point count stations and between years; • surveyors were knowledgeable of all species occurring in the area; • number of species detected on all point counts represent the total number of detectable species.
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Determination of species accumulation does not include incidental observations or time spent travelling between stations. The total survey time is the time taken to complete a transect (start time to stop time) whereas the total survey effort (as used in this analysis) is the time spent at each point count station. The total survey effort was calculated by multiplying the number of point count stations by 5 minutes and assumes that the survey time at each point count station was 5 minutes. Only species recorded at point count stations were considered and all species groups were included (passerines, raptors, waterfowl).
Species Diversity
The results of songbird surveys completed in 2006 and 2008 were analyzed to determine the diversity of this species group within the PRC and TL study areas and within the potential Site C reservoir. The Simpson Reciprocal Index and the Shannon-Weiner Index were used to analyze diversity (Krebs 1998). The Simpson and Shannon-Weiner indices are measures of diversity that take into account how common individual species are within an area, where higher values indicate higher diversity.
The Simpson Reciprocal Index is a measure of species diversity and is weighted towards the common species in an area. This Index increases as species diversity increases, but minimal change occurs when new, rare species are added. The Shannon-Weiner Index increases as both richness and evenness ( i.e., how common species are, relative to others) increase.
The two diversity indices were analyzed using Kruskal-Wallis tests, followed by a Mann-Whitney test to analyze any differences in diversity between the two study areas and the potential Site C reservoir (Zar 1999). These tests are non-parametric statistical tests for comparing groups of data to determine if they differ.
2.4.4 Results
Results of 2008 surveys and a compilation of data from surveys completed between 2005 and 2008 are reported below. Data from previous surveys were included when available from original databases or reports. The locations of songbird surveys completed in 2005, 2006 and 2008 are shown on Maps 2.4.4a and 2.4.4b.
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2.4.4.1. 2008 Inventory Surveys
Twenty breeding bird transects were established in the study area, 15 in the Peace River Corridor (PRC) study area and 5 in the transmission line (TL) study area. Transects were completed during three survey periods (May 22 to June 1, June 2 to June 12, and June 19 to 28, 2008).
Fifteen bird transects were completed in the PRC study area in 2008, with nine wholly or partially within the potential Site C reservoir area. Poor weather conditions prevented four replicates from being completed for Transects B, C, X and N. In 2008, 41 songbird surveys were completed, with 9 to 18 point counts stations completed per transect. The total survey effort in the PRC study area was 172.45 hours to complete 588 point count stations (Table 2.4.4.1a, Appendix 6a).
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Map 2.4.4a. Songbird survey locations.
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Map 2.4.4b. Songbird survey locations.
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Table 2.4.4.1a. Summary of breeding bird survey effort in the PRC study area in 2008.
Average Number of Total Survey Time Transect Label Point Count Stations Number of Replicates (hrs:min) per survey 12 13:29 18 3 13 10:43 18 3 A* 13:32 10 3 B 10:21 16 2+ C* 9:17 16 2+ E* 12:41 13 3 F* 11:46 13 3 G* 11:53 15 3 H* 13:49 15 3 J* 11:48 15 3 K* 13:44 13 3 L* 12:49 13 3 N 10:00 14 2+ Q 9:50 14 3 X 6:45 10 2+ Total 172:27 588** 41 *transect was wholly or partially in the potential Site C reservoir; **Total of all surveys completed; +One replicate was not completed due to poor weather.
Five transects were completed in the TL study area, resulting in 14 songbird surveys with 10 to 17 point count stations per transect. Inclement weather conditions resulted in only two replicates for transect 11. The total survey effort in the TL study area was 51.2 hours to complete 195 point count stations (Table 2.4.4.1b, Appendix 6b).
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Table 2.4.4.1b. Summary of breeding bird survey effort in the TL study area in 2008.
Average Number of Transect Label Survey Time (hrs:min) Number of Replicates Stations 8 10:24 13 3 9 10:15 14 3 10 11:55 14 3 11 9:05 17 2* 14 9:33 12 3 Total Effort 51:12 195** 14 *One replicate was not completed due to poor weather; **Total of all stations completed.
During surveys in 2008, 90 songbird species were detected in the PRC study area and 59 species were detected in the TL study area (Appendix 6c). Incidental observations accounted for an additional 14 species in the PRC study area and 16 in the TL study area. Two species (Palm Warbler and the Red Crossbill) were only detected in the TL study area and 31 species were only detected in the PRC study area. In total, 106 different species were detected in 2008 in 223.65 survey hours at 783 point count stations.
Red- or Blue-listed songbirds detected during breeding bird surveys in the PRC study area include Bay-breasted Warbler, Black-throated Green Warbler, Canada Warbler, Connecticut Warbler, LeConte’s Sparrow, Olive-sided Flycatcher and Rusty Blackbird (Table 2.4.4.1c). The Black-throated Green Warbler was detected the most frequently with 188 detections on 12 of the 15 transects in the PRC study area. Two LeConte’s Sparrows and 3 Rusty Blackbirds were detected on only one transect and 10 Olive-sided Flycatchers were detected on two transects. Cape May Warblers were not detected. The number of detections recorded does not equal the number of individuals present in the study areas since counts of individuals may have been duplicated on repeat visits to point count stations.
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Table 2.4.4.1c. Number of Red- or Blue-listed songbirds detections during point count surveys completed in the PRC study area in 2008.
Black- Bay- Olive- Transect throated Canada Connecticut LeConte’s Rusty Total breasted sided Label Green Warbler Warbler Sparrow Blackbird Detections* Warbler Flycatcher Warbler 12 1 3 3 7 13 2 2 4 A 9 3 12 B 1 4 5 C 6 11 17 E 1 25 9 1 8 44 F 35 11 46 G 1 3 4 H 1 33 7 41 J 2 2 K 24 30 5 59 L 20 25 45 N 1 20 21 Q 7 8 15 X 1 5 8 14 Total 5 188 105 23 2 10 3 336 *note that number of detections is not equivalent to number of birds.
Red- or Blue-listed songbird detections during breeding bird surveys in the TL study area include Black-throated Green Warbler, Connecticut Warbler, LeConte’s Sparrow, Olive-sided Flycatcher and Rusty Blackbird (Table 2.4.4.1d). The Black-throated Green Warbler was recorded the most frequently, with 26 detections on all 5 transects in the TL study area. Two Connecticut Warbler observations and one LeConte’s Sparrow were recorded on one transect, and two Olive-sided Flycatcher and five Rusty Blackbird detections were recorded on two transects. Bay-breasted Warblers, Cape May Warblers and Canada Warblers were not detected in the TL study area. Habitat use for listed species is discussed in section 2.4.4.2.
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Table 2.4.4.1d. Number of Red- or Blue-listed songbird detections during point count surveys completed in the TL study area in 2008.
Black- Transect throated Connecticut LeConte’s Olive-sided Rusty Total Label Green Warbler Sparrow Flycatcher Blackbird Detections* Warbler 8 3 1 2 6 9 4 2 1 7 10 11 11 11 4 4 14 4 1 4 9 Total 26 2 1 2 6 37 *note that number of detections is not equivalent to number of birds.
Bay-breasted Warbler, Connecticut Warbler, LeConte’s Sparrow, Olive-sided Flycatcher and Rusty Blackbird were recorded present on less than 5% of the point count stations in either the PRC (224) or TL (79) study area (Table 2.4.4.1e). Black-throated Green Warblers were observed on approximately a third of the point count stations in the PRC study area, but were recorded on less than one quarter of the point count stations in the TL study area. Connecticut Warblers were also detected on more stations in the PRC compared to the TL study area, and Canada Warblers and Bay-breasted Warblers were only detected in the PRC study area.
Table 2.4.4.1e. Percentage of point count stations visited in 2008 at which Red- or Blue-listed species were detected (does not include incidental detections).
Number of point count % of point count stations at Study Species stations at which species was which the species was Area detected* detected Bay-breasted Warbler PRC 3 1.3 Black-throated Green PRC 69 30.1 Warbler TL 16 20.3 Canada Warbler PRC 38 17.0 PRC 15 6.7 Connecticut Warbler TL 2 2.5 PRC 1 0.4 LeConte’s Sparrow TL 1 1.3 PRC 6 2.7 Olive-sided Flycatcher TL 2 2.5 PRC 5 2.2 Rusty Blackbird TL 2 2.5
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Call-playback surveys for American Bittern and Yellow Rail were completed in May and early June, 2008. Surveys were completed at four apparently suitable wetlands as determined from the draft habitat suitability maps for these species. Surveys were repeated one to two times at each site (Table 2.4.4.1f). No bitterns or Yellow Rails were detected.
Table 2.4.4.1f. Summary of wetland surveys for Yellow Rail and American Bittern completed in the TL study area in 2008.
Wetland Date Yellow Rail Detections American Bittern Detections TC1a 10-May-08 0 0 TC10 11-May-08 0 0 TC20 11-May-08 0 0 TC9 19-May-08 0 0 TC20 19-May-08 0 0 TC9 02-Jun-08 0 0
Incidental Observations
Significant incidental observations of passerine birds in 2008 included Barn Swallow, Bay- breasted Warbler, Black-throated Green Warbler, Canada Warbler, LeConte’s Sparrow and Olive-sided Flycatcher in the PRC study area, and Black-throated Green Warbler, Connecticut Warbler, LeConte’s Sparrow, Rusty Blackbird and Olive-sided Flycatcher in the TL study area. A list of all passerine and upland game bird species detected during surveys in 2008 is presented in Appendix 6c.
2.4.4.2. Multiple Year Data Analysis
Hawkes et al. (2006) completed point count surveys for songbirds in the Peace River Corridor (Core) and the surrounding uplands (Periphery) (Table 2.4.4.2a). In total, 4,580 observations of 114 species of passerines, owls, raptors, waterfowl and water-associated birds were recorded. Four Red- or Blue-listed songbirds were detected in the Peace River Corridor including the Black-throated Green Warbler, Canada Warbler, Connecticut Warbler and Olive-sided Flycatcher. In addition to these species, the Red-listed Cape May Warbler and the Blue-listed Rusty Blackbird were detected in the Periphery.
Keystone Wildlife Research Ltd. (2006b) completed 17 point count transects in 2006 in the Peace River Corridor (PRC) (Table 2.4.4.2a). In total, 6,371 bird observations were recorded
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In three years, over 1459 point count station surveys totalling 376 hours of survey time have been completed in the Peace River Corridor (Table 2.4.4.2a). An additional 473 point count station surveys and over 74 hours of survey time have been completed in the periphery and along the transmission line. This effort has resulted in the detection of 116 passerine and upland game bird species (Appendix 6c).
Table 2.4.4.2a. Total breeding bird survey effort completed in 2005, 2006 and 2008.
Total Number Number of of Point Count Total Survey Songbird Survey Station Number of Time Species Study Area Year Period Surveys Replicates (hrs:min)* Detected Periphery June 4 to 277 1-6 23:10** 72 2005 Core July 10 393 (52) 1-6 32:45** 73 April 23 to Peace River 2006 478 (185) 2 170:53 77 June 27 Corridor 588 (174) 3 172:15 90 May 22 to Transmission 2008 June 28 195 3 51:08 59 Line Total 1931 (411) 1-6 450:10 116 + () number of point count surveys in the Site C Reservoir; *Total survey time is the time from the start to the end of the each transect (includes travel time between point count stations); **Time is estimated assuming that all stations were surveyed for 5-minute intervals; +Total of all species detected during all surveys.
Species Accumulation
In total, 130 bird species (passerine, raptors and waterfowl) were detected during point count surveys in the PRC study area in 2006 and 2008. A total survey effort of 88.8 hours was calculated for 1066 point counts, resulting in a detection rate of 0.12 species per point count. The initial rapid rate at which new species were detected (0.83 species / point count) declined after 115 point counts (Figure 2.4.4.2a). A slight increase occurred at the start of 2008, with the detection of some late migrants and rare breeders. Ninety two percent of all species recorded within the PRC were detected in 506 point counts (0.24 species / point count). An asymptote was reached at this level, with only 10 additional species detected in the remaining 560 point
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140
120
100
80
60
Number of Species of Number 40
20
0 0 200 400 600 800 1000 1200 Number of Point Counts
Figure 2.4.4.2a. Bird species accumulation curve for all point counts conducted in the Peace River Corridor.
Of the 1066 point count stations completed in the PCR study area, 359 were within the potential Site C reservoir. In total, 116 species were detected in 29.9 hours of total survey effort, resulting in a detection rate of 0.32 species per point count. A higher initial rate of species accumulation (1.72 species / point count) was observed in the SCR compared to the PRC study area. Species detection reached an asymptote at 204 point counts (Figure 2.4.4.2b) with 97% of the total species being detected. Only 4 additional species were detected in the remaining 155 point counts (0.03 species / point count). Surveying effort detected the majority of species by the end of the 2006 field season and migrants and rare breeders represented the additional species detected in 2008.
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140
120
100
80
60
Number of Species 40
20
0 0 50 100 150 200 250 300 350 400 Number of Point Counts
Figure 2.4.4.2b. Bird species accumulation curve for point counts conducted in the potential Site C reservoir.
In total, 79 bird species (passerine, raptors and waterfowl) were detected during point count surveys in the TL study area in 2008. A total survey effort of 16.25 hours was calculated for 195 point counts, resulting in 0.41 species per point count. Fewer species were detected with lower rates of detection (species/point count) in the TL study area compared to the PRC study area. The rate of accumulation did not reach an asymptote at the end of the 2008 field season, indicating that not all species were detected in the TL study area (Figure 2.4.4.2c). When compared to the rate of accumulation in the PRC, a species detection rate of 0.41 species per point count represents detection of 82% of the species present in the study area. This analysis indicates that an additional 250 point counts are required to detect 90% of the species in the TL study area.
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90
80
70
60
50
40
30 NumberofSpecies
20
10
0 0 50 100 150 200 250 Number of Point Counts
Figure 2.4.4.2c. Bird species accumulation curve for point counts conducted along the transmission line.
The difference in the overall number of species detected and the rate of detection reflects the different bird communities present in the study areas. The riparian bird community present in the PRC (and SCR) study area has greater equitability and diversity of species than the surrounding upland forest (Kinley and Newhouse 1997) resulting in more species detected per unit effort.
Habitat Use by Red- or Blue-listed Species
TEM habitat units were recorded at the location of each Red- or Blue-listed songbird detected during surveys in 2006 and 2008 (Table 2.4.4.2b). The Black-throated Green Warbler and the Canada Warbler were observed in sufficient numbers during point counts to support more detailed habitat use analyses in the PRC study area. The low number of detections precluded similar analysis of the other listed speces. The assumptions of this analysis include:
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results can not be extrapolated to estimate populations since the numbers of bird detections is not equivalent to numbers of individual birds.
• habitat data recorded in the field at each point count and at bird detection locations are assumed to be correct.
Table 2.4.4.2b. Number of Red- or Blue-listed songbird detections in each TEM habitat unit surveyed in 2006 and 2008.
Black- Bay- throated Canada Connecticut LeConte’s Olive-sided Rusty Map breasted Green Warbler Warbler Sparrow Flycatcher Blackbird Total* Unit Warbler Warbler PRC PRC TL PRC PRC TL PRC TL PRC TL PRC TL AM 3 100 3 35 2 4 147 LL 1 1 SW 18 5 5 3 31 BL 1 1 SO 1 79 1 39 2 1 123 SC 11 5 16 SH 49 13 1 63 BT 1 1 2 Fm02 6 1 7 TS 1 2 3 AM:ap 68 7 87 14 2 3 4 185 AMk:a 1 1 p SW:as 1 2 1 4 SC:ab 7 2 5 14 SC:ep 5 19 1 25 SH:ac 38 5 5 1 4 53 SH:ep 3 1 8 12 CF 1 2 3 SE 2 2 WH 2 3 5 WS 1 1 1 3 WW 2 1 3 Total 4 392 25 225 20 2 2 3 19 2 7 3 704 *note that number of detections does not indicate number of birds, but indicates an observation of a bird using that particular habitat.
Black-throated Green Warblers were detected the most frequently in non-seral habitats (Figure 2.4.4.2d) and in older forests (Figure 2.4.4.2e). The low numbers of samples (point counts) in some habitats prevented statistical analysis to determine the significance of these results, but
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45.0
40.0 % of point counts
-nonforested sites not shown 35.0 % of total Black-throated Green Warblers counted -incidental data not included
30.0
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20.0 percenttotal of 15.0
10.0
5.0
0.0
p k p c 3 01 02 0 04 05 06 07 08 09 2:a :ab 01:a 05 05:e 07:a $ $0 $03:as $ $ $ $07:ep Map unit Figure 2.4.4.2d. Black-throated Green Warbler detections in the PRC (2006, 2008) in relation to map unit (Appendix 3a).
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70.0 % point counts
% of Black-throated Green Warblers counted 60.0
50.0 -incidental data not included
40.0 %
30.0
20.0
10.0
0.0 1 2 3 4 5 6 7 structural stage Figure 2.4.4.2e. Black-throated Green Warbler detections in the PRC (2006, 2008) in relation to structural stage (Appendix 3b).
Canada Warblers were recorded in both seral and nonseral habitats within the PRC study area (Figure 2.4.4.2f). This species was detected the most frequently in seral associations containing birch (:ep map units), although these ecosystems were undersampled due to their relative rarity in the study area. A study in the aspen forests of Alberta found that Canada Warbler abundance was positively correlated with the presence of birch (Schieck and Nietfield 1995). Canada Warblers used a variety of structural stages in the Peace River Corridor, and were most frequently detected in mature forests (Figure 2.4.4.2g).
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45.0
% of point counts 40.0 % of Canada Warblers counted -does not include incidental detections 35.0
30.0
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k s p c 1 2 5 8 :a :a :e :a 0 0 03 04 0 06 07 0 09 2 3 7 7:ep 0 0 05 0 0 $01:ap $ $ $05:ab $ $ $ Map Unit
Figure 2.4.4.2f. Canada Warbler detections in the PRC (2006, 2008) in relation to map unit (Appendix 3a).
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60.0
% point counts % of Canada Warblers counted 50.0
40.0
30.0 percent
20.0
10.0
0.0 1 2 3 4 5 6 7 structural stage Figure 2.4.4.2g. Canada Warbler detections in the PRC (2006, 2008) in relation to structural stage (Appendix 3b).
Species Diversity
In total, 136 bird species (passerines, raptors and waterfowl) were observed, with 130 species in the PRC study area, 116 species in the SCR, and 79 species in the TL study area.
Statistical analysis of the Simpson and Shannon-Weiner diversity indices revealed that both the PRC and the SCR study areas had higher bird species diversity compared to the TL study area (p<0.05 for both; Table 2.4.4.2c).
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Table 2.4.4.2c. Bird diversity values for each study area.
Diversity Measure Study Area Number of Samples Mean Median Standard Dev. PRC 1066 29.4 29.5 0.460 Simpson Reciprocal SCR 359 32.4 34.4 5.535 TL 195 27.0 28.0 2.835 PRC 1066 3.8 3.8 0.098 Shannon-Weiner SCR 359 3.8 3.9 0.301 TL 195 3.5 3.6 0.196
The potential Site C reservoir had the highest values for both the Simpson Reciprocal and Shannon-Weiner indices, indicating that it has higher bird species diversity and has more occurrences of rare species, compared to the TL or PRC study areas. Review of the habitat types sampled in 2006 and 2008 indicates that proportionally more non-forested habitats were sampled in the SCR (Table 2.4.4.2d). This is thought to contribute to the higher diversity recorded in the SCR since non-forested habitats support different bird communities than forested sites and therefore add to the bird diversity in an area.
Table 2.4.4.2d. Number of songbird point count survey stations in each TEM habitat type surveyed in 2006 and 2008.
Site Series Forested PRC SCR TL AM Forested 121 32 10 AM:ap Forested 394 108 55 AS Forested 9 1 0 BL Forested 1 0 9 BT Forested 1 1 29 CF Non-forested 11 0 0 Fm02 Forested 25 4 0 GB Non-forested 1 1 0 LL Forested 5 1 2 LL:ak Forested 1 0 1 RZ Non-forested 2 0 0 SC Forested 10 3 0 SC:ab Forested 21 6 8 SC:ep Forested 11 3 2 SE Non-forested 10 10 10 SH Forested 63 37 14 SH:ac Forested 131 56 13 SH:ep Forested 5 5 2
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Site Series Forested PRC SCR TL SO Forested 64 32 4 SW Forested 42 11 15 SW:as Forested 6 0 3 TS Forested 6 6 13 WH Non-forested 26 14 0 WS Non-forested 2 2 2 WW Non-forested 7 1 0 Total Number of Forested 911 306 180 Sites Sampled Total Number of Non-forested 59 28 12 Sites Sampled Total Number of Unclassified 96 25 3 Sites
2.4.5 Summary
Analysis of the results indicate that the Peace River Corridor has higher species diversity than the Transmission line, although this result may be confounded by the lower survey effort in the TL study area. Comparison of the number of point counts surveyed in forested and non- forested habitats also indicates that non-forested habitats were undersampled in proportion to their availability, due to the surveys being targeted primarily at the forest-dwelling rare warblers. This may account for the low detection rate of some species that prefer non-forested habitats (wetlands). Where habitat associations could be confirmed for rare species they were consistent with those previously reported.
2.5 BUTTERFLIES
Few invertebrate species in northeastern BC have been sufficiently studied for accurate population trends to be determined and species at risk to be identified. Butterflies are strongly associated with specific vegetation and often have restricted local distributions. These aspects of their life history make them particularly vulnerable to disturbance. Surveys in 2008 were required to:
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• determine habitat associations for listed species.
2.5.1 Introduction
Butterflies are four-winged insects within the order Lepidoptera. Butterflies go through four life stages: egg, larva, pupa, and adult. Eggs are laid by adults onto food plants, with some species requiring a particular plant species as a host, while others use a variety of plant host species. The eggs hatch into caterpillars (larvae), which feed on the food plant. Full-grown caterpillars leave their food plant to search for a protected place to pupate. During the pupa stage, the tissues of the insect’s body are broken down and re-organized into its adult winged form. The metamorphosis is complete when the adult butterfly breaks out of its pupa. It is capable of flight within a few hours, as soon as its wings have dried and stiffened. Adult butterflies feed on nectar, sap, overripe fruit and other liquids.
There are 19 Red- or Blue-listed butterfly taxa potentially present in the Peace River corridor (Table 2.5.1a). Surveys were conducted to determine habitat relationships, distribution and abundance for these target species.
Table 2.5.1a. Rare butterflies potentially present in the Peace River study area.
Provincial BCCF English Name Scientific Name Status priority Alberta Arctic Oeneis alberta Red 3 Assiniboine Skipper Hesperia assiniboia Red 3 Coral Hairstreak, titus ssp. Satyrium titus titus Red 3 Great Spangled Fritillary, Speyeria cybele 3 pseudocarpenteri ssp. pseudocarpenteri Red Old-world Swallowtail, hudsonianus ssp. Papilio machaon hudsonianus Red 2 Striped Hairstreak Satyrium liparops Red 3 Aphrodite Fritillary, manitoba ssp. Speyeria aphrodite manitoba Blue 4 Arctic Blue, lacustris ssp. Plebejus glandon lacustris Blue 4 Carterocephalus palaemon 4 Arctic Skipper, mandan ssp. mandan Blue Bronze Copper Lycaena hyllus Blue 4 Checkered Skipper Pyrgus communis Blue 4 Common Ringlet, benjamini ssp. Coenonympha tullia benjamini Blue 4 Common Woodnymph, nephele ssp. Cercyonis pegala nephele Blue 4 Mead’s Sulphur Colias meadii Blue 3 Mountain Alpine Erebia pawloskii Blue 2 Old-world Swallowtail, pikei ssp. Papilio machaon pikei Blue 3 Tawny Crescent Phyciodes batesii Blue 4
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Provincial BCCF English Name Scientific Name Status priority Uhler's Arctic Oeneis uhleri Blue 4 White-veined Arctic, edwardsi ssp. Oeneis bore edwardsi Blue 3
2.5.2 Background
Butterflies have been documented in the Peace River Valley since the late 1990’s. Historical data was collected by Kondla et al. ( 1994), Bird et al. (1995), Layberry et al. (1998), Baker (2002), Guppy et al . (2003) and Hemmera (2006). The current status (to 2000) of species identification, photographs, distribution, habitat and biology are summarized in Guppy and Shepard (2001).
Baker (2002) surveyed grasslands around Grand Prairie and Fairview, Alberta, for butterflies in 2001. Assiniboine skipper ( Hesperia assiniboia ) was recorded at 5 sites and coral hairstreak (Satyrium titus ) was recorded at 1 site. Common ringlet ( Coenonympha tullia ), great spangled fritillary ( Speyeria cybele ) and Garita skipper ( Oasrisma garita ) were also recorded.
Guppy et al. (2003) conducted extensive habitat-focussed inventory in the South Peace. Surveys were conducted according to RISC standards (RIC 1998d). In total, 147 habitat blocks were searched and 81 species were identified. Fifteen Blue-listed species and two new species for the area were recorded. Blue-listed species detected included arctic skipper (Carterocephalus palaemon mandan) , common branded skipper ( Hesperia comma assiniboia), Baird’s swallowtail ( Papilio bairdii pikei) , Mead’s sulphur ( Colias meadii elis) , coral hairstreak (Satyrium titus titus), striped hairstreak ( Satyrium liparops fletcheri) , arctic blue ( Agriades glandon lacustris) , great spangled fritillary ( Speyeria cybele pseudocarpenteri) , Aphrodite fritillary ( Speyeria aphrodite manitoba) , tawny crescent ( Phyciodes batesii lakota) , common ringlet ( Coenonympha california benjamini) , common woodnymph ( Cercyonis pegala ino) , red- disked alpine ( Erebia discoidalis), Uhler’s arctic ( Oeneis uhleri varuna), and Alberta arctic (Oeneis alberta Alberta) (note that the status and taxonomy have changed for some of the taxa since 2003).
Hemmera (2006) completed butterfly surveys on Bear Mountain, 14.5 km southwest of Dawson Creek. Butterfly surveys completed in 2003 and 2006 resulted in documentation of 19 butterfly species. Provincially-listed species that were observed include the Arctic blue and Arctic skipper.
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Alberta Arctic
The Alberta arctic is Red-listed. It inhabits dry bunchgrass hillsides along the Peace River in BC (Guppy and Shepard 2001). The larval food plant is unknown in the Peace River but is likely one or more species of bunchgrass. Layberry et al. (1998) state that “many species of native grasses” may be used. Although, the Peace River populations of Alberta arctic have traditionally been placed in subspecies O. alberta alberta , authorities believe they are likely an unnamed subspecies that occurs only in the Peace River of British Columbia and Alberta (C. Guppy, unpubl. data.).
Aphrodite Fritillary
The Aphrodite fritillary, manitoba subspecies, is Blue-listed. Its habitat is mesic, prairie grasslands, sedge wetlands, and open aspen woodlands (E.H. Strickland Entomological Museum 2008; Guppy and Shepard 2001). The larval food plants are not known for the Peace River area, but the caterpillars of other subspecies are known to feed on the leaves of wild violets ( Viola spp.) (Guppy and Shepard 2001).
Arctic Blue
The arctic blue, lacustris subspecies is Blue-listed. It is found on south-aspect grass/shrub slopes, open, dry, young aspen stands (AS) and cleared powerline right-of-way (Guppy et al. 2003). In the Peace River area, adults have been seen laying eggs on Oxytropis species (family Fabaceae). They have also been noted to have a strong association with Saxifraga species (family Saxifragaceae), which is a known food plant elsewhere (Guppy and Shepard 2001). Populations in the Peace River area tend to be small and highly localized. They frequently occur on the crests of grass slopes (Guppy et al. 2003).
Arctic Skipper
The Arctic skipper, mandan subspecies, is Blue-listed. In the Peace River area, habitats include forest openings in mature, mesic to dry aspen/poplar and aspen forests, moist grass/shrub slopes, clearcuts, roadside ditches, and hay fields (Guppy et al. 2003). The larval food plants are not known for certain in the Peace River, but are apparently grasses that grow in moist
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Assiniboine Skipper
The Assiniboine skipper is Red-listed. In the Peace River area, habitats include clearings in aspen forest, hay fields, dry grass and open, dry aspen, south-aspect slopes, sedge wetlands, and river edges (Guppy et al. 2003). Gravel bars are used as “mudpuddling” sites. The larval food plants in the Peace River are unknown, but are presumably grasses and/or sedges.
Bronze Copper
The bronze copper is Blue-listed. The habitats at the two sites in the Peace River area found by Hawkes et al. (2006) were roadside ditches. The population near Fort Nelson in 1999 uses wet marshy habitat that also supports the Dorcas copper ( Lycaena dorcas) (Guppy and Shepard 2001). A population near Prince George apparently uses the cattail edges of sewage treatment ponds. Overall, habitat used by this species can be generally described as “wetlands”. This species occurs in widely scattered colonies in northeast BC. The larval food plants in the Peace River are unknown, but are presumably sorrel ( Rumex) species (Guppy and Shepard 2001).
Common Ringlet
The common ringlet, benjamini subspecies, is Blue-listed. In the Peace River area, it is found in dry to moist grass areas, including roadside ditches, south-aspect grass/shrub slopes, openings in aspen forests, hay fields, wetlands, and rights-of-way (Guppy et al. 2003). The larval food plants in the Peace River are unknown, but are presumably grasses. Elsewhere the food plants are grasses, including bluegrass ( Poa pratensis ) and needlegrass ( Stipa) (Layberry et al. 1998).
Common Woodnymph
The common woodnymph, nephele subspecies, is Blue-listed. In the Peace River area, it uses mesic to dry grassy meadows, mesic openings in aspen forests, cleared areas, hay fields and wetlands. The larval food plants in the Peace River area are unknown, but are presumably grasses. Elsewhere the food plants include wild oats ( Avena fatua ), purpletop grass ( Tridens flavus ) and bluestem ( Andropogon spp.) (Layberry et al. 1998).
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Coral Hairstreak
The coral hairstreak, titus subspecies, is Red-listed. In the Peace River area, south-aspect dry grass/shrub slopes are used by this species (Guppy et al. 2003). The single individual found in 2006 was feeding on nectar along a river bank in open aspen forest; this may have been a stray from a dry grass/shrub slope further up the hillside (Keystone Wildlife Research Ltd. 2006b). In the Peace River area, the adults are strongly associated with choke cherry ( Prunus virginiana ) (Guppy and Shepard 2001; C. Guppy unpubl. data), and may also use saskatoon ( Amelanchier alnifolia ) (Layberry et al. 1998).
Great Spangled Fritillary
The great spangled fritillary, pseudocarpenteri subspecies, is Red-listed. In the Peace River area, it is found at moist grassy sites in otherwise dry grass/shrub slopes, open aspen forest and clearings in aspen forest (Guppy et al. 2003). The larval food plants in the Peace River are unknown, but are presumably wild violets ( Viola spp.). Violets are used as the food plant elsewhere (Layberry et al. 1998; Guppy and Shepard 2001).
Old-world Swallowtail
The Old-World Swallowtail, pikei subspecies, is Blue-listed. It uses steep, south-aspect grass slopes and clay cliffs. The males characteristically patrol the crests of the slopes and cliffs, while females are most commonly found on the face of the grass slopes and cliffs (Guppy and Shepard 2001; C. Guppy unpubl. data). The larval food plant is Artemisia dracunculus (tarragon) (Guppy and Shepard 2001). Caterpillars were found on A. dracunculus in the Peace River area by Guppy (2001; unpublished data).
The old-world swallowtail, pikei subspecies, ( Papilio machaon pikei ) was observed along south- facing slopes along the Peace River near Clayhurst, Taylor, Attachie and Hudson’s Hope from 1980 to 1994 (BC CDC 2009). One record also exists from the Beatton River (BC CDC 2009). Larvae were found on tarragon (BC CDC 2009).
Striped Hairstreak
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(Prunus virginiana ) and spreading dogbane ( Apocynum androsaemifolium ) (Guppy et al. 2003). The larval food plants in the Peace River are unknown, but adults are strongly associated with saskatoon (Guppy and Shepard 2001; C. Guppy unpubl. data). The populations in the Peace River are traditionally called subspecies fletcheri , but are an unnamed subspecies found only in the Peace River of British Columbia and Alberta.
Tawny Crescent
The Blue-listed tawny crescent is found in open aspen forests and south-aspect, dry shrub slopes (Guppy and Shepard 2001). The larval food plants in the Peace River are unknown, but adults are strongly associated with aster species (Guppy and Shepard 2001; E.H. Strickland Entomological Museum 2008), especially showy aster ( Aster conspicuus ) (C. Guppy unpubl. data).
Uhler’s Arctic
Uhler’s arctic is Blue-listed. In the Peace River valley, this species occupies the grassy south aspect slopes and grassy openings in dry open aspen forest, up to at least 1000 m elevation (Guppy et al. 2003). The larval food plants in the Peace River are unknown, but adults are strongly associated with grasses (Guppy and Shepard 2001).
2.5.3 Methods
Inventory methods used in 2008 followed the BC Resource Inventory Standards Committee’s (RISC) Inventory Methods For Terrestrial Arthropods (RIC 1998d). The survey methodology for butterflies included a map-based evaluation of habitat suitability for the rare butterflies, field review and confirmation of habitat suitability and field surveys.
Draft habitat suitability mapping for target species was completed according to British Columbia Wildlife Habitat Ratings Standards (RIC 1999a).
2.5.3.1. Inventory Methods
Butterfly surveys were completed in the PRC and TL study areas. Habitat maps were used to identify potentially suitable habitat for listed butterflies and survey sites were defined as TEM polygons (habitat unit). The criteria used for polygon selection included presence of suitable habitat for one or more Red- or Blue-listed taxa (which varied depending on the time of year), July 2009 -98-
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Inventory efforts were focused on habitats used by the target butterfly taxa in flight during each of the four sample periods. Previously identified habitats at the Clayhurst Bridge were visited during each sample period, to confirm the flight period of the target butterflies. Other survey sites were seldom revisited to maximize the number of polygons inventoried.
Each TEM habitat polygon was inventoried for butterflies by walking throughout the area to sample all the microhabitats within the polygon. Sufficient time was spent in each polygon to ensure that all Red- or Blue-listed butterfly species using the polygon for breeding on the date of inventory were detected. Survey time varied from 15 minutes to 120+ minutes, depending on polygon size, microhabitat diversity, abundance and diversity of butterfly species and level of butterfly activity.
Butterflies were inventoried through sight observations and by netting. Netted butterflies were released after identification (most) or collected as a specimen. Specimens were killed (genus Phyciodes ) by pinching the thorax between thumb and forefinger, and then placed in a glassine envelope for temporary storage until permanent preparation. The habitat was recorded for each individual butterfly observation.
The Animal Observation Form for Terrestrial Arthropods was used to record butterfly observation data. This form was modified by Guppy et al. (2003) for butterfly surveys and is consistent with RISC standards. The TEM habitat type was recorded rather than listing the dominant plant species present.
All butterflies were identified by Crispin Guppy. Crescent butterflies (genus Phyciodes ) were identified from voucher specimens since sight observations are unreliable due to the great similarity of the species in this genus.
The English common names and Latin scientific names of the Red- or Blue-listed butterflies correspond to those used by the Conservation Data Centre (BC CDC 2009). The names used for the butterfly species that are not of conservation concern are based on current literature.
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2.5.3.2. Habitat Suitability Mapping
Draft habitat ratings for 14 butterfly taxa at risk were developed in 2006 (Keystone Wildlife Research Ltd. 2008b). Updates of the habitat ratings were completed using data from 2006 and 2008. For each taxon, the first and last dates on which the species was recorded were determined separately for each year. All the TEM habitat polygons inventoried in that time period, each year, were then assessed for use by the specific taxon.
The recorded use, or lack of use, was then used to estimate the relative habitat suitability for each taxon for each TEM habitat type that was inventoried in 2006 and 2008, during the recorded flight periods for each species. The suitability ranking for each taxon is based on “expert opinion” using the available data.
2.5.4 Results
Results of 2008 surveys and a compilation of data from surveys completed between 2005 and 2008 are reported below. Data from previous surveys were included when available from original databases or reports. The locations of butterfly surveys completed in 2005, 2006 and 2008 are shown on Maps 2.5.4a and 2.5.4b.
2.5.4.1. 2008 Inventory Surveys
Suitable habitat for butterflies were surveyed during 4 sampling periods: May 25 to 28, June 27 to July 1, July 18 to 21 and August 3 to 7, 2008. In total, 195 TEM polygons were surveyed for butterflies, with 147 polygons in the Peace River Corridor (PRC) study area and 48 polygons in the transmission line (TL) study area (Table 2.5.4.1a). Seventy polygons were wholly or partially within the potential Site C reservoir (SCR). No inclement weather conditions were experienced during butterfly surveys completed in 2008.
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Table 2.5.4.1a. Number of TEM polygons surveyed in each study area in 2008.
Number of TEM Polygons Surveyed Sampling Peace River Site C Transmission Total Period PRC and SCR Corridor Reservoir Line May 25 to 28 45 8 3 0 56 June 27 to July 1 15 19 1 20 55 July 18 to 21 13 14 2 9 38 August 3 to 7 4 23 0 19 46 Total 77 64 6 48 195
Within each TEM polygon, a number of sampling stations were completed. In total, 637 sample stations were visited in 2008, with 511 in the PRC study area (of which 239 are in the SCR), and 126 in the TL study area (Table 2.5.4.1b).
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Map 2.5.4a. Butterfly survey locations.
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Map 2.5.4b. Butterfly survey locations.
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Table 2.5.4.1b. Number of butterfly survey sample stations completed in 2008.
Number of Stations Date Peace River Total Site C Reservoir Transmission Line Corridor 25-May-08 39 39 26-May-08 71 71 27-May-08 35 33 68 28-May-08 43 43 27-Jun-08 12 12 28-Jun-08 11 29 40 29-Jun-08 11 23 34 30-Jun-08 14 12 26 01-Jul-08 47 47 18-Jul-08 7 48 55 19-Jul-08 7 13 20 20-Jul-08 13 13 21-Jul-08 11 15 26 03-Aug-08 38 38 04-Aug-08 8 8 05-Aug-08 63 63 06-Aug-08 2 18 20 07-Aug-08 14 14 Total 272 239 126 637
Fifty-six butterfly species were observed in 2008, with 46 species in the PRC study area and 32 in the TL study area (Appendix 7). Fourteen species were only detected in the potential Site C reservoir. Eight Blue-listed taxa and five Red-listed taxa were recorded in 2008 (Table 2.5.4.1c). Observations of 1295 individual butterflies were recorded, with 550 in the PRC study area and 307 in the TL study area (Appendix 7). Observations included 435 Blue-listed individuals and 108 individuals of Red-listed taxa (Table 2.5.4.1c). This resulted in 317 correlations between Red- or Blue-listed butterfly populations and TEM polygons (section 2.5.4.2).
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Table 2.5.4.1c. Red- or Blue-listed butterfly taxa detected during surveys in 2008.
Common Name Scientific Name Status PRC TL Total Alberta Arctic Oeneis alberta Red 22 22 Assiniboine Skipper Hesperia assiniboia Red 55 9 64 Coral Hairstreak, titus Red 4 4 subspecies Satyrium titus Speyeria cybele Red 9 4 13 Great Spangled Fritillary pseudocarpenteri Striped Hairstreak Satyrium liparops Red 5 5 Aphrodite Fritillary Speyeria aphrodite manitoba Blue 5 5 Arctic Blue, lacustris Blue 23 23 subspecies Plebejus glandon lacustris Old-world Swallowtail, pikei ssp. Papilio machaon pikei Blue 5 5 Bronze Copper Lycaena hyllus Blue 3 3 Common Ringlet, benjamini Blue 77 20 97 subspecies Coenonympha tullia benjamini Common Woodnymph Cercyonis pegala nephele Blue 83 83 Tawny Crescent Phyciodes batesii Blue 8 2 10 Uhler's Arctic Oeneis uhleri Blue 209 209 Total 508 35 543
2.5.4.2. Multiple Year Data Analysis
Hawkes et al . (2006) completed butterfly surveys in the Peace River Corridor (Core) and the surrounding uplands (Periphery) in 2005 (Table 2.5.4.2a). Eight Red or Blue-listed butterfly taxa were confirmed in the core area including Aphrodite fritillary, arctic skipper, old-world swallowtail (formerly Baird’s swallowtail), Assiniboine skipper (formerly common branded skipper), common ringlet, common woodnymph, coral hairstreak and great spangled fritillary (Table 2.5.4.2b).
Keystone Wildlife Research Ltd. (2006b) completed butterfly surveys in the Peace River Corridor (PRC) in 2006 (Table 2.5.4.2a). Twelve Red or Blue-listed taxa were recorded including Aphrodite fritillary, Arctic blue, Arctic skipper, old-world swallowtail (formerly Baird’s swallowtail), Assiniboine skipper (formerly common branded skipper), common ringlet, common woodnymph, coral hairstreak, great spangled fritillary, striped hairstreak, tawny crescent and Uhler’s arctic (Table 2.5.4.2b). The status of some taxa has changed since the surveys described above.
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Table 2.5.4.2a. Summary of butterfly survey effort in each study area in 2005, 2006 and 2008.
Number of Stations Number of taxa Study Area Year Surveyed** observed Core* June 1 to 33 35 Periphery* July 24, 2005 28 24 May 24 to July 24, 2006 90 54 Peace River Corridor 511 47 May 25 to August 7, 2008 Transmission Line 126 32 Total 788 65 + * information from Hawkes et al. 2005; **Number of Stations includes replicates; +Total number of species detected during all surveys .
In three years, 634 sites have been surveyed for butterflies in the Peace River Corridor and 154 site have been surveyed in the surrounding area (TL and periphery), resulting in the detection of 65 taxa, of which 14 were Red- or Blue-listed (Table 2.5.4.2b, Appendix 7). The provincial status has changed for some taxa since 2005; these changes are summarized in Table 2.5.4.2b.
Table 2.5.4.2b. Summary of the reported occurrence of Red- or Blue-listed butterflies in the Peace River Study Area in 2005, 2006 and 2008.
BC Status Detected in English Name Scientific Name 2006 2008 2005 2006 2008 Alberta Arctic Oeneis alberta Blue Red No No Yes Assiniboine Skipper Hesperia assiniboia Blue Red Yes Yes Yes Coral Hairstreak, titus ssp. Satyrium titus titus Blue Red Yes Yes Yes Great Spangled Fritillary, Speyeria cybele pseudocarpenteri ssp. pseudocarpenteri Blue Red Yes Yes Yes Old-world Swallowtail, Papilio machaon hudsonianus ssp. hudsonianus n/a Red No No No Striped Hairstreak Satyrium liparops Blue Red No Yes Yes Aphrodite Fritillary, manitoba Speyeria aphrodite ssp. manitoba Blue Blue Yes Yes Yes Arctic Blue, lacustris ssp. Plebejus glandon lacustris Blue Blue No Yes Yes Carterocephalus Arctic Skipper, mandan ssp. palaemon mandan Blue Blue Yes Yes No Bronze Copper Lycaena hyllus Blue Blue Yes No Yes Checkered Skipper* Pyrgus communis Blue Blue No No No Coenonympha tullia Common Ringlet, benjamini ssp. benjamini Blue Blue Yes Yes Yes Common Woodnymph, nephele ssp. Cercyonis pegala nephele Blue Blue Yes Yes Yes Mead's Sulphur Colias meadii Blue Blue No No No Mountain Alpine Erebia pawloskii Blue Blue No No No
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BC Status Detected in English Name Scientific Name 2006 2008 2005 2006 2008 Old-world Swallowtail, pikei ssp. Papilio machaon pikei Blue Blue Yes Yes Yes Tawny Crescent Phyciodes batesii Blue Blue No Yes Yes Uhler's Arctic Oeneis uhleri Blue Blue No Yes Yes White-veined Arctic, edwardsi ssp.* Oeneis bore edwardsi Blue Blue No No No Red-disked Alpine Erebia discoidalis Blue Yellow No No No *species are incorrectly listed for the Peace Forest District by the Conservation Data Centre.
In 2006 and 2008, 3307 individual butterflies were recorded with 1232 observations of Red- or Blue-listed taxa (Table 2.5.4.2c). Sufficient information was gathered in 2006 and 2008 to determine the habitat associations for 10 of the taxa (Table 2.5.4.2d). The Alberta arctic, coral hairstreak, striped hairstreak and bronze copper were found in low numbers at only a few sites and habitat associations were not confirmed for these taxa. This project provides the first data to correlate TEM habitat units with use by butterfly species in BC.
Six taxa have not been documented in the study area in three years of surveys and are unlikely to occur. The old-world swallowtail, hudsonianus ssp., checkered skipper, Mead’s sulphur, mountain alpine, white-veined arctic, edwardsi ssp. and red-disked alpine should be removed from the list of potential species for the study area.
The range of the 14 Red- or Blue-listed taxa in the study area was determined to extend from the Alberta border upstream to Hudson’s Hope. It is likely that these taxa also occur upstream of Hudson’s Hope and outside of the study area in suitable habitat.
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Table 2.5.4.2c. Number of Red- or Blue-listed butterfly taxa detected in TEM polygons sampled in 2006 and 2008.
# Individuals recorded # TEM Polygons Species Name 2006 2008 Total 2006 2008 Total Alberta Arctic 0 22 22 0 7 7 Aphrodite Fritillary, manitoba subspecies 38 5 43 12 4 16 Arctic Blue, lacustris subspecies 40 23 63 11 6 17 Arctic Skipper, mandan subspecies 49 0 49 17 0 17 Assiniboine Skipper 24 64 88 12 16 28 Old World Swallowtail, pikei subspecies 38 5 43 11 4 15 Bronze Copper 0 3 3 0 3 3 Common Ringlet, benjamini subspecies 88 97 185 22 40 62 Common Woodnymph, nephele subspecies 42 83 125 12 23 35 Coral Hairstreak, titus subspecies 1 4 5 1 3 4 Great Spangled Fritillary, pseudocarpenteri subspecies 38 13 51 13 10 23 Striped Hairstreak 7 5 12 1 4 5 Tawny Crescent 246 10 256 33 9 42 Uhler's Arctic 78 209 287 15 28 43 TOTAL 689 543 1232 160 157 317
Table 2.5.4.2d. Presence of rare butterfly taxa by TEM habitat units during surveys completed in 2006 and 2008. nephele ssp. ssp. ssp. ssp. titus titus mandan lacustris ssp. ssp. ssp. TEM MapcodeHabitat Arctic Blue,Arctic Alberta Arctic Alberta Arctic Aphrodite Fritillary, manitoba Striped Hairstreak Tawny Crescent Uhler's Arctic Great SpangledGreat Fritillary, Arctic Skipper,Arctic Assiniboine Skipper Bronze Copper Common Ringlet, benjamini Common Woodnymph, ssp. Coral Hairstreak, Old World Swallowtail, pseudocarpenteri pikei AM:ap y y n y y n y y y y y y y y AM n y n y y n n y n n n n y n AS n y y n y n y y n y n n y y BL n y n y n n n n n n BT n n n y n n n n n n CB n n y n CF n n y n n y y n n n n n n Fm02 y n n y y y y n y n n y n
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nephele ssp. ssp. ssp. ssp. titus titus mandan lacustris ssp. ssp. ssp. TEM MapcodeHabitat Alberta Arctic Alberta Arctic Aphrodite Fritillary, manitoba Blue,Arctic Striped Hairstreak Tawny Crescent Uhler's Arctic Arctic Skipper,Arctic Assiniboine Skipper Bronze Copper Common Ringlet, benjamini Common Woodnymph, ssp. Coral Hairstreak, Old World Swallowtail, Great SpangledGreat Fritillary, pikei pseudocarpenteri GB n n n y n n n n n n n n LL:ak n n n LL n n n n n RD n RI n n n n y y n n n n n n RZ y n n n n n n SC:ab n n n SE n y n n n y n y n y n n n n SH:ac n n y n n y n n n y n SH n n n SO y n n n n n y n n n n SW:as n n n n n y y n n n n y y SW n y n y n TS n y n y y n WH y n y y n y y n y n n y n WW y y y y y n y y y y y y y y y = taxa detected on at least one survey in 2006 and 2008; n = taxa not detected in this habitat unit during surveys completed during the flight period of this taxa.
2.5.5 Summary
Fourteen Red- or Blue-listed butterfly taxa have been confirmed in the study area. Habitat associations for ten of these taxa have been confirmed through inventory work completed in 2006 and 2008. The old-world swallowtail, hudsonianus ssp., checkered skipper, Mead’s sulphur, mountain alpine, white-veined arctic, edwardsi ssp. and red-disked alpine were not found in the study area during three years of sampling and should be removed from the list of potential species present in the study areas.
2.6 DRAGONFLIES
Dragonfly surveys were added to the 2008 scope of work due to the increasing concern about this species group. Surveys were conducted at a reconnaissance level to provide background information for potential future studies. The 2008 objectives were to:
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• determine species presence;
• inform the need for future surveys.
2.6.1 Introduction
Dragonflies and damselflies are relatively large and conspicuous winged insects. Dragonflies and damselflies reproduce in aquatic habitats such as rivers, streams, lakes, ponds, wetlands, and wet seepage areas including springs and ditches. There are two species of damselflies and one species of dragonfly on the provincial Blue list that potentially occur in the core study area (Table 2.6.1a).
Table 2.6.1a. Blue-listed damselflies and dragonflies potentially present in the study area.
Provincial English Name Scientific Name BCCF priority Status
Damselflies Prairie Bluet Coenagrion angulatum Blue 4 Hagen's Bluet Enallagma hageni Blue 4 Dragonflies Beaverpond Baskettail Epitheca canis Blue 4
2.6.2 Background
There are 12 location records of the Blue-listed prairie bluet within the Peace and Fort Nelson regions (Royal British Columbia Museum and the Spencer Entomological Museum 2004a). The prairie bluet is found in forested marshes and grassland ponds (Royal British Columbia Museum and the Spencer Entomological Museum 2004a).
Hagen’s bluet has been found on ponds and marshy lakes and is most common in the Cariboo and Prince George regions. There is one record from the Peace River area (Royal British Columbia Museum and the Spencer Entomological Museum 2004b).
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The beaverpond baskettail inhabits slow-moving streams, marshy shorelines and ponds. There are two records from the vicinity of the Peace River (Royal British Columbia Museum and the Spencer Entomological Museum 2004c).
No dragonfly surveys have been completed in or near the study area.
2.6.3 Methods
Inventory methods used in 2008 followed the BC Resource Inventory Standards Committee’s (RISC) Inventory Methods For Terrestrial Arthropods (RIC 1998d). Dragonfly surveys were completed in conjunction with butterfly surveys.
2.6.3.1. Inventory Methods
Dragonfly and damselfly surveys were conducted at a reconnaissance level to inform the need for additional species-specific studies. Dragonfly specimens were collected opportunistically as part of the butterfly inventory in the PRC and TL study areas (section 2.5.3). Specimens were collected at potential breeding sites including small ponds and other aquatic habitat. At each site, surveyors attempted to collect at least one male and one female specimen of each species present. Mated pairs were preferentially captured, since they have greater scientific value than do single individuals of either sex. A limited number of Individuals seen outside of potential reproductive habitat were also collected, to supply species records for the general area. The UTM location (NAD 83) was recorded for each specimen captured.
Specimens were placed into glassine envelopes and dehydrated in acetone in accordance with the Royal BC Museum standards (Victoria, BC). All specimens were deposited in the Royal BC Museum and were identified by the Entomology Curator Dr. Robert A. Cannings, the BC expert on dragonflies and damselflies.
2.6.3.2. Habitat Suitability Mapping
Habitat ratings have not been developed for dragonflies due to the reconnassiance nature of the 2008 surveys and the lack of published habitat data for most species. Dragonflies and damselflies are expected to reproduce in aquatic habitats such as rivers, streams, lakes, ponds and wetlands, and in wet seepage areas including springs and ditches.
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2.6.4 Results
The locations of dragonfly surveys completed in 2008 are shown on Maps 2.6.4a and 2.6.4b. Specimens were collected during butterfly surveys between May 25 and August 7, 2008, in the Peace River Corridor (PRC) and transmission line (TL) study areas. Eighteen species of dragonflies and damselflies were found in 2008. No species of conservation concern were detected. In total, 155 individual voucher specimens were captured for all 18 species (Table 2.6.4a).
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Map 2.6.4a. Dragonfly survey locations.
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Map 2.6.4b. Dragonfly survey locations.
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Table 2.6.4a. Dragonfly and damselfly species captured during surveys completed in 2008.
Study Area Common Name Scientific Name BCCF Total priority PRC TL Black Meadowhawk Sympetrum danae 6 9 1 10 Boreal Bluet Enallagma boreale 6 11 1 12 Boreal Whiteface Leucorrhinia borealis 6 1 1 2 Four-spotted Skimmer Libellula quadrimaculata 6 8 8 Hudsonian Emerald Somatochlora hudsonica 5 2 2 Hudsonian Whiteface Leucorrhinia husonica 6 1 1 Lake Darner Aeshna eremita 6 2 1 3 Marsh Bluet Enallagma ebrium 6 15 15 Northern Bluet Enallagma annexum 6 5 7 12 Northern Spreadwing Lestes disjunctus 6 12 4 16 Paddle-tailed Darner Aeshna palmata 6 2 1 3 Pale Snaketail Ophiogomphus severus 6 1 1 Sedge Darner Aeshna juncea 6 7 7 Spotted Spreadwing Lestes congener 6 8 8 Taiga Bluet Coenagrion resolutum 6 6 3 9 Variable Darner Aeshna interrupta 6 25 1 26 White-faced Meadowhawk Sympetrum obtrusum 6 12 3 15 Cherry-faced Meadowhawk Sympetrum internum 6 2 3 5 Total 127 28 155
2.6.5 Summary
The 2008 survey was intended as a baseline reconnaissance. Eighteen dragonfly and damselfly species were detected. Although not detected in 2008, all three Blue-listed species have historical records in the Peace region. Based on the known habitat preferences for these species, they are more likely to occur in the TL study area where wetlands, ponds and lakes are more prevalent. The fluctuating water level typical of riparian habitat along the Peace River may not provide suitable habitat for these species.
2.7 RARE VASCULAR PLANTS
Rare plant surveys were not undertaken in the Peace River Valley prior to 2005 and limited information exists on the presence and distribution of rare plants in northern BC. A number of
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• determine the occurrence, distribution and abundance of rare taxa occurring in floodplain and riparian habitats in the study area;
• determine the ecological characteristics of rare populations and their potential vulnerability.
2.7.1 Introduction
A list of 101 rare plant taxa that potentially occur in the study area was compiled prior to fieldwork in 2008 (Appendix 8a). That list was developed based on known occurrences or reports of species within or near the study area. Data sources included previous rare plant work completed in the area (Hawkes et al. 2006; Keystone Wildlife Research Ltd. 2006b), CDC occurrence records (BC CDC 2009), E-flora BC distribution maps (Klinkenberg 2006) and the dot maps in Volume 8 of the Illustrated Flora of British Columbia (Douglas et al. 2002). No SARA-listed species are expected to occur in the study area.
2.7.2 Background
No inventory surveys documenting rare plant species had been completed within the study area prior to 2005.
2.7.3 Methods
There are no provincial (RISC) standards for rare plant surveys. Survey methodology followed Survey Protocol for Vascular Plants (USDA FS and USDI BLM 1999) and Survey Protocols for Survey and Manage Strategy 2: Vascular Plants (Whiteaker et al. 1998).
2.7.3.1. Inventory Methods
Field surveys for rare plants focused on rare taxa potentially present in valley bottom, floodplain habitats in the PRC study area and other suitable sites in the TL study area. A sampling plan was developed by the project botanist to target habitats likely to support rare plant taxa within the two study areas. The locations of target habitats in the study areas were determined on the TEM map and these polygons were prioritised for sampling. Non-target polygons and habitats
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Rare plant surveys took place in two sample periods to ensure that plants with different times of emergence and flowering were sampled in their prime condition (Klinkenberg and Penny 2006). It is essential to collect mature plant parts such as flowers or seeds to confirm species identification.
Surveys were conducted on foot by two experienced botanists, using intuitive controlled surveys (Whiteaker et al. 1998). An intuitive survey is a variable intensity survey protocol that involves walking through pre-selected sample sites to survey a representative cross-section of the major habitat types and environmental conditions in a study area (USDA FS and USDI BLM 1999). Surveyors completed a zigzagging traverse and when an area of high potential habitat (as defined in the pre-field review or encountered during the field visit) was located, a more thorough survey for target species was completed. Information for each site was recorded on a Ground Inspection Form (GIF) including UTM location (NAD 83), polygon number, all plant species observed (i.e. name, % cover) and site series. A BC CDC Field Survey Form was also completed when a rare plant was detected. Surveys within single sites lasted between one and eight hours.
Plants were collected as voucher specimens if a sample could be collected without compromising the population (Klinkenberg and Penny 2006; RIC 1999c). Collected materials were pressed as soon as possible to ensure a high quality voucher specimen. Plants were collected in flower or seed where possible. Specimens were collected for voucher material for at least one population of each of the rare plant species, whenever possible. Specimens were deposited at the University of British Columbia herbarium. Voucher photos were also taken to record occurrences whenever possible.
All vascular plant species were recorded at each site. Reference books consulted for identification include the Illustrated Flora of British Columbia volumes 1 through 8 (Douglas et al. 1998a, 1998b, 1999a, 1999b, 2000, 2001a, 2001b, 2002), the Flora of the Pacific Northwest (Hitchcock & Cronquist 1973), the Jepson Manual (Hickman 1993) and the published volumes of the Flora of North America (Flora of North America Editorial Committee
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1993, 1997, 2000, 2002, 2003a, 2003b, 2004, 2005, 2006a, 2006b, 2006c, 2007a, 2007b). Additional original taxonomic literature was consulted in some cases.
Species Diversity
An index of species diversity was calculated for transects in the PRC and TL study areas, as well as for transects wholly or partially within the potential Site C reservoir (SCR). A rough diversity index was calculated by dividing the total number of plant species encountered by the distance sampled. Søerensons Quotient (SQ) was used to compare the similarity in plant species between the study areas (Magurran 1988). Søerensons Quotient is calculated by doubling the number of species common to both areas and dividing it by the total number of species found in both of the study areas (number of species common to both*2/number of species in PRC + number of species in TL), expressed mathematically as
2J/(A+B) where
A = number of species in the PRC
B = number of species in the TL
J = number of species common to both.
Values close to 1 have most of their species in common, while values close to 0 indicate dissimilar plant assemblages.
2.7.3.2. Habitat Suitability Mapping
Species models and habitat suitability maps were not prepared for rare plant taxa. Modelling may not be appropriate given that most species occurrences appear correlated with microhabitat characteristics rather than characteristics available at the 1:20,000 scale of mapping.
2.7.4 Results
Results of 2008 surveys and a compilation of data from surveys completed between 2005 and 2008 are reported below. The location of rare plant surveys completed in 2005, 2006 and 2008 are shown on Maps 2.7.4a and 2.7.4b.
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2.7.4.1. 2008 Inventory Surveys
Twenty-five rare plant transects were completed in 2008, with 21 transects in the Peace River Corridor (PRC) study area and 4 in the transmission line (TL) study area. Transects were completed during two survey periods, July 15 to 25 and September 14 to 21, 2008. It is unlikely that any early-flowering plants were missed since the 2008 growing season was unusually late and vascular plants were identifiable in July and September. In total, 150 TEM polygons were sampled, 49 of which were wholly or partially within the potential Site C reservoir (Table 2.7.4.1a).
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Map 2.7.4a. Rare plant survey locations.
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Map 2.7.4b. Rare plant survey locations.
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Table 2.7.4.1a. Summary of rare plant transects completed and the number of taxa detected in 2008.
Transect Survey Distance Study Number of Number of Label Period surveyed Area TEM Vascular Taxa (km) Polygons Recorded Surveyed RP01 July 2.3 SCR 11 192 RP02 July 1 SCR 6 171 RP03 July 0.5 PRC 2 60 RP04 July 2 PRC 7 144 RP05 July SCR 7 2.05 259 RP05 Sept. SCR 4 RP06 Sept. 1.8 SCR 5 RP06E July 1.6 SCR 5 277 RP06W July 0.84 SCR 4 RP07 July 0.15 SCR 3 85 RP08E July 1.4 SCR 2 119 RP08W July 2.8 SCR 7 205 RP09 July 4.5 SCR 16 207 RP11E July 3.4 PRC 8 181 RP11W July 1.8 SCR 5 213 RP13 Sept. 0.12 PRC 1 91 RP15 Sept. 0.58 SCR 4 158 RP23 Sept. 0.01 SCR 1 96 RP16/24 Sept. 0.2 SCR 1 82 RP25 Sept. 4.7 PRC 14 182 RP26 Sept. 1.9 PRC 10 152 RP27 July 0.24 SCR 3 71 PRC total* 33.9 109 539** RP19 Sept. 1.1 TL 8 145 RP20 Sept. 1.8 TL 10 162 RP21 Sept. 2.9 TL 14 193 RP22 Sept. 4 TL 9 167 TL Total* 9.8 41 310** *Subtotals do not include repeat visits; **Total of all species detected during all surveys.
In 2008, 3,751 observations were recorded, with 60 to 277 vascular species recorded per transect. In total, 588 vascular plant taxa were identified, including 539 taxa in the PRC study area and 310 in the TL study area (Table 2.7.4.1a, Appendix 8b). In total, 59 non-native plant taxa were found during surveys, with 55 in the PRC study area and 33 in the TL study area (Appendix 8b).
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Twenty-eight vascular plant taxa listed by the BC CDC were recorded during surveys in 2008 (Table 2.7.4.1b). Twenty-four Blue-listed taxa were found, with 18 in the PRC study area and 6 in the TL study area. Only two species were found in both study areas. Six Red-listed taxa were found in the PRC study area, one of which was also detected in the TL study area.
Table 2.7.4.1b. Number of rare plant populations recorded during rare plant surveys in 2008.
Study Status in Number of Area Species Common Name BC Populations Anemone virginiana var Red 6 cylindroidea Riverbank anemone Arnica chamissonis ssp incana Meadow arnica Blue 1 Artemisia herriotii (A rtemisia Red 8 longifolia misapplied ) Harriet's mugwort Boechera sparsiflora Sickle-pod rockcress Red 9 Calamagrostis montanensis Plains reedgrass Blue 2 Carex heleonastes Hudson's Bay sedge Blue 1 Carex sychnocephala Many-headed sedge Blue 1 Carex vulpinoidea Fox sedge Blue 1 Chrysosplenium iowense Iowa golden-saxifrage Blue 1 Cicuta virosa European water hemlock Blue 1 Cirsium drummondii Drummond's thistle Red 1 PRC Epilobium halleanum Hall's willow herb Blue 1 Epilobium leptocarpum Small-fruited willowherb Blue 1 Helictotrichon hookeri Spike-oat Blue 2 Juncus arcticus ssp alaskanus Arctic rush Blue 1 Muhlenbergia glomerata Marsh muhly Blue 1 Oxytropis campestris ssp davisii Davis' locoweed Blue 4 Packera plattensis Plains butterweed Blue 8 Penstemon gracilis Slender penstemon Red 1 Salix serissima Autumn willow Blue 1 Scolochloa festucacea Rivergrass Red 2 Sphenopholis intermedia Slender wedgegrass Blue 2 Symphyotrichum puniceum var Blue 3 puniceum Purple-stemmed aster Trichophorum pumilum Dwarf clubrush Blue 1 Total PRC 60
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Study Status in Number of Area Species Common Name BC Populations Cirsium drummondii Drummond's thistle Red 1 Galium labradoricum Northern bog bedstraw Blue 1 Malaxis brachypoda White adder's mouth Blue 1 Packera plattensis Plains butterweed Blue 2 TL Pedicularis parviflora var Blue 1 parviflora Small-flowered lousewort Salix petiolaris Meadow willow Blue 1 Symphyotrichum puniceum var Blue 3 puniceum Purple-stemmed aster Total TL 10
Of the six Red-listed vascular plant taxa located during field surveys, three are only known from the Peace River Corridor in British Columbia (Harriet's mugwort , slender penstemon and Drummond's thistle).
Thirteen taxa (species or subspecies) were found in 2008 that appear to be previously undescribed (not reported or named in the literature) (Table 2.7.4.1c). Two of these species appear to be secure, with numerous populations and minimal sensitivity ( Bromus sp nov and Rumex sp nov cf mexicanus ). Additional research is required to confirm the uniqueness of these species.
Table 2.7.4.1c. Previously undescribed vascular plants located in the study area in 2008. Scientific Name Study Area Notes Bromus sp nov PRC Carex sp nov cf PRC/TL Differs from Carex atherodes in several characteristics atherodes Carex sp nov cf tenera PRC Intermediate between Carex tenera and Carex crawfordii Differs from all other Cicuta in North America in fruit shape Cicuta sp nov PRC (though only half-mature fruits were seen in July 2008) as well as other characteristics Cystopteris sp nov PRC Differs from Cystopteris fragilis in several characteristics More research is needed to determine whether these plants may Elymus sp nov PRC be a hybrid of two Elymus grass species, and whether this form occurs elsewhere. Differs from other Epilobium species in our region in having hairs Epilobium sp nov TL evenly distributed all around the stem, and in other characteristics Erigeron sp nov (aff PRC These plants are closest morphologically to Erigeron cespitosus cespitosus)
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Scientific Name Study Area Notes The most similar species is Erigeron pumilus , which differs in Erigeron pacalis ined. PRC having glandular stems, narrower basal leaves, almost always taller stature. Intermediate in characteristics between M. cuspidata, M. Muhlenbergia sp nov PRC filiformis, and M. richardsonis . This is clearly a close relative of Platanthera aquilonis , and Platanthera aplectra ined. PRC probably evolved from it. Rumex sp nov cf PRC Like Rumex mexicanus mexicanus Clearly belongs to Viola renifolia, but differs from both var Viola renifolia var nov PRC renifolia and var brainerdii . Type specimens need to be examined.
Fourteen vascular plants were found during surveys that appear to be rare in British Columbia but are not currently listed by the BC CDC (Table 2.7.4.1d). Two species new to British Columbia ( Rorippa calycina and Rumex britannica ) were recorded and one species was previously known from British Columbia but appears to be rare and limited to the Peace Lowland grasslands ( Geum triflorum var. triflorum ).
Table 2.7.4.1d. Vascular plants located in the study area in 2008 that appear to be locally rare but are not listed provincially (includes species previously undescribed).
Study Number of Species Common Name Comments Area Populations Carex sp nov cf atherodes No common name exists undecribed 1 Carex sp nov cf tenera No common name exists Undecribed 5 Cicuta sp nov No common name exists Undecribed 1 Cystopteris sp nov No common name exists Undecribed 5 Elymus sp nov No common name exists Undecribed 2 Erigeron pacalis ined . No common name exists Undecribed 1 Erigeron sp nov (aff Undecribed No common name exists 2 PRC cespitosus) Known from BC, but Geum triflorum var triflorum old man's whiskers 5 limited to the Peace Muhlenbergia sp nov No common name exists Undecribed 1 Platanthera aplectra ined . No common name exists Undecribed 2 Persistent-sepal yellow Rorippa calycina New to BC 3 cress Viola renifolia var nov No common name exists Undecribed 3 Total PRC 31
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Study Number of Species Common Name Comments Area Populations Carex cf atherodes No common name exists Undecribed 1 Carex cf tenera No common name exists Undecribed 1 TL Epilobium sp nov No common name exists Undecribed 1 Rumex britannica British dock New to BC 4 Total TL 7
Fifty-nine vascular plant species found in the project area are exotics not native to the flora of British Columbia, having been introduced via non-First Nations immigration, colonialization and economic activity (Appendix 8b). Almost all of these plants originated in Europe and their invasive spread is facilitated by human activities, such as ranching/agriculture, recreational activities, road and trail use, logging, mining and hydroelectric development (Boersma et al . 2006). These activities are prevalent in the study areas. The spread of invasive species is one of the leading contributors to the loss of biodiversity in large areas of the world (Wilcove et al. 1998), and a leading cause of habitat loss (Lodge 1993). Generally, invasive species are better adapted to human-caused disturbance than native flora, allowing them to out compete native flora and dominate disturbed habitats. These disturbed areas become source populations facilitating the spread of invasive species into less disturbed habitats or wilderness areas.
The prickly pear ( Opuntia fragilis ) is of interest to local residents of the Peace River Valley. This species is at the northern extent of its range in northeast BC and is provincially Yellow-listed, but described as possibly rare along the Peace River by Douglas et al. (1998b). The prickly pear was found in 2% of the habitat plots completed during TEM map truthing in 2005 (Keystone Wildlife Research Ltd. 2008a) and was found in the dry grassland habitat unit (WW; Appendix 3a), which occurs along the slopes of the Peace River.
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Habitat Associations
Descriptions of rare plant taxa located in the study area are presented in Appendix 8c. The rare plants detected in select habitats types are summarised in Table 2.7.4.1e.
Table 2.7.4.1e. Summary of habitat types and rare species detections.
Habitat Type Rare Species Detected Active Channel Long-leaved mugwort , sickle-pod rockcress, fox sedge , Carex sp nov cf tenera, arctic rush, Davis’ locoweed, plains butterweed, persistent sepal yellowcress, and slender wedgegrass. AM (White Spruce – Trembling Riverbank anemone, long-leaved mugwort, sickle-pod Aspen - Step moss) rockcress, Drummond’s thistle and plains butterweed. AMy:ap (Trembling Aspen - Epilobium sp nov, plains butterweed, and purple-stemmed Creamy peavine - seral aster association) BT (Black Spruce - Labrador White adder's-mouth orchid and small-flowered lousewort tea – Sphagnum) Fm02 (Balsam Poplar - White Riverbank anemone Spruce - Red-osier dogwood) SE (Sedge wetland) Meadow arnica , many-headed sedge , Carex sp nov cf atherodes, Carex sp nov cf tenera, European water-hemlock , Cicuta sp nov, small-fruited willowherb, plains butterweed, British dock, rivergrass, and purple-stemmed aster SW (White Spruce - Wildrye - Riverbank anemone, Carex sp nov cf tenera. Iowa golden- Peavine) saxifrage , Cystopteris sp nov , plains butterweed, purple- stemmed aster TS (Tamarack - Sedge - Fen) Hudson Bay sedge , Hall’s willowherb , northern bog bedstraw , Platanthera aplectra ined. , autumn willow , and purple- stemmed aster WH (Willow - Horsetail - Sedge Long-leaved mugwort and Carex sp nov cf tenera . - Riparian wetland) WS (Willow - Sedge - Wetland) British dock and purple-stemmed aster WW (Fuzzy-spiked wildrye - Riverbank anemone, long-leaved mugwort, sickle-pod Wolf willow) rockcress, plains reedgrass , Elymus sp nov, Erigeron sp nov (aff cespitosus) , Erigeron pacalis ined ., old man's whiskers, spike-oat, and slender penstemon
Richness
The transmission line (TL) had the highest relative richness (310 species / 9.8 km) of all the study areas. This result is likely related to the relative undersampling of the TL study area (4 transects compared to 21) since the number of new species detected decreases as the survey effort increases. The potential Site C reservoir (SCR) had the second highest species richness
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(519 species / 22 km), followed by the Peace River corridor (PRC) (540 species / 34 km). The Søerensons Quotient for the TL compared to the PRC was 0.62, indicating that over half of the species occur in both areas.
2.7.4.2. Multiple Year Data Analysis
Hawkes et al. (2006) completed rare plant surveys in the Peace River Corridor (Core) and the surrounding uplands (Periphery) in 2005 (Table 2.7.4.2a). Twenty-one Red- or Blue-listed taxa were detected, with 82 observations of 18 listed taxa in the core area and 32 observations of 12 listed taxa in the periphery. The grasslands and shrublands above the Peace and Beatton Rivers were identified as having the most diverse rare plant communities.
Keystone Wildlife Research Ltd. (2006b) completed rare plant surveys in the Peace River Corridor (PRC) and along the Transmission Line (TL) in 2006 (Table 2.7.4.2a). Eleven Red- or Blue-listed taxa were detected in 60 observations. The sedge wetland (SE) and fuzzy-spiked wildrye – wolf willow (WW) ecosystem units contained the most rare taxa.
Based on the results from 2008, specimens from 2006 were reviewed by botanist C. Björk. He determined that several taxa had been misidentified, despite confirmation of several specimens by the UBC herbarium in 2006. Re-examination and additional consultation with the UBC herbarium confirmed that these species had been erroneously reported. The total number of Red- or Blue-listed taxa observed in 2006 was revised to seven based on these results.
Table 2.7.4.2a. Summary of rare plant surveys completed in 2005, 2006 and 2008.
Number of Red- or Blue Number of Sites listed plant taxa Study Area Year Survey Period Sampled identified Periphery 44 12 2005 July 20 and August 6 Core 170 18 Peace River 2006 June 19 to Sept. 16 102 7 Corridor 109 24 2008 July 15 to Sept. 21 Transmission Line 41 7 Total 466 42* *Total number of species detected during all surveys.
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Of the 101 potential Red- or Blue-listed vascular taxa (Appendix 8a), 42 taxa have been recorded near the Peace River valley as a result of surveys in 2005, 2006 and 2008 (Table 2.7.4.2b). Two species, dainty moonwort and slender mannagrass, were only detected in the periphery in 2005 and were not recorded in 2006 or 2008.
Table 2.7.4.2b. Rare vascular plant taxa detected in 2005, 2006 and 2008.
Provincial Survey year Scientific Name Common Name Project Area Rank 2005 2006 2008 Anemone virginiana var. Riverbank anemone Red X X PRC cylindroidea Arnica chamissonis ssp. Meadow arnica Blue X X PRC incana Artemisia herriotii (misreported in BC as Long-leaved mugwort Red X X X PRC Artemisi a longifolia) Atriplex nuttallii Nuttall's orache Red X PRC Boechera lignifera ( syn . Woody-branched Blue X PRC Arabis lignifera) rockcress Boechera sparsiflora ( syn . Sickle-pod rockcress Red X PRC Arabis sparsiflora) Botrychium crenulatum Dainty moonwort Blue X periphery Calamagrostis Plains reedgrass Blue X X PRC montanensis Carex heleonastes Hudson Bay sedge Blue X PRC Carex sychnocephala Many-headed sedge Blue X PRC Carex torreyi Torrey's sedge Blue X PRC Carex vulpinoidea Fox sedge Blue X PRC Carex xerantica Dry-land sedge Red X PRC Chrysosplenium iowense Iowa golden-saxifrage Blue X X PRC European water- Cicuta virosa Blue X PRC hemlock Cirsium drummondii Drummond's thistle Red X X X PRC/TL Eleocharis elliptica Slender spike-rush Blue X PRC Epilobium halleanum Hall's willowherb Blue X PRC Small-fruited Epilobium leptocarpum Blue X PRC willowherb Rocky Mountain Epilobium saximontanum Red X PRC willowherb Galium labradoricum Northern bog bedstraw Blue X X TL Glyceria pulchella Slender mannagrass Blue X periphery Helictotrichon hookeri Spike-oat Blue X X X PRC Juncus arcticus ssp. Arctic rush Blue X PRC alaskanus Juncus confusus Colorado rush Red X PRC White adder's-mouth Malaxis brachypoda Blue X TL orchid
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Provincial Survey year Scientific Name Common Name Project Area Rank 2005 2006 2008 Muhlenbergia glomerata Marsh muhly Blue X PRC Oxytropis campestris var . Davis' locoweed Blue X PRC davisii Oxytropis campestris var . Jordal's locoweed Blue X PRC jordalii Packera plattensis ( syn . Plains butterweed Blue X PRC/TL Senecio plattensis) Pedicularis parviflora ssp . Small-flowered Blue X TL parviflora lousewort Penstemon gracilis Slender penstemon Red X X PRC Salix petiolaris Meadow willow Blue X TL Salix serissima Autumn willow Blue X X PRC, periphery Schizachyrium scoparium Little bluestem Red X X PRC Scolochloa festucacea Rivergrass Red X PRC Selaginella rupestris Rock selaginella Red X PRC Silene drummondii var . Drummond's campion Blue X PRC drummondii Sphenopholis intermedia Slender wedgegrass Blue X PRC Sphenopholis obtusata Prairie wedgegrass Red X PRC Symphyotrichum puniceum var puniceum ( syn . Aster Purple-stemmed aster Blue X PRC/TL puniceus var puniceus) Trichophorum pumilum Dwarf clubrush Blue X PRC X – species recorded during surveys.
2.7.5 Summary
In three years, 42 Red- or Blue-listed vascular plants have been recorded in the Peace River Valley and the surrounding upland areas. Fourteen additional species were documented that appear to be rare but are not currently listed by the CDC.
2.8 BATS
Bats tend to be relatively little-known species due to their nocturnal nature and the need for specialized study techniques and equipment to document their habitats and life history. Additional studies were required in 2008 to:
• obtain additional information on the northern myotis;
• estimate relative bat activity in habitat types in the study area;
• determine roosting habitat use in the study areas.
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2.8.1 Introduction
The Peace River Corridor is ecologically distinct from surrounding boreal regions due to the climatic influence of the Rocky Mountains and the presence of a large river. The rich floodplain habitats and surrounding agricultural landscapes may influence bat species presence and activity.
Nine bat species potentially occur in the Peace River Corridor (Table 2.8.1a), based on Nagorsen and Brigham (1993) and others (Wilkinson et al. 1995; Crampton et al. 1997; Vonhof et al. 1997; Lausen and Barclay 2006b; Lausen et al. 2008). The northern myotis is Blue-listed provincially, and the remaining species are Yellow-listed. All nine species are insectivores and will forage anywhere insects concentrate, including in open forests, over slow-moving water or ponds, and along cliffs. Body size, manoeuvrability, and flight speed vary between species, allowing smaller, more manoeuvrable bats to forage in dense forests, while larger species tend to fly over the canopy or along cliff edges (Nagorsen and Brigham 1993).
Table 2.8.1a. Bat species potentially present in the study area.
Existing Provincial BCCF records from Common name Scientific Name Status priority Northeastern BC Californian Myotis Myotis californicus Yes Long-eared Myotis Myotis evotis Yes Little Brown Myotis Myotis lucifugus 5 Yes Northern Myotis Myotis septentrionalis Blue listed 2 Yes Long-legged Myotis Myotis volans 2 Yes Silver-haired bat 1 Lasionycteris noctivagans 2 Yes Eastern Red Bat 1 Lasiurus borealis No Big Brown Bat 1 Eptesicus fuscus 6 Yes Hoary Bat 1 Lasiurus cinereus 2 Yes 1 Species considered “big bats”.
All nine species are known to roost in trees, with some documented also using buildings, rock crevices, or cliffs. In boreal forests, the limited research on roost selection by little brown myotis, northern myotis, and silver-haired bat suggests that these bats predominantly roost in dying or dead poplar trees (balsam poplar and trembling aspen) (Vonhof et al. 1997; Crampton and Barclay 1998). Bats commonly roost beneath loose bark, in cracks or cavities or in foliage clusters (hoary and red bats) on large trees or snags, in old, open forest stands (Barclay and Brigham 1996).
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All bats in BC mate in the late summer or fall, prior to hibernation or migration. Females store sperm over the winter, and fertilization occurs in the spring after females emerge from hibernacula (Nagorsen and Brigham 1993). Most pregnant female bats gather in maternity colonies of the same species and the young are born in June or July. The developmental rate of the foetus is temperature-dependent; thus in cooler climates, birth may occur later in the summer. In the Liard area in 1995, bats gave birth between the last week of June and the first week of July, with the first post-lactating female captured in late July (Wilkinson et al . 1995). In the same region in 1997, bats were lactating throughout July and the first post-lactating female was caught in August (Vonhof et al . 1997).
As temperatures drop in the fall and insect activity ceases, bats must migrate or hibernate until spring. In northeastern BC, this could mean a hibernation period of 7 to 8 months (September through to April or May). During this time, relatively warm spells may enable bats to become active to forage or drink (Nagorsen et al . 1993; Lausen and Barclay 2006b). Very little is known about BC’s bats behavour and activity patterns in the winter. Hoary bats and red bats are considered migratory throughout their range and do not hibernate. Silver-haired bats in Canada are believed to migrate, although some populations may remain in the province (Nagorsen et al . 1993). All other species in northeastern BC hibernate, but may travel several hundred kilometres between summer roost areas and hibernacula (Nagorsen and Brigham 1993). Unlike hibernacula in eastern Canada, the few identified hibernacula in western Canada contain solitary individuals or small clusters of bats (2 – 48 animals) (Nagorsen et al . 1993; Hill et al . 2006), similar to what is found in Washington and Oregon (Perkins et al . 1990). There are no documented hibernacula in the Peace River/ Fort St. John area, but limestone areas on the east side of the Rocky Mountains may contain cave features. The caves at Monkman Park, south of Tumbler Ridge (150 km from the Peace River) are an example of potentially suitable features.
The suitability of a site as a hibernaculum depends on the climatic conditions inside. Bats may hibernate in caves, rock crevices, mines, houses, tree cavities, or under bark (Whittaker and Gummer 1992; Nagorsen et al . 1993; Hill et al . 2006; Lausen and Barclay 2006b), as long as the conditions keep them from freezing or desiccating. Temperatures are usually stable and just above freezing, although bats have been documented hibernating at –7°C (Nagorsen and Brigham 1993). Hibernacula must also be relatively humid and conditions reported from natural
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Prior to hibernation, bats exhibit swarming behaviour, when groups of bats of both sexes fly through potential hibernacula. Bats may come from a large surrounding area (Parsons et al. 2003a) and many will mate during swarming. Swarming may serve other functions as well, such as showing young the location of hibernacula (Parsons et al . 2003a). Not all bats swarming at a site will hibernate there (Fenton 1983 in Caceres and Pybus 1997). Swarming was reported at Cadomin Cave, AB in late August and early September (Schowalter 1980 in Caceres and Pybus 1997) and this likely reflects the timing of swarming in the study area.
2.8.2 Background
Knowledge of bats in the Peace River Corridor is limited to early collections at Hudson’s Hope in 1931 (mentioned in Nagorsen and Brigham 1993), specimens from the general region in 1977- 1981 (in Caceres and Pybus 1997) and studies of silver-haired bats and big brown bats (Schowalter et al. 1978 and Schowalter and Gunson 1979, cited in Nagorsen and Brigham 1993). There is also a growing body of literature on bats in boreal ecosystems, including research in the BWBS biogeoclimatic zone at the Liard River located about 700 km northwest of Dawson Creek (Wilkinson et al. 1995; Vonhof et al. 1997) and Prophet Rivers located 250 km northwest of Fort St. John (Crampton et al. 1997). Studies have also been conducted in the boreal mixedwood forests in northwestern Alberta (Patriquin and Barclay 2003), northcentral Alberta (Crampton and Barclay 1998) and northeastern Alberta (Hubbs and Schowalter 2003; Stefan 2004). Other studies that have documented bats in the area include Cowan (1939), Thurber (1976), Westworth (1998) and Hemmera (2006).
Cowan (1939) observed female big brown bats and silver-haired bats, in late pregnancy or lactating, in the Peace River area in mid-June. One little brown myotis was observed incidentally during surveys of the valley in 1974 and 1975 (Thurber 1976).
Roost-site preferences, abundance and diversity of bats were studied on Liard Highway, north of Fort Nelson in northeastern British Columbia from June to August 1997 (Vonhof et al. 1997). During mist net surveys, northern myotis, little brown myotis, long-legged myotis and long-eared myotis were captured. The most common species captured was the little brown myotis, followed by the northern myotis, long-eared myotis and long-legged myotis. Of the 39 bats
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Vonhof et al. (1997) also used radio-telemetry to locate roosting sites used by the northern myotis. Six adult female northern myotis were outfitted with radio-transmitters and tracked to 14 different roost trees. Eleven of the roosts were in cracks, three were abandoned cavities and one was beneath loose bark. Roost trees were primarily trembling aspen, but balsam poplar was also used. On average, northern myotis switched roosts every 1.4 days and alternate roosts were located within a 50 to 75 ha area.
Bat surveys were conducted in late July and early August 1997 in the Prophet River area (Crampton et al. 1997). In this study, mist nets and acoustic detectors were used to survey bats in four different habitat types: mature conifer stand, mature mixed wood, old forest conifer stand and immature stand. Total netting effort was 187.2 net-hours, with a capture success of 0.048 bats/net-hour or 0.75 bats/night. Little brown myotis and northern myotis were the only species captured in mist nets. All bats were captured in mature mixed wood and mature coniferous habitat by water sources. Myotis species, big brown bats and possibly silver-haired bats were detected acoustically during surveys. Myotis species made up the majority of the detections (84.1%). The highest amount of bat activity was detected in mixed wood forests.
Westworth (1998) completed a bat inventory in the Burnt River Landscape Unit, 60 km south of Chetwynd, in July 1998. Mist-netting and acoustic detection surveys were completed according to RISC standards (RIC 1998e). The capture rate was 0.5 bats/night and all bats caught were little brown myotis. Big bats (big brown bat and silver-haired bat) were detected at five sites and a hoary bat was detected at one site.
In 2006, acoustic detection and mist net surveys were conducted on Bear Mountain, located 14.5 km southwest of Dawson Creek (Hemmera 2006). Twenty-seven net-nights of sampling were completed in late August with an overall capture rate of 0.5 bats /net night. Five species were captured, including little brown myotis, northern myotis, big brown bat, long-eared myotis and long-legged myotis. The northern myotis and little brown myotis were the most common species captured. All bats captured were non-breeding adults. Acoustic surveys detected
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Californian Myotis (Myotis californicus)
The Californian myotis is generally considered to be a western species, ranging north to central BC and the Alaskan panhandle (Nagorsen and Brigham 1993). Wilkinson et al. (1995) reported this species in the Liard area, but review of measurements from that study have led to the belief that bats identified as Californian myotis were long-legged myotis that were mis-classified (Lausen 2006a). The Californian myotis has not been documented elsewhere in northeastern BC or in Alberta.
The Californian myotis uses rock crevices, tree cavities, crevices under the bark of trees, mine tunnels, buildings, and bridges for day roosts and maternity roosts (Nagorsen and Brigham 1993; Vonhof and Gwilliam 2007). Like other Myotis species, the Californian myotis is considered non-migratory and likely hibernates within several hundred kilometres of its summer range, although there are no known hibernacula in BC (Nagorsen and Brigham 1993). To date, winter specimens or records are all from southern British Columbia (Nagorsen et al. 1993).
Long-eared Myotis (Myotis evotis )
This species is considered a more southern and western counterpart to the northern myotis (Nagorsen and Brigham 1993). The long-eared myotis ranges across southern and central BC, and has been reported in the Liard area (Vonhof et al. 1997) and in Nahanni National Park Reserve in the Southwest Northwest Territories (Lausen 2006a). Genetic sampling in the southern Northwest Territories (Lausen 2006a), southern BC (Haney et al. 2002), and southern Alberta (Lausen 2006b) has confirmed overlap in the distribution of both the long-eared and northern myotis in these areas. Overlap between these species is also reported for the Liard area, but this has not been genetically confirmed (Vonhof et al. 1997). Differentiation between these two species is difficult using physical characteristics (colouration, size), thus confirmation requires genetic sampling (Nagorsen and Brigham 1993; Burles 2004). The long-eared myotis has been found roosting in buildings, under bark on snags, in caves, and in sink holes and fissures in south-facing cliffs (Kellner and Rasheed 2002; Nagorsen and Brigham 1993). Maternity colonies have been located in buildings (Nagorsen and Brigham 1993), in rocky
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Little Brown Myotis ( Myotis lucifugus )
The little brown myotis is widely distributed and common across most of western Canada (Nagorsen and Brigham 1993). It has been recorded in boreal forests in BC (Prophet River - Crampton et al. 1997; Liard area – Vonhof et al. 1997), the Yukon (Jung et al. 2006) and the Northwest Territories (Lausen 2006a), and in the mixedwood boreal forest across northern Alberta (Crampton and Barclay 1998; Hubbs and Schowalter 2003; Patriquin and Barclay 2003). Little brown myotis have been observed roosting in tree crevices and cavities, rock crevices, caves, human structures and under bark (Nagorsen and Brigham 1993; Psyllakis and Brigham 2006). This species has been found hibernating in caves and old mines, and there are several known hibernacula in central BC where individuals hibernate singly or in small groups (Nagorsen et al. 1993). Hibernacula have been located up to 200 km from summer roost areas (Nagorsen and Brigham 1993).
Northern Myotis (Myotis septentrionalis)
The northern myotis is currently Blue-listed (vulnerable) in BC and Alberta due to its perceived rarity, suspected requirement for mature and old forests and lack of information on distribution (BC CDC 2009; Caceres and Pybus 1997; Nagorsen and Brigham 1993). Its range includes the northcentral US and Canada east of the Rocky Mountains (BC CDC 2009). The northern myotis is believed to be associated with boreal forests although its distribution includes southern interior rainforest habitats (Haney et al. 2002).
In BC, locations of this species include Hudson’s Hope in 1931 (Nagorsen and Brigham 1993) and the Revelstoke area (southwest BC) in the 1980s (Nagorsen and Brigham 1993) and 1990s (Rasheed and Holroyd 1995; Caceres 1998). Recently, reproductive populations have been found at the Prophet River and in the Liard area in northeastern BC (Crampton et al. 1997; Vonhof et al. 1997; Vonhof and Wilkinson 2000) and in the southeastern Yukon (Lausen et al. 2008). Non-reproductive individuals (males and/or females) have been captured in the
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Roosting may occur in buildings and in trees, under loose bark or in cracks or crevices (Nagorsen and Brigham 1993; Broders and Forbes 2004; Garroway and Broders 2008). There are no known hibernacula or winter records in BC, but northern myotis in other areas are known to hibernate in caves and mines up to 56 km from summer roost areas (Nagorsen and Brigham 1993). Two hibernacula are known in Alberta, in Wood Buffalo National Park and in Cadomin Cave, near Jasper (Caceres and Pybus 1997).
Long-legged Myotis ( Myotis volans )
The long-legged myotis is widespread across southern and western BC, but has also been reported from northwestern and northern BC (Kispiox and Atlin) (Nagorsen and Brigham 1993), with a reproductive population reported in the Liard area (Vonhof et al. 1997). It is found in Alberta north to Jasper and Cadomin (Holroyd and Van Tighem 1983) and non-reproductive males and females were captured in the southwestern Northwest Territories (Lausen 2006a). The long-legged myotis has not been found in surveys of the mixedwood boreal forest in Alberta (Crampton and Barclay 1998; Hubbs and Schowalter 2003; Patriquin and Barclay 2003) or at the Prophet River in BC (Crampton et al. 1997). This species may roost in buildings, crevices in rock cliffs, fissures in the ground and under the bark of trees (Nagorsen and Brigham 1993). No hibernacula are known in BC, but it has been found hibernating in caves in Alberta (Nagorsen and Brigham 1993).
Silver-haired Bat ( Lasionycteris noctivagans )
The silver-haired bat has been captured in mixedwood boreal forests in Alberta (Crampton and Barclay 1998; Hubbs and Schowalter 2003; Patriquin and Barclay 2003). In northeastern BC, this species was not captured at the Prophet River (Crampton et al. 1997) or in the Liard area (Vonhof et al. 1997), but it was possibly heard on detectors. There is at least one earlier record of a silver-haired bat around the Peace River / Taylor area (Nagorsen and Brigham 1993). This
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Eastern Red Bat ( Lasiurus borealis )
A solitary, foliage-roosting bat of southern and eastern Canada and the United States, the eastern red bat was first documented in the Fort McMurray area of Alberta in 2001 (Patriquin 2001). Calls have recently been recorded in the same area (Stefan 2004) and calls were recorded and an “orange bat” was observed but not captured, in the southwestern Northwest Territories (Lausen 2006a). Calls have also been recorded in southern Alberta (Lausen 2006b). Occurrence of this bat in Alberta seems to be increasing and it has been hypothesized that its’ increasing range may reflect global climate change (Willis and Brigham 2003). This bat has not been recorded in BC, but is included as a potential species in the Peace River area based on the recent Alberta records and its affinity for boreal forests. The eastern red bat is a solitary species, and roosts alone in thick forest foliage (Alberta SRD 2008). Studies in other parts of its range show preference for deciduous trees for roosting (Hutchison and Lacki 2000). Eastern red bats are migratory, leaving Canada for the winter (Cryan 2003).
Big Brown Bat ( Eptesicus fuscus )
There are records of big brown bats from the Peace River/ Taylor area (Nagorsen and Brigham 1993), Jasper National Park (Holroyd and Van Tighem 1983) and southeast of Dawson Creek (Hemmera 2006). Calls have been reported in mixedwood boreal forests (Crampton and Barclay 1998; Hubbs and Schowalter 2003), in the Liard area (Vonhof et al. 1997), possibly at the Prophet River (Crampton et al. 1997), and in the boreal forest in the southwestern Northwest Territories (Lausen 2006a). In much of its range, this species prefers human structures, but it also roosts in tree cavities and rock crevices (Nagorsen and Brigham 1993; Lausen and Barclay 2006a; Metheny et al. 2008). Big brown bats hibernate in British Columbia, and solitary individuals or small groups have been found in caves, mines and houses, including 1 record from Prince George (Nagorsen et al. 1993). Recent studies on
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Hoary Bat ( Lasiurus cinereus )
The hoary bat is another solitary foliage-roosting bat that has been captured and recorded in mixedwood boreal forests in central and eastern Alberta (Crampton and Barclay 1998; Hubbs and Schowalter 2003), in the Liard area (Vonhof et al. 1997) and in the southwestern Northwest Territories (Lausen 2006a). The hoary bat was not recorded at the Prophet River (Crampton et al. 1997) and is generally found in the southern half of BC (Nagorsen and Brigham 1993). This bat roosts in the branches of live coniferous and deciduous trees and shrubs (Nagorsen and Brigham 1993; Willis and Brigham 2005) and is migratory. It is believed to travel north in June and south out of Canada from mid-August through October (Nagorsen and Brigham 1993; Cryan 2003).
2.8.3 Methods
Survey methods used in 2008 followed the BC Resource Inventory Standards Committee’s (RISC) Inventory Methods for Bats (RIC 1998e). Bat capture was permitted under Ministry of Environment permit FJ08-44000, which authorized the live trapping and on-site release of bat species for identification and radio tagging purposes in Region 7B.
Assumptions
Assumptions inherent in the study methodology described below include:
For acoustic detection (these and other considerations are raised by Menzel et al. (2005), Weller et al. (1998), Sherwin et al. (2000), and Gannon and Sherwin (2002)):
• A pass was defined as a series of at least two calls (Thomas 1988); • Each pass was considered an independent event of crossing in the path of a microphone; • The numbers of bat passes was positively correlated with activity levels of bats, but not necessarily numbers of bats, in a particular habitat;
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• Habitat was stratified only in two dimensions, as detectors were placed at only one height; • Species groups were equally and consistently detectable across all habitats, • All detectors detected calls equally well across all habitats; • Variations in the rate of calling occurred only in response to the habitat variable, and occur at the scale of analysis (e.g. phenology or behavioural and interspecific interactions do not affect rate of calls); and • Identification to species group could be made based on call characteristics.
For radio-telemetry to locate roost habitat:
• Radio-tagged bats did not alter their behaviour in response to capture, radio-tagging, or tracking, • Each roost tree was considered independent; • Roost habitat use by conspecifics was similar within reproductive/non-reproductive groups, allowing data to be pooled for analysis; • Capture sites were foraging areas and bats ‘commuted’ between foraging and roosting areas; and • The commuting distance between foraging sites (capture locations) and roosting areas was an approximate measure of the radius of the home range of a bat.
For the study in general,
• Any conclusions reflect local patterns of species distribution and habitat use and extrapolation beyond the local study area should be interpreted with caution.
2.8.3.1. Inventory Methods
Survey methods included acoustic detection to determine relative activity in habitat units (defined from the TEM), mist-netting to determine species presence, and radio-telemetry to investigate day-roost selection in the Peace River Corridor. The potential for hibernacula within the potential Site C reservoir was also investigated. All surveys were completed in the PRC study area and a reconnaissance survey was completed in the TL study area. Sampling occurred in two sessions to document relative activity and habitat use in TEM habitat units
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(session 1) and to investigate potential hibernacula and document the change in activity levels as bats become less active and possibly leave the study area to hibernate or migrate (session 2).
Bat Capture
Mist-netting occurred at suitable sites to document species presence and radio tag individuals to locate roost sites. Surveys were completed according to Inventory Methods for Bats (RIC 1998e). Three to seven nets, measuring 2 m high by 6, 9 or 18 m wide, were used at each site. Mist nets were set up across slow-moving creeks, ponds, wetlands, forest gaps, and forest trails.
Nets were opened at dusk (20:30 – 22:30), monitored approximately every 10 minutes and closed when bat activity declined (often around 01:00). A net-night is a standard measure of effort and is defined as one 2x6 m net-equivalent set up for 1 night (RIC 1998e); thus the 18 m net resulted in 3 net-nights of effort for each night it was used. Net hour is another measure of effort and is equivalent to the total hours that each net was open for each site.
Captured bats were removed from nets promptly and most were kept in cloth bags for at least one hour to allow food to clear the digestive tract. Females that were lactating or in the late stages of pregnancy were processed and released immediately after capture. Since not all bats were held for the requisite hour to allow food to clear their digestive tract, the recorded weights may be higher than average. For each bat captured, the weight, sex, age class, reproductive condition, forearm length (mm), and presence/absence of a prominent keel on the calcar were recorded. Foot length (mm) was also recorded for some bats, to aid in species identification. Reproductive condition was determined for males by the presence of enlarged testes, and for females, by visual examination and gentle palpation of the abdomen and nipples (Racey 1998). Age was determined based on the degree of ossification of the finger joints. The identification key in Nagorsen and Brigham (1993) was used to confirm species. Bats were released on-site by allowing them to fly off the hand.
Acoustic Detection
Acoustic sampling with bat detectors was used to verify bat activity, quantify activity levels, and to document the presence of species or species groups that were not captured. Remote bat
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Site C Hydro Project Stage 2 Vegetation and Wildlife Report detectors were used to obtain data on the relative activity of bats in different habitat types. Ultrasound detectors (Anabat II and Pettersson D230) and digital recorders were deployed in a wide range of forested and wetland ecosystems (TEM units) to provide information on the relative activity level of bats in each ecosystem unit. Two Anabat II units with ZCAIM were also used. At each site, a single broadband detector coupled with a digital recorder was placed one to two m above the ground, pointing upwards at a 45-degree angle. Detectors were placed in homogeneous habitat patches. In forested sites, sites with small gaps, representative of those found in the stand, were targeted if present. Bat activity was recorded for 1 to 10 hours, starting at the time of sunset calculated for Fort St. John by Environment Canada.
One to eight sites were sampled each night, in different TEM habitat units. Each site was sampled once, in a session and select sites were sampled in both sessions. Efforts were made to distribute the sampling of habitats across the session, to randomize any effects of nightly temperature on activity. Sampling sessions were of variable length due to factors such as night length, weather and equipment malfunction.
Digital recording were transcribed by a biologist and activity was recorded in five-minute intervals. The number of passes and feeding buzzes were recorded for two species groups: Myotis species (potentially including little brown, long-legged, long-eared and northern) and big bats (potentially including silver-haired, big brown, eastern red and hoary bats). Myotis and big bats calls were distinguished based on the call charactristics. A pass was defined as an uninterrupted series of at least 2 echolocation calls as a bat traveled past a microphone and a buzz was the buzzy sound of accelerating calls as a bat homed in on its insect prey.
Radio-telemetry
Bats were radio-tagged to locate day roosts used by bats and to identify habitat types used for roosting. Initially, female northern myotis were targeted for radio-tagging, but low capture success resulted all species being considered for radio-tagging. Radio-tagging of early- pregnancy or lactating females was a priority in order to locate maternity colonies. Transmitters were attached to individuals that met criteria (RIC 1998e) for species, gender, reproductive condition, and the 5% rule, which suggests that transmitters should not exceed 5% of the animal’s body mass (Nagorsen and Brigham 1993). The minimum weight of radio-tagged bats was 7.4 g based on the weight of the transmitters (0.37 g).
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Bats were tagged by clipping hair, if required, in the area below the scapulae where the transmitter was to be attached. A small amount of Skin Bond ® was applied to the clipped area and to the transmitter, and allowed to stand until it bubbled. The transmitter was then placed on the bat and held in place for three to five minutes. Bats were released on-site once the glue had set. Holohil Systems BD-2N transmitters were used and each bat that could be relocated was tracked for a minimum of 8 days. The transmitters had an expected battery life of 8 to 15 days, but could potentially be removed by the bat at any time through grooming activity.
Roosts were found by relocating the bat every 1 to 2 days from a boat or vehicle, followed by walking up to the roost structure on foot. Habitat type was recorded (site series and structural stage) on a RISC standard ground inspection form (GIF), for all accessible roosts. If the site was inaccessible (e.g., across the Peace River), the signal was triangulated from two or more locations and, if feasible, visited by shortly thereafter to locate the roost, if transportation to the site was available. If inaccessible, a UTM location was obtained for the roost based on triangulation data and the habitat was determined from the TEM map (Keystone Wildlife Research 2006a). Most polygons were also visited on subsequent days to confirm the habitat type.
Roost trees were described using the methodology for describing wildlife trees in the Field Manual for Describing Terrestrial Ecosystems (BC MWLAP and BC MoF 1998). The tree species, diameter at breast height, estimated height, percentage bark remaining, crown class, appearance class, crown condition class, bark retention class and wood condition class were recorded for each roost tree.
Investigation of Potential Hibernacula
An overview flight of the river corridor, between the potential Site C dam site and Peace Canyon dam, was completed to identify potential hibernacula such as deeply fissured rock outcrops. Two observers ranked available habitat for its potential suitability for hibernacula, based on the presence of stable or semi-stable cutbanks or rock outcrops with visible cracks or fissures. Suitable sites were resurveyed on foot to confirm suitability and identify signs of use. Two remote acoustic detectors (Anabat II with ZCAIM) were set up at the most visibly suitable and accessible locations to monitor activity from late August though mid-October. Because bats
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2.8.3.2. Habitat Suitability Mapping
Draft species models and ratings tables were prepared for bat species as a group since species-specific habitat preferences cannot be represented at this scale. Highest-rated habitats for roosting included cutbanks, mature and old balsam poplar forest and young, mature and old aspen forests. Water bodies (open water, river, reservoir, pond and lake), wetlands and old forests were rated highest for foraging.
2.8.3.3. Analysis
Acoustic Detection
Analysis of acoustic data was used to determine the presence of hoary bats in the study area, since this species is known to occur in the area but was not captured in 2008. Hoary bats have easily identifiable calls and calls recorded with the Anabat system were analyzed in search of hoary bat calls using AnalookW 3.3q software. Criteria used for attributing calls to hoary bats were:
• minimum frequency of 18 – 20 kHz, low slope of call (Keinath 2008),
• sweep (change in frequency throughout a call) usually from 25 – 20 kHz (Fenton et al. 1983),
• inconsistent minimum frequency within a sequence (O’Farrell et al. 1999),
• comparison with reference recordings obtained from various sources.
Mapped site series were grouped into biologically-relevant groups (Table 2.8.3.3a) for comparison of activity across TEM units (Appendix 3a), because it was logistically impossible to obtain sufficient sample size at all mapped site series and age classes. Forested sites were grouped based on moisture regime since this influences the species and size of trees present and may influence the abundance of insects for foraging. Moisture regimes included Moist (MO), Mesic (ME) and Dry (DR). Where sample sizes were sufficient, forests were also subdivided into deciduous (d) or coniferous (c) forests. Two site series, the moist riparian Fm02 unit and the moist coniferous SO unit, had sufficiently large sample sizes to be assessed
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Site C Hydro Project Stage 2 Vegetation and Wildlife Report individually. Structural stage (4, 5 or 6) was also recorded in the field and relative use of these age classes (Appendix 3b) was assessed where sufficient sample sizes were available.
Non-forested sites were separated into 7 groups based on the habitat type and the expected influence of the Peace River (Table 2.8.3.3a). The “open water” group (OW) includes wetland, lake and creek sites (SE, WH, WS site series) not influenced by the Peace River. Detectors placed in “open water” habitats typically sampled a matrix of open water and adjacent vegetation. The “river” and “backchannel” groups include sites that may be influenced by the fluctuating water levels of the Peace River due to upstream dam activity (Peace Canyon dam and W.A.C. Bennett dam). The backchannel group included riparian wetland and open water (WS and OW site series) sites where the detector was set up over vegetation, in a backchannel or adjacent to the Peace River. The river group included river and gravel bar (RI and GB site series) sites where the detector was set up over or immediately beside the Peace River. Other non-forested units were grouped into general habitat types of cutbank (CB), cultivated field (CF), and grassland (GR).
Table 2.8.3.3a. Habitat groupings for analysis of relative activity of bats in the Peace River Valley.
Mapcode* Group name Grouped code TEM habitat type name* Pine – Lingonberry LL Dry coniferous forest DRc/d Spruce - Wildrye – Peavine SW Dry coniferous forest DRc/d $ Aspen – Soopolallie - Fuzzy-spiked SW:as Dry deciduous forest DRc/d Wildrye Spruce - Aspen – Rose AM Mesic coniferous forest MEc/d $ Aspen – Rose – Showy aster AM:ap Mesic deciduous forest MEc/d Spruce – Cranberry SO Moist coniferous forest: SO SO Black Spruce - Labrador tea – BT Moist coniferous forest: other MOc: other Sphagnum Spruce – Dogwood SC Moist coniferous forest: other MOc: other Spruce – Horsetail SH Moist coniferous forest: other MOc: other Balsam Poplar – Horsetail – Floodplain Fm02 Moist deciduous forest: Fm02 Fm02 $ Balsam Poplar – Dogwood SC:ab Moist deciduous forest: other MOd: other $ Balsam Poplar – Horsetail SH:ac Moist deciduous forest: other MOd: other
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Mapcode* Group name Grouped code TEM habitat type name* $ Paper birch – Dogwood SC:ep Moist deciduous forest: other MOd: other Cultivated Field (includes grazed CF Cultivated field CF transmission ROW) Fuzzy-spiked Wildrye - Wolf willow WW Grassland GR Lake LA Open water OW
Cliff CL Cutbank CB Cutbank CB Cutbank CB Open water or River (depending Open Water OW OW or RI on proximity to river) River RI River RI Gravel bar GB River RI Open water or Backchannel OW or Sedge Fen SE (depending on proximity to river) BK Willow – Horsetail – Sedge – Riparian Open water or Backchannel OW or WH Wetland (depending on proximity to river) BK Open water or Backchannel OW or Willow – Sedge – Wetland WS (depending on proximity to river) BK * see Appendix 3a for definitions of TEM units.
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Timing of Use
The timing of bat activity was determined using data from 13 sites, sampled over 3 nights (July 15 to 17, 2008). This subset was selected because sampling began before dusk and continued successfully until 02:30, at all thirteen sites. Pre-dusk sampling did not record any bats, so sampling sessions were truncated to 22:00, just prior to the first recorded bat call. The sites were grouped into forested and riparian (non-forested) habitat types for the activity analysis. For each group (forested or riparian), the proportion of calls in every 5-minute interval was calculated as the total number from all sites within the group, for that interval, divided by the total number of calls for that habitat (forest: 196 calls from 22:00 – 02:30, riparian: 204 calls from 22:00 – 02:30). Activity patterns in forested versus riparian habitats were determined by plotting the proportion of calls at 5-minute intervals throughout the sample sessions.
Relative Activity
The numbers of bat passes and foraging buzzes recorded by the detectors were analyzed to give an index of relative bat activity in the different habitat groups. The activity rate was determined for each site as the average number of calls (passes and buzzes), per sampling period (2 hours post-sunset). Foraging rate was also determined as the average number of feeding buzzes per sampling period.
Relative activity was compared between habitat groups and structural stages. For analyses, recordings were truncated to include only the first 2 hours post-sunset, in order to include as many samples as possible while maintaining a reasonable session length. Relative activity was analyzed graphically, by plotting the total activity in each habitat group. Box plots were used to illustrate the distribution of non-normal data. Box plots use a bar to identify the mid-point of a dataset, a central box to show the distribution of the central half of the dataset, two whiskers extending from the box to encompass ninety percent of the data points, and dots to show the values of remaining outliers. Because the data was expected to have an unusual distribution, non-parametric methods of analysis were used. G-tests were used to compare the distribution of calls between species and the number of bat calls (relative activity) was compared across habitat groups using Kruskal-Wallis and Mann-Whitney tests (Swystun et al. 2007; Zar 1999). These tests provide a measure of how likely the observed result is to occur by chance. A
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Radio-telemetry
Radio-tracked bats of each species were divided into two groups for analysis. The “reproductive” group included pregnant, lactating, or post-lactating female bats and the “non- reproductive” group included male bats and apparently non-reproductive females. No juvenile bats were radio-tagged. Analysis was completed for each reproductive group for each species captured.
The maximum commuting distance was determined for each radio-tracked species and reproductive group, as the distance between the capture site and the furthest roost location for an individual. ArcGIS 9.2 was used to determine the average roost location as a single roost, the midpoint between two roosts, or the centre of a minimum convex polygon for bats with three or more roosts. A circular buffer with a radius equal to the maximum commuting distance was created around each average roost location to approximate the home range area for each bat. This "circle method" was used to delineate available habitat at the stand scale for each bat (Joly et al. 2003). The area (ha) of each available habitat (ecosystem unit and structural stage) was then calculated for each home range.
The habitat summaries were calculated from the TEM map and from the 1:50,000 biophysical mapping when the available habitat area extended outside of the TEM mapped area. Ecosystem units with little to no potential to provide roosting structures (non-forested units and structural stage 2 forested units) were excluded from the analysis of available habitat (Appendix 3a).
Forested ecosystem units were grouped by structural stage based on their ability to provide suitable roosting structures. Structural stages 3 and 4 include shrub-dominated and pole- sapling forested sites, less than 40 years old (Appendix 3b). These structural stages are unlikely to provide suitable roosting microsites and were grouped. Structural stages 5, 6, and 7 include young, mature and old forests (>40 yrs old) and are more likely to contain snags or trees with cavities and other defects. The selection ratios were calculated for each available habitat type as per Manley et al. (2002).
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Potential hibernacula
Nightly recordings at the two potential hibernacula were made from August 28 to October 4, 2008. The number of call files in a recording was used as an estimate of the number of passes and therefore represents the amount of bat activity each night at each site. A subset of nightly recordings was analyzed by a biologist to determine the actual number of bat passes contained within a recording and the species present. The actual number of passes was compared to the number of call files in a recording to verify that the number of files represents the number of bat passes. The proportion of calls identified as Myotis and big bat species was also determined for the subset of recordings. Myotis calls were distinguished from big bat calls based on the minimum frequency and shape of the call. The number of call files was plotted over time to identify potential swarming activity and to provide information on how bat activity changes in the fall. Subsets of the recordings were also analyzed in Analook software to determine the latest date that bats within each species group ( Myotis and big bats) were active at each site.
2.8.4 Results
Results of 2008 surveys and a compilation of data from surveys completed between 2005 and 2008 are reported below. Data from previous surveys are included when available from original databases or reports. The locations of bat surveys completed in 2005, 2006 and 2008 are shown on Maps 2.8.4a and 2.8.4b.
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Map 2.8.4a. Bat survey locations.
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Map 2.8.4b. Bat survey locations.
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2.8.4.1. 2008 Inventory Surveys
Mist-netting, acoustic sampling and radio-tracking of tagged bats occurred from July 15 to August 2, 2008 in the Peace River corridor (PRC). Assessment of potential hibernacula, assessment of bat habitat around the transmission line (TL), and late-season acoustic sampling occurred from August 27 to 31, 2008. Acoustic monitoring of two potential hibernacula took place between August 28 and October 4, 2008.
Capture rates
Twelve nights of netting were completed over 9 calendar nights by 2 crews. Eight sites were sampled, some repeatedly, in efforts to catch bats for radio-tagging. Conditions were generally favourable with temperatures at sunset above 5°C and no heavy precipitation during sampling. Wind speed was classed as 3 on the Beaufort scale on 1 night but the wind calmed to 2 by the end of the survey. On nights with wind, nets were placed to minimize exposure to the wind to reduce net movement.
Sixty-nine bats were captured in 89.5 net nights, for a capture rate of 0.77 bats per net night (Table 2.8.4.1a; Appendix 9a). Excluding data from sampling at a known night roost (Farrell Creek), where capture success was higher than average, the capture rate was 0.29 bats per net night.
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Table 2.8.4.1a. Summary of sampling effort and capture rates for each sampling site in the Peace River Corridor in July 2008.
Number of Number of nights bats Net Bats per Sample Station Stratum sampled captured hours Net nights net night Alces River Open water – creek 1 1 11.5 5.0 0.20 Cache Creek Open water - creek 3 9 57.2 21.0 0.43 Cottonwood Backchannel / Moist Campsite deciduous forest 1 8 30.0 10.0 0.80 Farrell Creek night roost Open water - creek 3 49 69.3 20.0 2.45 Backchannel / Moist Limestone Campsite deciduous forest 1 0 24.9 6.0 0.00 Lynx Creek Open water - creek 1 2 24.5 9.0 0.22 Moberly Backchannel Backchannel – river 1 0 20 10.0 0.00 Watson Slough Open water - wetland 1 0 12.3 8.5 0.00 Total 12 69 249.7 89.5 0.77 Total excluding captures at Farrell Creek night roost 9 20 180.4 69.5 0.29
Species Presence
Sixty-nine bats were captured of six species, including 56 little brown myotis, 1 long-eared myotis, 5 long-legged myotis, 1 northern myotis, 3 big brown bats and 2 silver-haired bats (Table 2.8.4.1b). One Myotis species escaped during handling and the species was not determined.
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Table 2.8.4.1b. Bat species captured in mist-nets along the Peace River Corridor in 2008.
Little Long- Big Brown Silver- Long-eared Northern Unknown Date Brown legged Total Bat haired Bat Myotis Myotis species Myotis Myotis 16-Jul-08 8 8 17-Jul-08 1 1 2 18-Jul-08 1 2 3 19-Jul-08 2 1 1 2 6 20-Jul-08 33 1 4 38 21-Jul-08 1 1 22-Jul-08 2 2 23-Jul-08 8 1 9 Total 3 2 1 56 1 5 1 69
Acoustic sampling
Acoustic sampling was conducted in 2 sampling sessions (July 15 to 31 and from August 28 to 31, 2008) in the Peace River Corridor and Transmission Line. Sampling was conducted at 79 sites in the first session and 14 sites in a second session, including reconnaissance at 4 sites in the TL study area on August 29.
The quality of the recordings varied, with background noise (due to wind and/or rain) affecting the ability to detect bats on some recordings. Length of the recordings also varied, with data from several nights being truncated due to technical difficulties. Only samples greater than 2 hours and of sufficient quality to identify bat calls were included in the analysis of relative activity (section 2.8.4.2).
A subset of call files from the anabat/ZCAIM untis was analyzed to try to confirm presence of the hoary bat in 2008, as that species was not captured. Overall, 1276 call files were analyzed from 10 sites (Table 2.8.4.1c), with none of the files positively identified as hoary bat calls.
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Table 2.8.4.1c. Number of Anabat call sequences analyzed and number of sites sampled for activity of hoary bats in 2008.
Survey timing Number of calls analyzed Number of sites sampled July 27 – 31, 2008 347 8 Aug 30 – 31, 2008 929 2 Total 1276 10
Radio-telemetry
Thirteen adult bats were radio-tagged between July 19 and 23, 2008, including eleven reproductive female bats and two males (Table 2.8.4.1d). Five species were tagged: two big brown bats, one silver-haired bat, seven little brown myotis, two long-legged myotis and one northern myotis. Eight bats were relocated and tracked between July 19 and August 2, 2008. Five bats could not be relocated (no signal detected), including one female northern myotis, two female long-legged myotis and two female little brown myotis. Due to the number of tagged bats and their distribution across the study area, nightly roost-watches could not be completed to confirm that the transmitter was still attached to the bat.
The eight bats were tracked to 24 roost stands, and 22 roost structures were identified within those stands. The remaining two roost structures could not be identified due to logistical difficulties, but the roost stands were located by triangulation. The roost structures included 16 balsam poplars ( Populus balsamifera ), 5 trembling aspen ( P. tremuloides ) and one cutbank.
Table 2.8.4.1d. Species, gender, reproductive condition, duration of tracking, and minimum number of roosts used by 13 bats radio-tagged in the Peace River Corridor in 2008.
Capture Days Minimum # of Bat ID Bat species Sex Reproductive status* date tracked roosts used 19-Jul SWE Big brown bat F Reproductive - L 14 5 22-Jul BET Little brown myotis F Reproductive - L 11 6 20-Jul LUC Little brown myotis F Reproductive - L 12 2 23-Jul OPA Little brown myotis F Reproductive - L 2 1 23-Jul RUB Little brown myotis F Reproductive - L 9 3
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23-Jul MOL Little brown myotis F Reproductive - P 0 n/a 23-Jul BAB Little brown myotis F Reproductive - P 0 n/a 20-Jul PRI Long-legged myotis F Reproductive - P 0 n/a 20-Jul VIC Long-legged myotis F Reproductive - P 0 n/a 20-Jul SAL Northern myotis F Reproductive - P 0 n/a 19-Jul LIL Silver-haired bat F Reproductive - P 13 3 19-Jul GOO Big brown bat M Not-reproductive** 14 3 19-Jul ALN Little brown myotis M Not-reproductive** 7 1 *Reproductive – L : lactating, Reproductive – P : pregnant; **Apparently reproductively capable, not currently in a state of potency (testes not enlarged).
Potential hibernacula
One overview flight of the river corridor was completed between the potential Site C dam site and Peace Canyon dam on August 27, 2008. Two observers in a helicopter assessed habitat along the corridor for suitability as potential hibernacula based on the stability of the substrate and the presence of any cracks or fissures. The sites with the most potential were revisited by boat or on foot on August 28, 29, and 30, 2008, to further investigate suitability and to examine sites for signs of use.
Most sites along the river corridor appeared to have little to no suitability for hibernacula. There are no historical or active mine adits in the Peace River Corridor, nor are any caves known. The side slopes of the Peace River are dominated by cutbanks that are subject to frequent erosion and do not provide a stable substrate for hibernating bats. Thirteen sites were considered to have moderate to high suitability for hibernating bats. No suitable sites were located in the potential Site C reservoir and most suitable sites were located upstream of Halfway River. Two sites were located closer to the potential Site C dam site, but these were higher elevation cliffs outside of the potential Site C reservoir. No signs of use were visible at suitable sites visited on the ground.
Two sites assessed as having high potential to provide hibernacula were selected for long-term monitoring, and detectors were deployed on August 28 (B-122, a limestone outcrop immediately above the Peace River, near Hudson’s Hope) and August 30 (B-121, an outcrop of sedimentary rock above a small wetland) and left on site until October 4, 2008 (Table 2.8.4.1e).
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Table 2.8.4.1e. Detector site labels, dates that detectors were deployed, and numbers of files generated by remote Anabat detectors, at 2 potential hibernacula in 2008.
Detector Start date End date # Nights monitored # Call files B-122 – limestone Aug 28 Oct. 4 38 8826 B-121 – sedimentary Aug 30 Oct. 3 35 2081
2.8.4.2. Multiple Year Data Analysis
Two studies were completed in the Peace River Corridor (PRC) in 2005 and 2006 to determine species presence, use of roosting habitat and relative activity in roosting/ foraging areas (Kellner and Simpson 2005, 2006). Data from these studies have been included in this report where applicable.
Capture Rates
Mist-netting to inventory bat species occurred during four sampling periods: August 22 to 29, 2005, July 10 to 17, 2006, July 28 to August 4, 2006, and July 15 to 23, 2008. Overall, 34 nights of netting were completed, 8 in 2005, 14 in 2006 and 12 nights in 2008.
In total, 104 bats were captured in 269 net-nights of effort or 462 netting hours, completed over 34 evenings at 13 different sites (Appendix 9a). This effort resulted in an overall capture rate of 0.39 bats per net night. Three nights were spent netting at a night roost, to capture reproductive females for the radio-tagging program. Capture success at this site (2.45 bats per net night) was extremely high relative to other sites. Inclement weather conditions, defined as temperature at sunset <5°C, precipitation heavier than drizzle, or strong wind (Beaufort 3 or above) (RIC 1998e), were experienced on six evenings in 2005 and 2006, accounting for 42 net nights. Excluding nights with inclement weather and nights at the night roost results in a more representative capture rate of 0.24 bats per net night.
Species Presence
Over the three years, 104 bats of seven species were captured, including little brown myotis, long-eared myotis, long-legged myotis, northern myotis, big brown bats, silver-haired bats, hoary bats, and 1 unknown Myotis that escaped during handling (Table 2.8.4.2a). All species were confirmed to be reproducing in the area, based on the capture of juveniles or pregnant or
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lactating females (Figures 2.8.4.2a and 2.8.4.2b). The majority of bats captured were adult females, possibly reflecting sexual segregation of females in warm valley-bottom habitats (Barclay 1991; Senior et al. 2005).
Table 2.8.4.2a. Summary of bat species captured during four survey periods in 2005, 2006, and 2008.
Big Little Long- Long- Silver- Northern All Sample period brown Hoary bat brown eared legged haired myotis species bat myotis myotis myotis bat Aug 22 – 29, 2005 5* 2* 1 8 Jul 10 -17, 2006 1 1* 7* 1* 4* 14 Jul 8 - Aug 4, 2006 1 1 8* 2* 1* 13 Jul 15 -23, 2008 3* 56* 1* 5* 1* 2* 68 All periods 5 2 76 1 7 5 7 103 *reproductive population documented with the capture of one or more reproductive females and/or juveniles.
80 70 Juvenile 60 Adult 50 40 30 20 Number of bats Number 10 0 Long- Little Northern Long- Silver- Big Hoary eared brown myotis legged haired brown bat myotis myotis myotis bat bat
Species
Figure 2.8.4.2a. Numbers of adult and juvenile bats captured, by species, in 34 nights of netting completed in 2005, 2006 and 2008.
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60 Female 50 Male 40
30
20 Number of bats 10
0 Long- Little Northern Long- Silver- Big Hoary eared brown myotis legged haired brown bat myotis myotis myotis bat bat Species
Figure 2.8.4.2b. Numbers of female and male bats captured, by species, in 34 nights of netting completed in 2005, 2006 and 2008.
Although, long-eared bats (northern myotis, specifically) were targeted for study, only 6 (5.8%) were captured (Table 2.8.4.2b). Results indicate that both long-eared species (northern myotis and long-eared myotis) are present and reproducing in the study area. The range of these two similar species was believed to be spatially segregated (Nagorsen and Brigham 1993), but recently the long-eared myotis has been documented from northeastern BC (Crampton et al. 1997; Vonhof et al. 1997), southeastern Yukon (Jung et al. 2006; Lausen et al. 2008) and the southwestern Northwest Territories (Lausen 2006a). Genetic analysis would confirm these field calls.
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Table 2.8.4.2b. Capture location and date, suspected species, age, gender, and measurements of long-eared bats captured from 2005-2008.
Forearm Weight length Ear length Capture location Date Species Age Gender (g) (mm) (mm) Cache Creek 25-Aug-05 Northern myotis A M 6.3 39.0 15 Cache Creek 13-Jul-06 Northern myotis A F1 7.6 38.8 n/a Lynx Creek 30-Jul-06 Northern myotis A M 5.5 35.6 n/a Farrell Creek 31-Jul-06 Northern myotis J M 5.6 36.7 n/a Long-eared n/a Cache Creek 19-Jul-08 myotis J F 7.3 37.6 Farrell Creek 20-Jul-08 Northern myotis A F2 8.5 37.5 n/a 1Lactating female; 2Pregnant female.
The species most commonly captured in each sample period and overall was little brown myotis, accounting for 72% of all bats captured at all sites, and 58% of all bats captured away from the Farrell Creek night roost (Figure 2.8.4.2b). This may be due to the species’ relative abundance, but also likely reflects its generalist habits and its relative ease of capture (Nagorsen and Brigham 1993).
No Californian myotis were captured. Although this species was reported from the Liard River in northern BC (Wilkinson et al. 1995), those records were excluded from the recently released provincial range maps for this species (BC Ministry of Environment 2008) since the reported forearm measurements suggest that the bats identified as Californian myotis were actually long- legged myotis (Lausen 2006a). Other than the Liard report, the most northern record of this species in the BC interior is at Wells Grey Park, east of Williams Lake (Nagorsen and Brigham 1993). On the BC coast, the most northern records is at Kitsumkalum Lake, north of Terrace (BC Ministry of Environment 2008).
Eastern red bats were also not captured or detected. Although calls tentatively identified as eastern red bats were heard on detectors at one site (Cache Creek) in 2005, eight nights of mist-netting and concurrent detector sampling at this site in 2006 and 2008 did not provide any further evidence of this species’ presence. The closest recorded location for this species is in the Fort McMurray area of northeastern Alberta (Stefan 2004). The presence of the Californian myotis and eastern red bat would represent significant range expansions for both species. The current study indicates that these species should be deleted from the list of potential species for the area.
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During sampling between July 10 and August 29, in 2005, 2006 and 2008, pregnant females were detected from July 13 to July 23, with one unusually-late pregnant female captured on August 26. Lactating females were detected from July 11 to July 28 and post-lactating females were detected from July 17 to August 25 (Table 2.8.4.2c). In Canada, bat pregnancy is expected to occur shortly after females leave the hibernacula, with offspring born in June and July (Nagorsen and Brigham 1993). The presence of pregnant females in late July, plus the occurrence of the one pregnant individual in August, suggests that females are reproductively active over a wide time period, with a varied schedule of parturition.
Table 2.9.4.2c. Earliest and latest calendar dates for captures of pregnant, lactating, and post-lactating female bats, by species, in 2005, 2006, and 2008.
Reproductive status Species Pregnant Lactating Post-lactating Earliest Latest Earliest Latest Earliest Latest Big brown bat 18-Jul 19-Jul Hoary bat 13-Jul Silver-haired bat 13-Jul 19-Jul 21-Jul 28-Jul 23-Jul/ Little brown myotis 13-Jul 26-Aug 1 11-Jul 23-Jul 17-Jul 25-Aug Northern myotis 20-Jul 13-Jul Long-legged bat 20-Jul 1Two dates are given for the little brown myotis – the first is the final capture of a pregnant bat under “expected” timelines of pregnancy; the second is an unusual record from late in the year.
Acoustic detection
Acoustic sampling occurred during five sampling periods: August 22 to 29, 2005, July 10 to 17, 2006, July 28 to August 4, 2006, July 15 to 31, 2008 and August 28 to 31, 2008. To minimize external influences on results (annual and seasonal variation), only data collected between July 15 and 31, 2008 were used in the following analyses.
Timing of Use
Analysis of activity data from 13 sites was completed to determine the timing of bat activity in mid-July. Sites included 9 forested sites (1 DRc/d, 3 MEc/d, 2 SO, 3 Fm02) and 4 riparian sites (3 BK, 1 RI) (Table 2.8.3.3a). The total number of calls recorded between 22:00 and 02:30 in the forested and riparian sites was 196 and 204 calls, respectively.
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Bat activity at forested and riparian sites began 30 and 50 minutes post-sunset, respectively (Figure 2.8.4.2c). The earlier activity in forests reflects the emergence of tree-roosting bats at dusk, which may forage near the roost before dispersing to other sites. Similarly, the later activity at riparian sites indicates that these sites are used for foraging and not for roosting.
Bat activity in both forested and riparian habitat types had dwindled by 00:15, just over 2 hours after activity began. The first 2 hours of the 4.5 hour sampling period included 89% of calls recorded at forested sites and 70% of calls recorded at riparian sites (80% of all calls recorded during the sampling period for both groups combined). These data represent timing of use for mid-July and bat activity may vary throughout the season (Zimmerman and Glanz 2000), therefore these results should not be extrapolated to other time periods.
18 16 Forest - 9 sites 14 Riparian - 4 sites 12 10 8 6
Percentage of Percentage all calls 4 within habitateach type 2 0 22:00 22:30 23:00 23:30 0:00 0:30 1:00 1:30 2:00 Time (5-min. intervals)
Figure 2.8.4.2c. Bat activity recorded over 5 minute intervals between 22:00 and 2:30, within 9 forested and 4 riparian sites sampled on July 15- 17, 2008.
Relative Activity
Relative activity was analyzed for habitat groups and structural stage. A 2-hour sample period, starting 20 minutes after sunset, was used for the analyses of activity levels. Recordings with less than 2-hours of data (unsuccessful) due to noise interference or technical difficulties were
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Site C Hydro Project Stage 2 Vegetation and Wildlife Report excluded. Sixty-two sites were sampled successfully between July 15 and 31, 2008 and these data were used to determine bat activity in each grouped habitat type (Table 2.8.4.2d). It should be noted that restricting analyses to 2 hours truncates a larger proportion of activity from riparian than from forested sites, based on results in Figure 2.8.4.2c.
Table 2.8.4.2d. The number of sites successfully sampled for two hours post- sunset, within each of the grouped habitat types.
Number of successful / unsuccessful Site type Habitat Group acoustic samples July 15 to 31 August 28 to 31 DRc/d 8 / 2 0 MEc/d 7 / 5 1 SO 8 / 2 0 Forested MOc 6 / 1 0 Fm02 7 / 1 2 MOd 4 0 OW 7 / 3 5 / 4 RI 8 0 Non-forested BK 5 / 3 1 GR 1 0 CF 0 1 CB 1 2 Total 62 / 17 12 / 4
In total, 2455 calls were recorded in the 2-hour sampling periods. Forty-four calls (1.8%) were identified as bat calls but could not be assigned to a species group, and were excluded from analyses, leaving 2411 calls for analyses (Appendix 9b). The majority of the activity was attributed to Myotis bats (1850 calls, 77%), with 561 calls (23%) attributed to big bats.
Bat activity was detected at all grouped habitat types except for grassland (GR) and cutbank (CB) habitats, which were each sampled at only one location. The activity of Myotis bats was distributed across habitats differently than the activity of big bats (Figure 2.8.4.2d, G-test for independence G = 38.2, df = 7, P < 0.001), but activity of both bat groups was concentrated at non-forested/riparian (OW, RI, BK) and moist forest (SO, MOc, Fm02, MOd) sites. The average activity of Myotis bats (long-eared, little brown, northern and long-legged) was greatest at river (RI) sites, followed by moist deciduous forest (Fm02, MOd) sites and open water (OW) sites.
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The average activity of big bats (sliver-haired, big brown and hoary) was greatest at river and backchannel (RI and BK) sites, followed by open water (OW) sites.
a. Myotis 75 Buzz
Pass 50
25 Number of calls of Number 5 6 8 0 OW RI BK DRc/d MEc/d SO MOc: Fm02 MOd: Grouped habitat type other other
25 b. Big bats Buzz 20 Pass
15
10
Number of calls calls of Number 5
0 OW RI BK DRc/d MEc/d SO MOc: Fm02 MOd: other other Grouped habitat type
Figure 2.8.4.2d. Average number of bat calls recorded in 2 hours of sampling, at 9 grouped habitat types, for a) Myotis bats and b) big bats.
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Foraging, implied by the detection of a feeding buzz, was recorded at non-forested/riparian sites (OW, RI, BK) and moist forest (SO, MOc, Fm02, MOd) sites. Foraging rates for Myotis were greatest at river (RI) and open water (OW) sites, while foraging buzzes of big bats were most common in open water (OW) sites and moist deciduous forest (MOd) sites.
Myotis and big bat passes and feeding buzzes were detected in all three non-forested/riparian habitat types (RI, OW, BK) that were sampled. Within non-forested/riparian habitats, activity levels of Myotis and big bats did not differ statistically across the three habitat types that were sampled (Appendix 9b).
Non-forested/riparian habitats (RI, OW, BK) had similar levels of Myotis activity compared to forested sites (Figure 2.8.4.2e). The level of Myotis activity in forested sites can be attributed to moist deciduous forest (MOd, SO, Fm02) habitats which had high levels of activity compared to other forested habitat types (DRc/d, MEc/d, MOc). Non-forested/riparian sites had higher activity of big bats than forested sites (Kruskal-Wallis H = 10.6, df = 1, P = 0.001).
400 120 a) Myotis b) Big bats 100 300 80
200 60
40 Number of calls 100 Number of calls 20
0 0 Forest = 40 Riparian = 20 Forest = 40 Riparian = 20 Habitat Habitat
(Sample sizes for each group are given on the X-axis. Note the different scale of the Y-axis for each species group).
Figure 2.8.4.2e. The number of calls recorded in 2 hours from a) Myotis and b) big bats in forested and non-forested/riparian habitats.
Within forested sites, sampling was distributed across structural stages 4, 5, and 6. Although efforts were made to sample across all combinations, the final proportion of successful samples in each structural stage differed across the grouped habitat types (Appendix 9b). Structural stage 6 had the highest levels of activity and the greatest variation in activity (Appendix 9b), but
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Activity levels within forested sites differed with moisture regime for Myotis bats (Figure 2.8.4.2f, Kruskal-Wallis H = 7.4, df = 2, P = 0.025). Activity levels within moist (MO) and mesic (ME) sites were not statistically different, but both were significantly greater than activity in dry (DR) sites (mesic-dry H = 8.2, df = 1, P = 0.004; moist-dry H = 4.4, df = 1, P = 0.036). Although more activity of big bats was recorded in moist forests, many sites had no activity, and activity levels did not differ statistically between moist habitat types due to small sample sizes.
160 50
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100 30
80 20 60
40 10 Numberof calls Number of calls 20 0 0
Dry = 8 Mesic = 7 Moist = 25 Dry = 8 Mesic = 7 Moist = 25 Moisture regime Moisture regime
(Sample sizes for each group are given on the X-axis. Note the different scale of the Y-axis for each species group).
Figure 2.8.4.2f. Activity of a) Myotis and b) big bats at forested sites of varying moisture regime.
Activity of Myotis within moist forests varied with forest type, with deciduous (d) forests supporting greater activity than coniferous (c) forests (Figure 2.8.4.2g, H = 5.2, df = 1, P = 0.022). Big bats occurred in both forest types, but many sites had no big bat activity, and sites did not differ statistically.
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20 50 Number of calls Number of calls 10
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Coniferous = 14 Deciduous = 11 Coniferous = 14 Deciduous = 11 Dominant forest type Dominant forest type
(Sample sizes for each group are given on the X-axis. Note the different scale of the Y-axis for each species group).
Figure 2.8.4.2g. Activity of a) Myotis and b) big bats at moist forested sites that were dominated by coniferous trees or deciduous trees.
Data from paired sites that were monitored in mid-July and again in late August show no change in the number of calls per sample period with time (Appendix 9b). Sampling at potential hibernacula, discussed below, also showed no decrease in bat activity until mid-September. When the average number of calls was compared for habitat groups with samples in both July 15 to 31 (session 1) and August 28 to 31 (session 2), activity at open water (OW) sites was similar, while activity at moist, deciduous (Fm02) sites was reduced by late August (Figure 2.8.4.2h).
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0 OW BK MEc/d Fm02 Grouped habitat type
(Sample sizes are shown for each group. Error bars are excluded for clarity).
Figure 2.8.4.2h. The average number of bat calls per grouped habitat type, in 2 hours of sampling, for habitat types sampled in both session 1 (late July) and 2 (late August) in 2008.
Radio Telemetry
Twenty-five bats of six species (little brown myotis, northern myotis, long-legged myotis, silver- haired bat, big brown bat, and hoary bat) were radio-tagged during the 2006 and 2008 field seasons (Appendix 9c). Eighteen of these bats were reproductive females, one was an apparently non-reproductive female, and six were males that were not currently reproductive. Of the 25 radio-tagged bats, 18 could be re-located. In 2006, 10 tagged bats used 23 roosts, and in 2008, 8 tagged bats used 24 roost sites, for a total of 47 roost sites. Three roost sites were only located through triangulation, and the exact roost structures used were not determined, resulting in 44 roost structures identified.
Each bat used one to six roosts and roost-switching and re-use was common for the 12 bats that used more than one roost. Roost trees used in 2006 were not re-used in 2008, but some roost trees were in the same stands. Roost-roost distances ranged from 12 to 1606 m (mean 347 m, s.d. 405 m). Roost areas (based on minimum convex polygons) for bats that had three or more roosts ranged from 0.1 to 29.2 ha (mean 7.2 ha, s.d. 10.5). All identified roosts were
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Table 2.8.4.2e. The number of bats in each species/reproductive group used for analysis, the number of roost sites identified and the maximum commuting distance for each group.
Reproductive Number Number of roost site Maximum commuting Species group of bats (number of structures ) distance (m) Reproductive 7 20 (19) 2083 Little brown myotis Not reproductive 4 7 1338 Reproductive 1 5 1303 Big brown bat Not reproductive 2 6 (5) 1223 Northern myotis Reproductive 1 1 1262 Silver-haired bat Reproductive 2 7 3900 Hoary bat Reproductive 1 1 (0) 4156 Total 18 47 (44)
Roost structures
The majority of the 34 roosts used by reproductive female bats of all species were in balsam poplar trees (73% of roosts, Figure 2.8.4.2i). Reproductive females also used trembling aspen trees (15%) and cutbanks (6%). The remaining roost structures were unconfirmed (6%). The 13 roosts used by non-reproductive females and males were primarily in balsam poplar (38%) and trembling aspen trees (38%), but they also roosted in a cutbank (8%), a garage (8%) and an unknown structure (8%).
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30 Reproductive Not reproductive 25
20
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Count Count of roosts 10
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0 Balsam Popular Trembling Apen Cutbank Garage Unknown Structure
Roost structure
Figure 2.8.4.2i. Number and type of roost structure used by 12 reproductive female bats (34 roosts) and 6 non-reproductive bats (13 roosts) radio-tracked in the Peace River Corridor in 2006 and 2008.
Within species, balsam poplar trees were used predominantly by reproductive female silver- haired (100% of roosts) and little brown myotis (82% of roosts) (Figure 2.8.4.2j). The single reproductive big brown bat roosted in trembling aspen trees (60% of roosts) and balsam poplar trees (40%), and the single reproductive northern myotis roosted in a cutbank.
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18 Cutbank Balsam poplar 16 Trembling aspen 14
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0 Little brown myotis Big brown (n=1) Silver-haired (n=2) Northern myotis (n=7) (n=1) Species of bat
In total, 32 roost structures were identified. The number of bats that were tracked by radio-telemetry is given for each species.
Figure 2.8.4.2j. Type of structures used as roosts by different species of reproductive female bats.
Four non-reproductive little brown bats roosted predominantly in balsam poplar trees (57% of roosts), but also used trembling aspen trees (29%) and a garage (14%, Figure 2.8.4.2k). The two non-reproductive big brown bats used trembling aspen trees (60%), balsam poplar trees (20%) and in a cutbank (20%).
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8 Garage 7 Cutbank
6 Balsam Poplar Trembling Aspen 5
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3 Countofroosts
2
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0 Little brown myotis (n=4) Big brown bat (n=2) Species of bat
(Twelve roost structures were identified. The number of bats that were tracked by radio-telemetry is given for each species).
Figure 2.8.4.2k. Type of structures used as roosts by different species of non- reproductive female and male bats.
Bats that roosted in trees generally used large-diameter trees or snags (Table 2.8.4.2f) with a diameter at breast height greater than 56 cm, total height greater than 15 m, and with more than 57% of bark remaining. All trees were classified as appearance classes 2 (injured or dying) through to 7 (standing stub) (Figure 2.8.4.2l). Roost trees generally offered specific microsites such as small to large pieces of exfoliating bark, cracks in a bole, healing scars where branches had dropped, and obvious cavity entrances into trees with heart rot. No roost trees were climbed to determine the specific microsite feature being used.
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Table 2.8.4.2f. Quantitative characteristics of live (appearance class < 3) and dead trees (appearance class >= 3) used as roosts by bats.
Live Trees Dead Trees Characteristic Average Range # of trees Average Range # of trees Diameter at breast height (cm) 56.2 26.1 - 133 13 57.7 23.1 - 85 26 Estimated height (m) 21.5 10 - 40 12 15.7 3.5 - 32 25 Bark remaining (%) 96.1 90 - 99 12 57.7 0 - 95 26
14
12
10
8
6
4
2 Countof roost trees 0 1 2 3 4 5 6 7 Appearance class
Figure 2.8.4.2l. Appearance classes of 36 trees used as roosts by 17 bats radio-tracked during 2006 and 2008. Classes are from DEIF.
The use of large balsam poplars by little brown and silver-haired bats likely reflects the abundant microsites that these trees provide for roosting. These features include large exfoliating bark flakes, crevices in the furrowed bark or in the exposed trunk and cavities created where limbs have dropped off. It also likely reflects the open nature of mature balsam poplar stands and the prevalence of balsam poplars in moist areas adjacent to foraging areas such as wetlands, rivers and sloughs.
Big brown bats were found to use trembling aspen trees more than other roost types, suggesting inter-specific differences in preference of roost tree species. Reproductive and non- reproductive little brown myotis also used aspen trees, but aspens were used less than balsam poplars. The use of aspen trees with appropriate microsites is consistent with known habitat use by bats in areas without balsam poplar floodplains. Within the Peace River Corridor, aspen-
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Other research in the aspen-, spruce-, or pine-dominated forests of northern British Columbia or in mixedwood forests in Alberta found that bats (including little brown myotis, northern myotis, long-legged myotis, and silver-haired bat) roosted primarily in balsam poplar and aspen trees (Vonhof et al. 1997; Crampton and Barclay 1998; Kalcounis and Brigham 1998; Vonhof and Wilkinson 2000; Psyllakis 2001; Psyllakis and Brigham 2006).
Cutbanks were widely available along the riverbanks and were used by 3 of the 18 radio-tagged bats. A male big brown bat and a lactating little brown bat were each detected using a cutbank once, while a lactating northern myotis used another exclusively. The cutbank used by the northern myotis was high on the south shore of the Peace River, where a large crevice was present that was seeping black fluid, presumably urine and guano. This feature was presumed to be the roost site. This roost could not be confirmed due to its inaccessible location.
Other work on the northern myotis in western Canada has identified day roosts in trees (aspen or balsam poplar) (Vonhof et al. 1997; Vonhof and Wilkinson 2000; Psyllakis 2001; Psyllakis and Brigham 2006) and a cabin (Wilkinson et al. 1995). Research in eastern Canada in mixed forests found that females used large deciduous trees in intermediate decay stages, while male northern myotis roosted in coniferous trees (Broders and Forbes 2004).
Roost Habitat
The Fm02 habitat type was used the most frequently (70%) as a day roost by reproductive females, followed by the AMap (12%), SHac (9%), LLak (3%) and cutbanks (6%) (Figure 2.8.4.2m, Appendix 3a). Non-reproductive females and males roosted in a wider variety of habitats, including the AMap (30%), Fm02 (23%), SHac (15%), SCab (8%), SWas (8%), a cutbank (8%), and a tin roof in a rural area (8%).
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25
Reproductive 20 Not reproductive
15
10 Count of roosts
5
0 FM02 AMap SCkab SCab SWakLLak SWas SHac CB Rural TEM unit
Figure 2.8.4.2m. TEM habitat units used for roosting by 12 reproductive female bats (34 roosts) and 6 non-reproductive bats (13 roosts).
Reproductive female little brown bats (n=7), big brown bats (n=1), and silver-haired bats (n=2) roosted most commonly in Fm02 stands (Figure 2.8.4.2n). Non-reproductive female and male little brown bats (n=4) used Fm02 (43% of roosts) and SCab (14%) stands (Figure 2.8.2.4o). Little brown bats also used AMap (29%) and a rural unit (14%). Non-reproductive big brown bats (n=2) roosted in aspen-dominated stands (AM:ap 33% and SW:as 17%), more frequently than in balsam poplar stands (Fm02 33%). One male big brown bat also used a roost in a cutbank (17%).
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8 Rural 7 CB SWas 6 SHac SCkab 5 AMap Fm02 4
3 Countofroosts
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0 Little brown bat (n=4) Big brown bat (n=2) Species of bat
(The number of bats radio-tracked is given for each species (n))
Figure 2.8.4.2n. Mapped TEM units used for roosting by different species of reproductive female bats.
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25 CB 20 SWakLLak SHac AMap 15 Fm02
10 Count of roosts
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0 Little brown bat Big brown bat (n=1) Silver-haired bat Northern myotis Hoary bat (n=1) (n=7) (n=2) (n=1) Species of bat
(The number of bats radio-tracked is given for each species (n))
Figure 2.8.4.2o. TEM habitat units used for roosting by different species of non-reproductive female and male bats.
Bats roosted in 12 different habitat and structural stage combinations. The major TEM habitat units used for roosting by the different species have been discussed above. Most bats roosted in habitats in structural stages 5 to 6. Forests in structural stages 3 to 4 were used to a lesser extent and bats found roosting in these structural stages were generally found in remnant snags. These features are likely the result of past disturbance (fire) and are not typical of these structural stages, which are dominated by shrubs and small, densely spaced trees.
The majority of habitats used by bats are used in greater proportion than available in the study area based on relative number of roosts used within each species and reproductive class in the available habitat as defined in section 2.8.3.3. Small sample sizes precluded statistical analyses of use versus availability.
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Potential hibernacula
Potential hibernacula were not widely available in the study area. The areas of the river corridor that appeared most suitable as potential hibernacula were generally those with limestone outcroppings or solid sedimentary rock layers with linear fissures. The limestone was restricted to areas around Hudson’s Hope. The most solid sedimentary layer was obvious from just below the Peace Canyon dam, where at its lowest point it was approximately 3 m above the river level, to the site of the potential Site C dam, where it is close to the surface of the surrounding plains. All entrances to potential hibernacula are above the potential Site C reservoir area.
Recordings were made over 35 nights at a potential hibernaculum in the sedimentary rock outcrop above a small beaver-dammed wetland (B-121) and 38 nights at a limestone outcrop directly above the Peace River (B-122), from August 28 to October 4, 2008. Detectors were programmed to record between 7:45 pm to 6:15 am each night. The number of call files in a nightly recording was correlated with the number of passes identified by a biologist on a subset of five randomly selected sample nights (Aug. 30 and 31, Sept. 13 and 25, and Oct. 3, 2008). A high degree of correlation (Pearson R 2 = 99%) indicated that the number of call files could be used as an approximation of bat activity. The proportion of calls attributed to Myotis and big bat species was also determined for the subset of recordings analyzed.
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B121 800 B122
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ep ep ep ep Aug Aug Sep Sep Sep 1-Sep 3-Sep 5-Sep 7- 9-S 1-Oct 3-Oct 28- 30- 11-S 13-Sep 15-Sep 17-Sep 19- 21- 23-S 25-S 27-Sep 29-Sep Date
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o 20.0
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5.0 Temperature ( 0.0
t ug ug ep ep ep ep ep ep c Sep O 1-S 3-Sep 5-Sep 7-Sep 9-Sep 1- 3-Oct 28-A 30-A 11-S 13-S 15-S 17-S 19-Sep 21-Sep 23-Sep 25-Sep 27- 29-S Date
Figure 2.8.4.2p. Total number of call files recoded per night at two potential hibernacula (sites B-121 and B-122) (top) and nightly temperature at sunset in Fort St. John (bottom).
Site B-122 had extremely high activity at the start of the monitoring session. Both sites had an obvious decrease in activity by September 21 when nightly temperatures dropped to between 5 and 10 oC (Figure 2.8.4.2p). Both Myotis and big bat calls were detected at both sites for the July 2009 -179-
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40 35 30 25 20 15 10 Number of calls 5 0
0:15 1:00 1:45 2:30 3:15 4:00 4:45 5:30 19:45 20:30 21:15 22:00 22:45 23:30 Time ( 5-min interval)
(Sunset in FSJ was at 19:59).
Figure 2.8.4.2q. Timing of bat activity on August 31, 2008 at site B-122.
Extremely high activity levels were recorded at site B-122 at the start of the survey period until September 5. This site was the most likely site for a hibernaculum, as it was the only large limestone outcrop in the study area and had numerous entrances that were deeper than 2 m. Additionally, land owners have reported that snow melts away around the openings, due to warm (>0 o C) air escaping from underground cavities. The high levels of activity at this site may be swarming activity and may indicate the presence of a hibernaculum. The activity could also reflect an insect hatch and a mass foraging event, but this is unlikely since no feeding buzzes were identified out of 1180 passes examined from five nights.
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The high amount of activity could also have been due to the site being a heavily used late- summer roost due to its high sun-exposure (south aspect) which would increase the ambient temperature inside the roost. The nightly timing of activity at site B-122 is somewhat contradictory since activity at roost sites usually peaks immediately post-sunset as bats exit the roost, then decreases as bats travel to other foraging areas (Crampton and Barclay 1998). Nightly activity at a swarming site in Britain indicates that bats arrive up to several hours post- sunset, presumably after foraging, and activity peaks around six hours post-sunset (Parsons et al. 2003b). The immediate presence of bats post-sunset at site B-122 suggests roosting in the area, while the duration of activity (+4hr) is suggestive of swarming activity.
The decrease in activity in mid-September may indicate the onset of hibernation or migration. The slight increase in activity at the end of September could be a migration pulse, or possibly bats responding to the warmer evening temperatures with an increase in activity. In southern Alberta, Lausen and Barclay (2006b) recorded sporadic bat activity in the winter, well after bats had begun hibernating, thus confirming local hibernation. In Alberta, swarming of Myotis species at known hibernacula in Cadomin Cave occurs in late August and early September (Schowalter 1980, in Caceres and Pybus 1997). Similar timing of swarming is reported in Britain (Parsons et al . 2003a,b).
2.8.5 Summary
A capture rate of 0.24 bats per net night was estimated for 3 years of sampling in the Peace River. This resulted in capture of 104 bats of seven species.
The greatest amount of bat activity were recorded within non-forested/riparian and moist forest habitat types. Other studies have found bat activity to be greatest at riparian sites (Lunde and Harestad 1986; Thomas 1988; Grindal et al. 1999; Seidman and Zabel 2001), likely reflecting the higher insect abundance (Thomas 1988) and, at sites with calm water, conditions that do not interfere with echolocation (von Frenckell and Barclay 1987; Mackay and Barclay 1989). Both non-forested/riparian and moist forests were used for foraging, based on the presence of feeding buzzes recorded in these habitats. Moist and mesic forest sites supported higher levels of activity of Myotis bats than did dry sites and deciduous forests had greater activity of Myotis than coniferous forests. There were trends towards different levels of activity by big bats across
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Activity was expected to vary with structural stage, as reported in coastal forests in Oregon (Thomas 1988) and aspen mixedwood boreal forests in Alberta (Crampton and Barclay 1998). Activity is generally lower in younger forests (structural stage 4 or 5), since these forests are generally dense, making them more difficult to fly in, and support few, if any, potential roost sites. Stands in structural stage 6 are more open and older trees are more likely to provide potential roost sites (Swystun et al. 2007). The lack of statistical difference in this study may reflect the interaction of structural stage and habitat type on activity levels, but small sample sizes preclude the ability to make statistical comparisons.
Big bats may have been under represented because larger species of bats tend to fly above the canopy and therefore escape detection by ground-based detectors (Menzel et al. 2005). There may also be inter-specific differences in habitat use within the Myotis and big bat groups (Broders et al. 2006). Bat activity levels may also vary by gender, reproductive status, or age (Broders and Forbes 2004; Broders et al. 2006; Henderson et al. 2008).
The amount of bat activity in the study area decreased by mid-September, signifying the onset of hibernation and/or migration. One potential hibernaculum was detected along the Peace River near Hudson’s Hope.
2.9 WATERFOWL / W ATER -ASSOCIATED BIRDS
The waterfowl group includes loons, swans, geese, and ducks. The water-associated birds group includes shorebirds, cranes, coots, herons and bitterns. These species groups are dependent on riverine and riparian habitats to feed and breed. They are important food sources for First Nations and Aboriginal communities. Field surveys for waterfowl and water-associated birds were required in 2008 to:
• add to the data from previous years to document seasonal (spring, summer and fall) trends in species occurrence, distribution and abundance;
• provide additional information on the breeding and migratory populations using the river corridor .
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2.9.1 Introduction
Waterfowl and water-associated birds that use the Peace River area include grebes, coots, loons, cormorants, swans, geese, ducks, gulls, rails, cranes, sandpipers and plovers (surveys for Great Blue Heron nests were discussed in Section 2.1). There are no at-risk waterfowl species known to breed in the Project area, but the river corridor may provide important migrating and staging habitat for large congregations of waterfowl. Provincially-listed species are known to travel through the area.
2.9.2 Background
Waterfowl have been documented in the Peace River Valley since the 1970’s. Historical data were collected by Ryder (1975), Thurber (1976), Blood (1979), Phinney (1998), Robertson (1999), Robertson and Hawkes (2000), Siddle (2005) and Lambie (2004, 2005, 2006, 2007, 2008).
Thurber (1973) completed waterfowl surveys by jet boat along the Peace River from Lynx Creek to Farrell Creek in 1973. Sixty-five bird species were observed including seven species of waterfowl. Thurber (1976) also completed stand-watches, boat and aerial surveys between April and June 1974 and 1975 in the Peace River Valley. Breeding species observed included Trumpeter Swan, Mallard, Pintail, American Wigeon, Green-winged Teal, Blue-winged Teal, Northern Shoveller, Common Goldeneye, Barrow’s Goldeneye, Bufflehead, Surf Scoter, Common Merganser, Lesser Scaup and Harlequin Duck. Twenty-eight species of waterfowl, 21 shorebirds and 7 gulls/terns used the Peace River for migration, staging or breeding habitat. Dabbling ducks congregated on mud flats and shallow backchannels along the Peace River and diving ducks were found mainly in the main channel and in deep water.
Blood (1979) conducted an aerial survey on April 27, 1977 from Moberly to Hudson’s Hope to census waterfowl, and summarized previous work conducted by Thurber (1976). Both found that dabbling ducks moved west through the area between mid April and mid May, and diving ducks passed through the area in May. Gulls and terns arrived in the Peace River Valley in July to feed. American Bitterns, Coots, Soras, Wilson’s Snipe and possibly Wilson’s Phalarope were observed nesting in Watson’s Slough. Canada Goose, Mallard, Common Goldeneye, Spotted Sandpiper and Killdeer were observed nesting in the Peace River Valley. A maximum of 27 different broods per year were seen in the potential Site C reservoir between 1974 and 1977.
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Phinney (1998) compiled bird-sighting data from the area around Dawson Creek between 1991 and 1995. During this time, listed waterfowl and water associated-birds that were seen around Dawson Creek included American Bittern, Sandhill Crane, Upland Sandpiper and Surf Scoter.
Systematic aerial surveys for aquatic birds were conducted in February 1996 and August 1999, with ground surveys in 1999 from the W.A.C. Bennett dam to the Alberta border (Robertson 1999; Robertson and Hawkes 2000). During the winter, the greatest concentrations of waterfowl were Common Mergansers below the W.A.C. Bennett Dam and between the Peace Canyon Dam and Hudson’s Hope (Robertson 1999). Robertson (1999) hypothesized that fish are stunned when they pass through the two dams and create feeding opportunities for diving ducks and raptors at the tailrace. Late summer concentrations of water-associated birds as well as terrestrial birds were also noted in the floodplain of the Peace River (Robertson and Hawkes 2000).
During surveys in August 1999, 20 waterfowl/water-associated bird species were recorded (Robertson 1999). Fifty-one percent of all individual birds recorded were Canada Geese or Mallards and sixty percent of the birds were observed between Cache Creek and the Pine River (Robertson 1999). Concentrations of geese, dabbling ducks and gulls were influenced by human food sources near Fort St. John (Robertson 1999; Robertson and Hawkes 2000). Most waterfowl and water-associated birds were found in backchannels except for Canada Geese, gulls, Common Mergansers and Spotted Sandpipers (Robertson 1999). Backchannel habitats along the Peace River were moderately productive for waterfowl, especially Mallards and dabbling ducks (Robertson 1999). Shorebirds observed in the study were mostly migrants but the Peace River provides important habitat for these birds (Robertson 1999; Robertson and Hawkes 2000).
Siddle (2005) recorded 6,500 observations of shorebirds between 1975 and 1989 near Fort St. John. Spring migration occurs from late April through to early June and fall migration occurs from late June through early October. In total, 30 species were observed, 22 in the spring and 24 in the fall. Spring migration peaked in late May and fall migration peaked in July and August. Siddle (2005) concluded that Fort St. John and the Peace River are significant stopover sites since they are the only suitable habitat in BC for the central flyway. Seven species observed by Siddle (2005) including the Lesser Yellowlegs, Solitary Sandpiper, Upland Sandpiper,
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Hudsonian Godwit, White-rumped Sandpiper, Pectoral Sandpiper and Stilt Sandpiper, were noteworthy due to their exclusivity to the Fort St. John area or their rarity in BC.
Ducks Unlimited recorded breeding pairs and brood numbers for 14 different duck species in Watson’s Slough between 2005 and 2008. The number of breeding pairs in Watson’s Slough ranged from 33 to 39 pairs and brood numbers ranged from 9 to 26.
The Mackenzie Bird Banding Station records birds seen everyday from mid July to late September (Lambie 2004, 2005, 2006, 2007, 2008) at Mugaha Marsh (14 km NW of Mackenzie). In 2005, a Lakewatch was started along Williston Lake from mid August to late September and this has continued yearly. This lakewatch documents birds on migration (Lambie 2005, 2006, 2007, 2008). Notable observations include the Blue-listed American Bittern, California Gull, Sandhill Crane, and Surf Scoter, and the Red-listed Upland Sandpiper.
American Bittern
The American Bittern is a rare migrant and summer visitant, that may breed in the area (Phinney 1998). Phinney (1998) recorded this species at Klukas Creek on May 17, 1991 and at McQueen’s Slough between May and June 1992. An American Bittern was seen at Mugaha Marsh on August 25, 2006 (Lambie 2006) and another was seen at the edge of the water at Gatiga by Highway 39 in 2007 (Lambie 2007). One American Bittern was also observed at Mugaha Marsh between August 31 and September 15, 2008 (Lambie 2008).
Caspian Tern
Three Caspian terns were observed at the Peace River on May 29, 1974 (Thurber 1976).
California Gull
Thurber (1976) found that the California Gull was a fairly common migrant and an occasional summer resident in the Peace River. Ryder (1975) observed the California Gull in the Peace Region in 1975. On August 9, 2006, two California Gulls were seen near the Mackenzie Nature Observatory (Lambie 2006) and one was seen flying over Williston Lake on September 8, 2007 (Lambie 2007).
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Sandhill Crane
Sandhill Cranes typically migrate north through the Peace Region in mid to late May (Phinney 1998) but are thought to be uncommon (Thurber 1976). Several flocks of Sandhill Cranes were observed in the Peace River in May 1975 (Thurber 1976). A flock of 51 birds was seen on September 10, 2005 at Mugaha Marsh and 4 were seen flying by Williston Lake on August 31, 2005 (Lambie 2005). On September 19, 2006, 263 Sandhill Cranes flew past the banding station (Lambie 2006). In 2007, two Sandhill Cranes and a juvenile were seen early in the season (late July) at Mugaha Marsh (Lambie 2007). Sandhill Cranes were also heard on July 28, 2008 at the Mackenzie Bird Banding Station (Lambie 2008).
Surf Scoter
Surf Scoters migrate north through the Peace Region during the month of May (Phinney 1998). Thurber (1976) and Ryder (1975) observed Surf Scoters using the Peace River in 1975. Two Surf Scoters were seen at Mugaha Marsh between from August 24 to 30 in 2005 (Lambie 2005). In 2006, 22 Surf Scoters were seen between August 28 and 30 at Williston Lake and on September 19, 118 were seen at Mugaha Marsh (Lambie 2006). One Surf Scoter was seen at Mugaha Marsh on August 23, 2008 (Lambie 2008).
Upland Sandpiper
Flocks of Upland Sandpipers were seen in fields and clearcuts around Dawson Creek in May and June, 1994 and 1995 (Phinney 1998). In 2007, 9 Upland Sandpipers were seen between August 20 and 26 at the Mugaha Marsh (Lambie 2007). Upland Sandpipers were found in open fields, roadside edges and recently burned fields by Siddle (2005), who also reported that the main breeding area for Upland Sandpipers in the province is in the Peace Region and numbers peak in mid to late August during breeding.
Western Grebe
The Western Grebe is a rare migrant and is not known to breed in the Peace Region (Phinney 1998). Phinney (1998) reported Western Grebes in the Peace area at Alcock Lake in June, 1992 and at Swan Lake in May 1993 (Phinney 1998)
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Yellow Rail
No records were found for Yellow Rail in the Peace Region.
2.9.3 Methods
Inventory methods used in 2008 followed the BC Resource Inventory Standards Committee’s Inventory Methods for Waterfowl and Allied Species: Loons, Grebes, Swans, Geese, Ducks, American Coot and Sandhill Crane (RIC 1999d).
Draft habitat suitability mapping for target species was completed according to British Columbia Wildlife Habitat Ratings Standards (RIC 1999a).
2.9.3.1. 2008 Inventory Surveys
Boat, helicopter and ground transects were completed to survey waterfowl species present in the PRC and TL study areas. All species observed during surveys were recorded, including waterfowl, water-associated birds, raptors and songbirds.
General survey conditions were recorded at the start and end of all surveys, including cloud cover, ambient air temperature, precipitation and wind speed. All observations were recorded on standard RISC datasheets customized for the project. Inclement weather (heavy rain, strong wind) conditions may affect the ability of surveyors to detect waterfowl. If these conditions were experienced during a survey the survey may not have been completed.
Species were recorded in three strata in the PRC study area: the main river channel, river backchannels and wetlands. In the TL study area, species were recorded in two strata: wetlands or lakes.
Aerial Surveys
Aerial surveys were completed by helicopter between the Peace Canyon Dam and the Alberta border. The survey transects were unlimited width and observations were recorded in 5 to 10 km long transect segments (depending on the number of observations). Due to the width of the Peace River, transects were flown in both directions, concentrating on either the north or south side of the river. The flight track and species observations were monitored to avoid recounting the same birds. Backchannels and tributaries were also surveyed. The number, species and
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Boat Transect Surveys
Boat surveys were completed from a drift boat or jet boat and occurred between the Peace Canyon Dam and the Alberta border. The river was sampled in five to ten km long transect segments of unlimited width, as determined by a portable GPS unit. The river was surveyed as one complete survey (one transect with multiple segments), over multiple days. The number of days taken to survey the river was determined by the amount of waterfowl activity. Distinct transect segments were also completed as crews were transported to survey sites for other species-specific surveys. Each survey involved at least two observers scanning the river in opposite directions.
The survey boat was allowed to drift downstream with the current in order to avoid alarming birds with engine noise. When the engine was used, it was cut immediately when waterfowl were observed. The surveyors generally followed the main channel of the Peace River. Pre- selected backchannels were also surveyed, either by boat or on foot after docking the boat. The number, species and sex (when possible) of all birds observed were recorded.
Ground Surveys
Observation stations were completed at backchannels and wetlands. These sites were identified from the TEM map prior to surveys and some of the sites coincide with wetlands and backchannels surveyed during other species-specific surveys (e.g., amphibian surveys). Sites were accessed by boat during boat transects or on foot if they were accessible from a road.
The number of separate observation stations was determined by the size of the area and the visibility. Observation stations were placed at vantage points where a sample independent from the previous station could be obtained. Each wetland or backchannel was surveyed one or more times depending on the site’s accessibility and the suitability of the habitat.
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2.9.3.2. Habitat Suitability Mapping
Draft species models and ratings tables were prepared for Yellow Rail, American Bittern and Sandhill Crane (Keystone Wildlife Research Ltd. 2008b). Nonforested wetlands and cultivated fields were rated up to Low according to their suitability for Reproducing-eggs for American Bittern, and up to High as Yellow Rail breeding habitat. Sandhill Cranes are not known to breed in the study area, so habitat for this species was rated on its suitability as migration habitat. Cultivated fields, wetlands and early structural stages of moist to wet forest were rated up to Low for cranes.
2.9.4 Results
Results of 2008 surveys and a compilation of data from surveys completed between 2005 and 2008 are reported below. Data from previous surveys are included when available from original databases or reports. The locations of waterfowl surveys completed in 2006 and 2008 are shown on Maps 2.9.4a and 2.9.4b.
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Map 2.9.4a. Waterfowl survey locations.
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Map 2.9.4b. Waterfowl survey locations.
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2.9.4.1. 2008 Inventory Surveys
Waterfowl surveys were completed along the Peace River between the Peace Canyon Dam and the Alberta border once per month between May 1 and October 30, 2008 (Table 2.9.4.1a, Appendix 10a). Additional river segments were surveyed in May, June and October 2008 and 32 backchannels were visited 1 to 9 times during the sampling period. Four wetlands in the Peace River Corridor (PRC) study area were surveyed 1 to 10 times for waterfowl from May to October 2008. Survey sites in the potential Site C reservoir (SCR) included 21 backchannels, 9 river segments and 1 wetland (Appendix 10a). Inclement weather conditions (wind >19 km/hr) were experienced during one survey on June 22, 2008.
In the transmission line (TL) study area, 4 lakes were surveyed 2 to 8 times and 43 wetlands were surveyed between 1 to 7 times between May 1 and October 30, 2008 (Table 2.9.4.1a, Appendix 10b). The majority of these surveys occurred from May to June and September to October, 2008. Generally, surveys were repeated where suitable habitat was present.
Table 2.9.4.1a. Numbers of waterfowl surveys completed in each stratum in 2008.
Number of Surveys Study Area Stratum Total May June July Aug. Sept. Oct. Backchannel 2 9 24 23 37 32 127 River (All) 1 1 1 1 1 1 6 PRC River Segment 8 20 2 30 Wetland 4 3 4 2 2 15 Total 15 33 25 28 42 35 178 Lake 1 1 7 9 18 TL Wetland 31 19 5 5 3 6 69 Total 32 20 5 5 10 15 87 Total 47 53 30 33 52 50 265
Fifty-seven species of waterfowl and water-associated birds (not including unidentified species) were recorded between May and October 2008, during ground, boat and aerial surveys (Appendix 10c). Forty-eight species were detected in the PRC study area, of which 40 were also in the potential Site C reservoir. Nine species were detected only in the SCR. Thirty-four species were observed in the TL study area (Appendix 10c). Of the species detected, 25 were
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observed in both the PRC and the TL study areas, 23 were detected only in the PRC and 9 were detected only in the TL. Forty species were observed incidentally during 2008 (Appendix 10d), 5 of which were not detected during waterfowl surveys. These include Pied-billed Grebe, Marbled Godwit, Red-necked Grebe, Western Grebe and Wilson’s Phalarope.
Most detections of listed bird species occurred during the spring or fall migration (Table 2.9.4.1b). The Red-listed Upland Sandpiper and Western Grebe and the Blue-listed California Gull, Great Blue Heron, Sandhill Crane and Surf Scoter were detected in the Peace River Corridor. The Blue-listed Surf Scoter, Double-crested Cormorant and Sandhill Crane were detected along the Transmission Line. The California Gull, the Double-crested Cormorant and the Upland Sandpiper are summer visitants to the study area. The Sandhill Crane and Surf Scoter are seasonal migrants and Great Blue Heron is a rare visitant (Phinney 1998). The Upland Sandpiper is the only listed species known to breed in the area.
Table 2.9.4.1b. Numbers of Red or Blue-listed waterfowl and water-associated bird species detected in 2008 (including incidentals).
Scientific BC PRC TL English Name Total Name Status May June Aug. Sept. Oct. May June Sept. Oct. Larus California Gull Blue 1 5 2 8 californicus Double- Phalacrocorax crested Blue 2 2 auritus Cormorant Great Blue Ardea Blue 1 1 2 Heron herodias Grus Sandhill Crane Blue 1 49 2 52 canadensis Melanitta Surf Scoter Blue 1 1 2 4 perspicillata Upland Bartramia Red 2 1 3 Sandpiper longicauda Western Aechmophorus Red 5 5 Grebe occidentalis Total 3 2 2 60 2 2 2 1 2 76
Three strata were identified in the PRC study area (main river channel, river backchannels and wetlands) and species composition and use was compared between strata. Of the 19,147 birds recorded in the PRC study area in 2008, 22% were in backchannels, 77% were in the main river
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25
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15 River Backchannels 10 Wetland
Numberspecies of 5
0 May Jun July Aug Sep Oct Month
Figure 2.9.4.1a. Number of species detected each month in the River, Backchannel and Wetland strata in the PRC.
In the River stratum, Canada Geese (23%) were observed the most frequently, followed by Mallards (9%), Franklin’s Gulls (35%) and Ring-billed Gulls (11%). In the Backchannel stratum, the most common species observed were Canada Geese (41%), Mallards (23%) and Franklin’s Gulls (12%). In Wetlands, Mallards (17%) were the most common, followed by Green-winged Teal (14%). A greater proportion of dabbling ducks (30% of species) was observed in Backchannels compared to the River (13%) and gulls were observed more frequently in the main channel (53%) than in Backchannels (13%). These observations are consistent with the foraging strategies employed by these species groups.
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Two strata were identified in the TL study area (Wetlands and Lakes) and species composition and use was compared between strata. Of the 1,938 observations recorded in the TL study area in 2008, 68% were in Lakes and 32% in Wetlands (Appendix 10f). Waterfowl activity (number of species and number of observations) peaked in the Wetlands and Lakes in the TL study area in September. Species diversity was greater in Lakes than Wetlands with 30 species detected overall and most (22) species detected in September (Figure 2.9.4.1b). In Wetlands, 23 species were detected overall, with most (15) detected in September. No species were observed in Lake surveys completed in June and August and only two species were observed in Wetland surveys completed in July and August.
25
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15 Wetland 10 Lake
NumberSpecies of 5
0 May Jun July Aug Sep Oct
Figure 2.9.4.1b. Number of species detected each month in the Wetland and Lake strata in the TL.
In the TL study area, Mallards (23%), Ring-necked Ducks (19%) and American Coots (14%) were detected the most frequently. Mallards (28%) were the most common species in the Lake stratum, followed by American Coots (23%). Ring-necked Ducks (48%) and Lesser Scaups (12%) were the most common species in the Wetland stratum.
Rails, coots (members of the family Rallidae), Soras and Long-billed Dowitchers were only observed in wetlands and lakes in the TL study area.
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2.9.4.2. Multiple Year Data Analysis
Hawkes et al . (2006) completed aerial and boat surveys in 2005 (Table 2.9.4.2a; 2.9.4.2b) in the Peace River Corridor (Core). They found that 63% of the all waterfowl species detected were observed on the Peace River above its confluence of the Moberly River.
Keystone Wildlife Research Ltd. (2006b) completed aerial and boat surveys in 2006 (Table 2.9.4.2a; 2.9.4.2b). Canada Goose, Mallard and Franklin’s Gull were the most common species detected. Five Blue-listed species were detected including the Surf Scoter, Sandhill Crane, Great Blue Heron, California Gull and Caspian Tern. Overall, waterfowl species appeared to use the river most heavily in September.
Table 2.9.4.2a. Summary of waterfowl surveys completed in 2005, 2006 and 2008.
Number of waterfowl and Number of Red- or Blue Study Area Year Survey Period water-associated species listed species detected detected June 15 to July Core 2005 32* 3* 18 April 26 to Peace River 2006 42 5 October 2 Corridor 48 6 May 1 to Transmission 2008 October 30 34 3 Line Total 61** 7** *Numbers in Hawkes et al. 2006, **total number of species detected during all surveys.
Survey effort increased from 2005 to 2008 with more surveys in wetlands and backchannels during 2006 and 2008 (Table 2.9.4.2b). In 3 years, 61 species of waterfowl and water- associated birds have been recorded in the Peace River Corridor and the surrounding area (Appendix 10g). Twenty-seven species were infrequently detected during the three years of surveys, with fewer than 3 observations in one or more years.
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Table 2.9.4.2b. Number of waterfowl surveys completed in 2005, 2006 and 2008.
Number of Site Visits* Stratum Total Core 2005** PRC 2006 PRC 2008 TL 2008 River 2 5 6 13 River Segments 15 30 45 Backchannel 116 127 243 Wetland 22 15 69 106 Lake 18 18 Total 17 143 178 87 425 *Includes replicates, ** Numbers given in Hawkes et al. 2006.
Listed species detected in 2005, 2006 and 2008 include the Red-listed Upland Sandpiper and Western Grebe and the Blue-listed California Gull, Caspian Tern, Great Blue Heron, Sandhill Crane and Surf Scoter. These species were all infrequently detected (observed 1 to 3 times) in one or more years. The majority of the listed species were observed in September during fall migration and were classified as migrants (Table 2.9.4.2c). The Upland Sandpiper is expected to breed in the uplands in open field habitat adjacent to the study area and the other listed species migrate through the area.
Table 2.9.4.2c. Numbers of Red- or Blue-listed species observed in the PRC study area in 2005, 2006 and 2008.
BC PRC 2005 PRC 2006 PRC 2008 English Name Total Status June July May June Sept. May June Aug. Sept. Oct. California Gull Blue 115 3 1 1 5 2 127 Caspian Tern Blue 2 2 Great Blue Heron Blue 1 1 1 3 Sandhill Crane Blue 2 1 49 52 Surf Scoter Blue 36 1 37 Upland Sandpiper Red 4 2 2 1 9 Western Grebe Red 5 5 Total 4 119 3 1 39 3 2 2 60 2 235
Thirty-five species are expected to be summer visitants, with 16 species that breed in the study area, 10 species that probably breed and 9 species that occur but do not breed in the study area (Appendix 10g). Twenty-two species are expected to migrate through the area seasonally and four species are vagrants (study area is outside of their normal range). Vagrant species include the American Dipper, Cinnamon Teal, Common Tern and Great Blue Heron.
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Trends in species diversity and seasonal use indicate that the Peace River Corridor provides important stopover habitat for migrating waterfowl and water associated birds. The number of species is generally highest during the spring (May and June) and fall (August and September) migration (Figure 2.9.4.2a).
45
40
35
30
25 2006 2008 20 2005
15 Numberspecies of 10
5
0 April May June July Aug Sept Oct
Figure 2.9.4.2a. Summary of the number of waterfowl and water-associated bird species observed in the Peace River Corridor during surveys completed in 2005, 2006 and 2008.
2.9.5 Summary
In total, 61 species of waterfowl and water-associated birds have been detected in the study areas. Of these 21 species were detected infrequently (1-3 detections in 1 or more years). Seasonal trends in species abundance and diversity indicate that migrating species heavily use the river corridor during the spring and fall migration. Species diversity was greatest in the Peace River compared to wetlands and lakes in the Peace River Corridor and on the existing
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2.10 UNGULATES
Ungulates are hunted in the Peace River and are important resources for local residents and First Nations. Species known to occur in the project area include mule deer, white-tailed deer, elk and moose. These species are not provincially or federally at risk. Thinhorn sheep have also been reported in the area.
Field surveys for ungulates were required in 2008 to:
• to determine the relative use by ungulates of areas that may be disturbed by the potential Site C dam, compared to adjacent undisturbed habitats;
• document ungulate population trends and fluctuations in the study area during typical winter conditions.
2.10.1 Introduction
Moose ( Alces americanus ), mule deer ( Odocoileus hemionus ) and elk ( Cervus canadensis ) winter within the Peace River valley (Rowe 2008). Several designated ungulate winter ranges (UWR) are located along the Pine and Moberly Rivers, which are primary tributaries running into the Peace River. Additional draft winter ranges are located along the south aspect slopes of the Peace River Valley. One winter range is located near the confluence of the Moberly River with the Peace River. The footprint of the potential Site C dam currently includes disposal and gravel extraction areas within and adjacent to this UWR.
2.10.2 Background
Ungulate surveys have been completed in the Peace River Valley, in association with Site C and Site One (Peace Canyon Dam), since 1973 (Thurber 1973, 1976). The abundance and distribution of ungulates were studied in the Peace Region management units (http://www.env.gov.bc.ca/fw/wildlife/hunting/regulations/ ) in the late 1970's and again in the early 1990's (Blood 1979; Simpson 1991, 1993).
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Thurber Consultants (1973) completed 15 ground transects in the spring of 1973 to count pellets and assess habitat use (browse, tracks) between the Halfway River and the W.A.C Bennett Dam. Thurber (1976) also conducted 5 aerial surveys and 19 ground transects to record ungulate browse and pellet groups around the potential Site C reservoir between 1973 and 1975.
Blood (1979) carried out ungulate surveys in the Site C region Management Units (MUs) 7-32, 7-34, and 7-35, the Site C project area (Peace River valley and tributaries) and the Site C impact area (area that will be directly influenced by the project). Winter helicopter surveys were completed in the Site C project area in January 1977 to census ungulates. Ground transects in different habitat types were completed in the spring (April and May) of 1977 to count pellet groups in the Site C region.
Harper (1985) completed 2 aerial surveys to determine moose population density, age and sex composition in MUs 7-32 and 7-44.
Simpson (1991, 1993) completed an aerial census, pellet transects and radio tracking of 9 mule deer, 14 moose, 11 elk and 2 white-tailed deer between July 1990 and March 1993. The study area included MUs 7-32, 7-34, 7-35, 7-43, 7-44, 7-45, 7-46 and parts of 7-33. Collared animals were located 4 to 6 times each month on aerial surveys. Random stratified block count surveys were also completed in 1990 to count deer, moose and elk in the reservoir area and adjacent slopes (Simpson 1991).
Random stratified block count surveys were also completed by Keystone Wildlife Research Ltd. (2006b) in the winter of 2005-06. Ungulates were widely distributed due to a lack of snow and counts underestimated numbers since many animals remained outside of the survey area. The following winter of 2006-07 was particularly severe and many deer and moose are reported to have died (Thiessen 2008).
The Ministry of Environment conducted aerial surveys for the Peace Region in 2004 (Anderson and Scheck 2004). Late-winter reconnaissance-level surveys were completed to inventory wildlife and complete habitat assessments for 77 areas of interest, including UWRs and WHAs. Confidence levels for population estimates were not provided.
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In 2007, Thiessen (2008) replicated aerial block count surveys completed by the Ministry of Environment in 2004. The survey was conducted in the Peace Region in MU 7-33 to provide comparative data to assess effects of liberalized hunting regulations and a severe winter on ungulate populations. The Ministry of Environment organized a winter ground count in 2008. This survey focussed on wildlife counts within the agricultural zone bounded roughly by Dawson Creek, Chetwynd and Hudson’s Hope (MOE 2008). Confidence levels for population estimates were not provided.
Moose
Thurber (1973) found that moose preferred mature white spruce, aspen or balsam poplar stands. Thurber (1976) reported that moose used the south-facing slopes of the Peace River more frequently during a severe winter. During mild winters, moose were common on the islands, floodplains and north-facing slopes of the Peace River Valley.
Blood (1979) counted 70 moose below 1515 ft in the Site C impact area and estimated the maximum number of moose present in the impact area at any one time was 110. Moose numbers were highest on the floodplain and valley slopes in the winter and the greatest use of the impact area was expected during winter. Blood (1979) also observed that the major use of the islands by moose seems to be for calving, and most moose observed during winter surveys were not on the islands.
Harper (1985) found that there were approximately 0.73 moose/km 2 in MU 7-32 and 0.96 moose/km 2 in MU 7-44. Those densities are based on two winter census flights.
Simpson (1991, 1993) tracked 16 moose (13 cows and 3 bulls) for 2-3 months (December through March) and found that moose spent 30 to 40% of their time in the flood zone, but frequently moved to the plateau and other drainages. Movements of moose were not restricted in the winter and all available habitats were used, but the valley bottom habitats had the greatest value. Cow moose used the floodplain most often, while bulls frequented upland aspen-rose habitat. Overall, 307 moose were estimated within the Peace River Valley during the winter of 1990-1991, based on stratified random block counts and 600 moose were estimated to use the potential Site C reservoir based on movements of collared animals. This
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There were 231 moose counted during aerial surveys by Anderson and Scheck (2004). Thiessen (2008) found that the moose population had decreased in MU 7-33 from 130 animals in 2005, to 100 in 2007. This study had limited scope and conclusions should not be drawn from the small data set. The winter wildlife count of 2008 recorded 159 moose in 127 survey blocks (MOE 2008).
Rowe (2008) summarized moose inventory and harvest data from the 1980’s to 2007 in the Peace Region. Site C is located in wildlife management subzone D and this subzone has the highest moose harvest by resident hunters compared to other subzones in the Peace Region (Rowe 2008). Subzone D is easily accessible and has relatively high moose densities (Rowe 2008). Stratified random block counts in MU 7-32, conducted by the Ministry of Environment between 1984 and 2004, resulted in the following population estimates: 2651 moose in 1984, 2520 moose in 1996 and 3431 moose in 2004 (Rowe 2008).
Mule Deer
Thurber (1973) found that mule deer preferred semi-open forest on steep, dry terrain. In early spring, mule deer were observed on south-facing slopes more frequently than in other habitats (Thurber 1976).
Mule deer winter range was observed mostly to be above 1515 ft elevation but islands within the Peace River Valley were used for fawning and post fawning during the summer (Blood 1979). Blood (1991) found that deer numbers in 1990 were higher than any time since the early 1960’s probably because of mild winters and conservative hunting regulations implemented in 1974.
Simpson (1991) estimated that 2533 mule deer used the potential Site C reservoir at some point during the year based on stratified random block counts. Telemetry studies identified two deer ecotypes in the Peace River Valley: migratory and resident (Simpson 1991, 1993). Migrants travelled long distances (25-110 km) during the spring and fall between their summer and winter habitat, while residents stayed within the same range (<10 km 2) year round. The potential Site C reservoir was important for resident females during all seasons and for migratory females
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Anderson and Scheck (2004) counted 643 mule deer during three days of aerial winter surveys. Thiessen (2008) found that the mule deer population index had decreased since 2005 from 661 to 333 in MU 7-33. There were 1188 mule deer counted in the agricultural zones during a winter wildlife count (MOE 2008).
White-tailed Deer
During 1963 to 1985, white-tailed deer were not targeted for research in the area and thus most records were incidental (Blood 1991). Thurber (1976) found that the white-tailed deer population had increased downstream of the Moberly River because of the presence of agricultural fields adjacent to the river.
Simpson (1991) estimated that there are 5 white-tailed deer to 100 mule deer in the Peace River study area. The north-facing slopes, islands and floodplains of the Peace River support low densities of white-tailed deer. Simpson (1993) tracked movements of 2 white-tailed deer and found that, similar to mule deer, migrants occupied a large area (>700 km 2) and residents occupied a small area (<10 km 2). Few white-tailed deer used the potential Site C reservoir and most were found on the plateau, often associated with agricultural land.
Only 12 white-tailed deer were counted during an aerial survey of the region in 2004 (Anderson and Scheck 2004). Thiessen (2008) found that white-tailed deer population index had increased from 47 in 2005 to 82 in 2008. There were 278 white-tailed deer counted in the winter of 2008 in the agricultural zone (MOE 2008).
Elk
Thurber (1973) found limited evidence of elk during ground surveys between the Halfway River and W.A.C Bennett Dam. Blood (1979) found that, in the late 1970’s, elk were only known in the Moberly drainage and made little use of the flood zone. The elk population in the Peace Region increased between 1965 and 1990 due to mild winters, negligible hunting mortality and immigration from other areas (Blood 1991). Blood (1991) also noted that there were three
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Simpson (1991, 1993) radio-collared 11 elk in the Peace River area. Four elk were found to cross the Peace and its tributaries but made little use of the flood zone. During the winter, elk were concentrated on the south aspect river breaks to avoid the deep snow pack. The home range of radio-tracked elk was found to be 30-60 km2.
Anderson and Scheck (2004) conducted an aerial survey along the Peace River and some of its tributaries upstream of Fort St. John in 2004. They counted 542 elk in the Peace River valley. Thiessen (2008) found that the elk population index increased since 2005 from 45 to 136. There were 407 elk counted in 127 blocks during a day survey of the agricultural zone in 2008 (MOE 2008).
2.10.3 Methods
Ungulate surveys were completed in the PRC study area. A detailed study area was defined within the Peace River Corridor to focus survey effort on ungulate winter ranges that may be effected during construction of the potential Site C dam. The study area was defined using potential footprint areas, including the potential dam site, disposal sites and granular investigation areas. All areas are within 3 km of the junction of the Moberly and Peace Rivers.
Snow-track survey methodologies followed those described in D’Eon et al. (2006). Aerial surveys were completed according to Aerial-based Inventory Methods for Selected Ungulates: Bison, Mountain Goat, Mountain Sheep, Moose, Elk, Deer and Caribou (RIC 2002) and are consistent with Unsworth et al. (1991).
2.10.3.1. Inventory Methods
Survey methods included aerial surveys to obtain species population estimates for the identified winter ranges and track counts to provide comparative habitat use by each species.
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Winter Track Counts
Twelve snow-tracking transects were established in the study area, which traversed both impact and no-impact areas. The 12 transects were surveyed three times during the sampling period (January to March 2009).
Two-person crews walked pre-defined transects through footprint and non-footprint habitats and recorded the species and number of crossings by ungulates and furbearers in each 50 m transect segment. The snow depth and habitat attributes (slope, aspect, structural stage) were also recorded at 50 m intervals. Surveys took place at least 12 hours after the most recent snowfall, when possible, and the number of days since the last snowfall was recorded. The UTM location (NAD 83) at the start of each 50 m segment was recorded with a hand-held GPS unit. The survey track was re-plotted on field maps after the first survey to allow duplication of the actual survey route on subsequent surveys.
Analyses will determine if the number of tracks/day/50 m is significantly different among three ungulate strata (flat, warm aspect slopes and cool aspect slopes) using the Kruskal-Wallis test (Zar 1999). The relationship between snow depths and ungulates (tolerance thresholds) will be confirmed. Snow depths among the different strata will be compared using t-tests. Differences in use between the potential footprint versus non-footprint areas will be tested using the Kruskal-Wallis test.
Aerial Census
The survey blocks defined by Simpson (1991) and Keystone Wildlife Research Ltd (2006b) were transferred to TRIM base maps. Some blocks were adjusted due to changes in habitat suitability (clearing for agricultural use) and some were eliminated. A pre-stratification helicopter flight was completed to classify blocks into high, moderate or low strata for expected numbers of deer, moose and elk (Unsworth et al. 1999). Previous surveys have shown that south aspect, north aspect and floodplain units support different densities of each species.
Survey blocks were prioritized for aerial surveys based on the objectives of the study. The first priority included blocks that overlapped or were adjacent to project footprints. These included 7 survey blocks in the Moberly (footprint) study area (Blocks 1, 18, 19, 22, 23, 30 and 34 as
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Site C Hydro Project Stage 2 Vegetation and Wildlife Report defined in 1991). The second priority including blocks within the potential Site C reservoir (2, 3, 4, 5, 6).
Twenty randomly selected blocks were surveyed from various other strata. This allowed a complete census of the study area, which was comparable to the results of surveys completed in 1991 and 2006.
Ungulates were counted and classified using aerial transects located within each survey block (RIC 2002). Fixed width transects (~200 m) were flown following a compass bearing in flat terrain or along contour lines in sloped terrain. The observers counted animals within the field from the centre of the aircraft to half way to the next transect on their side of the aircraft. Animals spotted outside the transect width were noted on the map and the pilot and navigator informed. Sample units were surveyed starting from the highest elevation and working systematically downward in intervals of 100 to 200 m, depending upon topography and cover (RIC 2002).
Surveys were completed in February 2009. Count data were summarized using Aerial Survey software (University of Idaho 2004). The population estimates were compared between years with consideration of the snow conditions and other significant factors that can influence ungulate distributions. The aerial survey software incorporates corrections for sightability that have not been validated in the Peace Region. Due to the lack of conifer cover and high visibility, the corrections are expected to be reliable but confirmation using marked animals would provide more certainty.
2.10.3.2. Habitat Suitability Mapping
Draft species models and ratings tables were prepared for moose, mule deer and elk (Keystone Wildlife Research Ltd. 2008b). The seasons and life requisites rated were Winter-Food, Winter- Security/Thermal and Reproducing-Birthing.
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Moose
Moist, shrubby floodplain and wetland habitats were rated highest for winter feeding for moose (up to Class High), and floodplain forests were rated highest for winter security/thermal cover (up to High), as well as Reproducing-birthing habitat.
Elk
Warm-aspect steep grassland and aspen shrubland were rated highest (up to High), for winter feeding for elk, while wet spruce and seral forest was rated highest (up to High), for security- thermal habitat. Young, wet, valley bottom forest and floodplain forest was rated highest (up to High) as birthing habitat.
Mule Deer
Warm-aspect steep grassland and aspen shrubland were rated highest (up to High), for winter feeding for mule deer, with warm aspect, mature and old dry forest rated highest for winter security/thermal habitat, and floodplain and wet forest in shrub and old forest stages rated highest for reproducing-birthing.
2.10.4 Results
Results of 2008 surveys and a compilation of data from surveys completed between 1991 and 2006 are reported below. Ministry of Environment designated Ungulate Winter Ranges are presented in Maps 2.10.4a and 2.10.4b. Ground transect locations are presented in Map 2.10.4c. Aerial census blocks are presented in Maps 2.10.4d and 2.10.4e.
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Map 2.10.4a. Ungulate Winter Range areas.
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Map 2.10.4b. Ungulate Winter Range areas.
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Map 2.10.4c. Ungulate transect locations.
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Map 2.10.4d. Ungulate aerial census block areas.
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Map 2.10.4e. Ungulate aerial census block areas.
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2.10.4.1. 2008 Inventory Surveys
Winter Track Counts
Each track count transect was sampled three times during the winter in order to better determine the timing of use and distribution of the ungulate species. The transects were surveyed mid January, mid February and late March of 2009 (Table 2.10.4.1a). Snow depths were high in January and March. The average snow depths recorded on the transects were 41 cm in January, 38 cm in February and 46 cm in March.
Table 2.10.4.1a. Survey effort and snow conditions during the winter track counts in 2008.
FSJ Snow Round Date Transect(s) Sampled Length (km) Recent Snow Depth (cm) 1 Jan 13, 2009 2 2.55 6.8 cm Jan 12 73 1 Jan 15, 2009 11, 12 5.95 6.8 cm Jan 12 73 1 Jan 16, 2009 9, 10, 13 8.7 6.8 cm Jan 12 70 1 Jan 17, 2009 4, 5, 7 9.1 6.8 cm Jan 12 67 1 Jan 18, 2009 6, 8, 14 9.35 6.8 cm Jan 12 63 1 Jan 21, 2009 3 2.55 6.8 cm Jan 12 42 2 Feb 14, 2009 8, 11, 12 9.35 2.0 cm Feb 10 26 2 Feb 15, 2009 4, 5, 13 8.2 2.0 cm Feb 10 26 2 Feb 16, 2009 6, 9, 10 9.2 2.0 cm Feb 10 26 2 Feb 17, 2009 2, 3, 14 8.85 2.0 cm Feb 10 26 3 Mar 25, 2009 5, 8, 13 9.65 4.2 cm Mar 25 68 3 Mar 26, 2009 11, 12 7.05 4.2 cm Mar 25 68 3 Mar 27, 2009 6, 9, 10 9.15 4.2 cm Mar 25 66 3 Mar 28, 2009 4, 14 5.85 4.2 cm Mar 25 64 3 Apr 6, 2009 2 3.65 3.4 cm Apr 3 43 3 Apr 7, 2009 3 2.75 3.4 cm Apr 3 37
In total, 112 km were surveyed, and total track counts were 1816 deer, 1038 moose and 716 elk. The total number of pellets observed was 361 deer pellets, 155 moose pellets and 106 elk pellets. Relative use was standardized by dividing the number of tracks per 50 m segment by the number of days since snow. Results from the snow transects show low amounts of use and high variability (Table 2.10.4.1b). Numerous other species were detected during the winter track counts including grouse, marten ( Martes americana ), fisher ( Martes pennanti ), weasel (long-tailed weasel Mustela frenata, ermine Mustela erminea or mink Neovison vison ),
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Table 2.10.4.1b. Pooled results (tracks/day/50 m±std dev) of winter track counts completed in 2008.
Potential Snow overlap with Aspect/ No. n Location Deer Moose Elk Depth project Stratum (cm) footprint 2 185 S FSJ 0.38±0.55 0.27±0.51 0.09±0.36 38 Yes Flat 3 164 S FSJ 0.62±0.62 0.02±0.07 0.03±0.11 32 No Flat Potential Site C 4 175 S FSJ 0.26±0.37 0.06±0.17 0.01±0.07 35 Reservoir Warm Potential Site C 5 190 S Peace 0.02±0.15 0.15±0.29 0.03±0.10 48 Reservoir Flat 6 190 Island 0.30±0.43 0.06±0.20 0.02±0.10 38 Portions Flat 8 227 Island 0.02±0.09 0.20±0.44 0.13±0.36 40 Portions Flat Potential Site C 9 184 Moberly 0.10±0.33 0.09±0.25 0.26±0.46 41 Reservoir Warm Potential Site C 10 169 Moberly 0.04±0.13 0.12±0.15 0.05±0.21 49 Reservoir Cool 11 208 S Peace 0.05±0.18 0.14±0.32 0.01±0.14 49 Portions Cool 12 179 S Peace 0.03±0.11 0.07±0.23 0.09±0.33 44 Portions Cool 13 172 S Peace 0.01±0.04 0.18±0.31 0.01±0.09 51 Portions Cool 14 178 N Peace 0.18±0.35 0.06±0.20 0.07±0.18 34 Portions Flat/Warm All 2238 0.16±0.37 0.12±0.30 0.07±0.26 42
Warm aspects with lower than average snow depth (30 cm) and had the highest use by deer (0.41±0.49) and elk (0.10±0.34), while flat areas had the highest use by moose (0.13 ±0.32). The warm aspect average snow depth of 30 cm was significantly lower than the snow depth on both cool aspects (42 cm) and flat areas (43 cm). No significant difference was found between snow depths on the cool aspects and flat areas. Deer had higher proportions of use up to 45 cm snow depth, while elk had higher use up to 50 cm and moose had higher use up to 55 cm (Figure 2.10.4.1a).
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35% 30% No. Plots 25% Deer Elk 20% Moose 15% 10% 5% 0% 5 10 15 20 25 30 35 40 45 50 55 60 65 70 75 80 Snow Depth (cm)
Figure 2.10.4.1a. Relative occurrence of ungulate tracks by 5 cm snow depth intervals.
Aerial Census
A pre-stratification flight was completed on February 13, 2009 to assess the relative numbers of each species within each block (RIC 2002). Block counts were completed from February 14 to 17, 2009 using a Bell Jet Ranger helicopter with two observers, one navigator/recorder and a pilot. Weather conditions were clear with temperatures ranging from –26 to –4oC. Snow cover was continuous (26 cm as measured at the Fort St John airport) with recent snow (Feb 12) and provided near optimal conditions for the census (RIC 2002).
The aerial census blocks included 21 south aspect blocks (stratum 1), 6 blocks in the Peace River valley bottom upstream of the potential Site C dam (stratum 2), 16 north aspect blocks (stratum 3) and 4 blocks in the Peace River valley bottom downstream of the potential Site C dam (stratum 4). In total, 47 blocks were defined in 2009 (Maps 2.10.4.1d and 2.10.4.1e). Blocks were bounded by obvious geographical features and varied in size from 3 to 20 km 2. The largest blocks were along the river where a large portion of the area was open water and gravel bars. All sample blocks but one were searched in less than one hour of helicopter time (Appendix 11). Thirty-two block counts were completed in 2009, including all 12 around the
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Site C Hydro Project Stage 2 Vegetation and Wildlife Report potential Site C dam footprint area and 20 randomly selected from other strata using a random number table.
In total, the 2009 census detected 1759 deer, 343 moose and 608 elk (Table 2.10.4.2a). Within the potential Site C reservoir, 203 deer, 108 moose and 98 elk were counted (Appendix 11). Within the blocks adjacent to the potential dam site (Blocks 1, 18, 19, 22, 23, 30 and 34), 182 deer, 53 moose and 89 elk were counted.
2.10.4.2. Multiple Year Data Analysis
Aerial Census
There have been three aerial ungulate censuses (conducted in 1991, 2006 and 2009) of the Peace River Corridor. The 1991 survey provided population estimates for deer, moose and elk in the Peace River Valley from the potential Site C dam to Hudson’s Hope. The survey area was expanded to include the Peace River Valley downstream to the Alberta border in 2006 and 2009. Most blocks were randomly selected although the entire potential Site C reservoir was censused each year. In 1991, 18/28 blocks were surveyed, 19/47 blocks were surveyed in 2006 and 32/47 blocks were surveyed in 2009 (Table 2.10.4.2a).
Table 2.10.4.2a. Numbers of ungulates counted in each stratum and number of blocks surveyed during the three aerial censuses (1991, 2006, and 2009).
# of Moose # of Deer # of Elk Stratum Area 1991 2006 2009 1991 2006 2009 1991 2006 2009 South Aspect 75 90 115 1444 701 1423 91 159 376 1 Breaks n=8 n=7 n=15 n=8 n=7 n=15 n=8 n=7 n=15 114 66 108 181 114 203 7 105 98 2 SCR (floodplain) n=6 n=6 n=6 n=6 n=6 n=6 n=6 n=6 n=6 North Aspect 39 12 30 96 39 99 1 0 73 3 Breaks n=4 n=4 n=7 n=4 n=4 n=7 n=4 n=4 n=7 Peace R 29 90 20 34 25 61 4 floodplain N/a N/a N/a n=2 n=4 n=2 n=4 n=2 n=4 (Downstream) Note: the 2006 and 2009 surveys included a larger study area.
Using the Aerial Survey software (University of Idaho 2004), population estimates were produced for the Peace River Corridor (PRC) upstream of the potential Site C dam to Hudson’s Hope, the potential Site C reservoir (SCR) and the PRC downstream of the potential Site C dam
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Table 2.10.4.2b. Ungulate population estimates (± 90%) for the Peace River study area for 1991, 2006 and 2009.
Study Area Species 1991 2006 2009 Deer 2946 ± 503 1146 ± 297 1257 ± 414 PRC n=26 (Upstream) Moose 334 ± 40 442 ± 206 382 ± 192 Elk 162 ± 91 578 ± 294 858 ± 329 Deer 219 ± 78 165 ± 69 227 ± 16 SCR n=6 Moose 118 ± 16 115 ± 69 183 ± 57 Elk 7 ± 2 132 ± 28 167 ± 127 Deer Not surveyed 1576 ± 654 1775 ± 522 PRC n=21 (Downstream) Moose Not surveyed 288 ± 104 283 ± 82 Elk Not surveyed 118 ± 76 243 ± 155
The estimated number of deer in the PRC was substantially lower in 2006 and 2009 than in 1991. The estimate from 2006 was believed to be an underestimate since many deer were observed outside the census area that year. The 2009 count was believed to be more representative since most deer were concentrated in the Peace valley. The lower count likely reflects the reduction in deer numbers following the very severe winter in 2007. The number of moose has remained stable even though some significant mortality occurred in the winter of 2007 (Thiessen 2008). The Peace River valley provides very high capability habitat for moose and most of the local population is expected to survive a severe winter.
Elk have been found in more blocks during each census and their total numbers have consistently increased. They reportedly weathered the severe winter of 2007 by moving to favourable habitats and using agricultural areas to forage. Elk hunting regulations were significantly relaxed in 2008 to reduce their numbers particularly in the agricultural zone, where conflicts with landowners were increasing.
The Ministry of Environment completed aerial surveys for the Peace Region in 2004 (Anderson and Scheck 2004). These surveys focussed on UWRs and other areas of interest in the Peace Region. Surveys of Ungulate Winter Ranges along the Peace River counted 379 mule deer, 7 white-tailed deer, 29 moose and 159 elk (Anderson and Scheck 2004). About half of the elk
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Weather Data
Data relevant to interpretations of wildlife distribution and movements, such as snow depth and temperature, were available from the permanent weather station at the Ft. St. John airport. Accumulated snow on the ground can restrict the movements and habitat use by ungulates in winter. Snow depths approaching chest height on ungulates make movement difficult and most animals seek areas with less snow (Telfer and Kelsall 1979; Parker et al. 1984). Deer are the least tolerant of snow and usually avoid areas with depths exceeding 40 cm. The threshold depth for elk is 50 cm and for moose is 70 cm. Snow depths greater than 50 cm on upper slopes and plateau areas near the Peace River probably precluded use by deer and restricted use by elk. Snow depths were marginally lower in the valley bottom and lowest on south aspect river breaks and benches. The recorded snow depths in the Peace River Corridor would restrict most deer and elk use of the upper slopes, plateau and valley bottom habitats, while moose use of the area would be largely unrestricted by snow depths.
A winter severity index (WSI) for deer was originally developed by Verme (1968) and simplified by the Department of Natural Resources (Wisconsin). The WSI combines the number of days with minimum temperature below -17.8 oC and the number of days with snow depth greater than 45 cm between December 1 and April 30. A WSI above 100 is very severe, 80 to 99 is considered severe, 50 to 79 is moderate and less than 50 is considered mild. The winter severity index for Fort St John shows three very severe winters (1982, 1996, 1997) and seven severe winters during the past 30 years (Figure 2.10.4.2a).
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180 160 140 120 100 80
Deer WSI 60 40 20 0
979 981 983 985 987 989 991 993 995 997 999 001 003 005 007 1 1 1 1 1 1 1 1 1 1 1 2 2 2 2 Year
Figure 2.10.4.2a. Deer Winter Severity Index using data from the Fort St John airport for the previous 30 years.
The pattern of severe winters may contribute to the number of deer counted during the censuses. Severe winters may reduce the deer population and recruitment (population recovery) may take several years. The count in 1991 was done in a moderate winter following eight mild or moderate winters, which may explain the substantially higher numbers. The count in 2006 was done in a very mild winter when animals were observed to be numerous but widely distributed outside the survey area. The census in 2009 followed two severe winters in 2007 and 2008, which were reported to result in significant mortality, and snow depths were sufficient to concentrate animals within the survey area. The 1991 and 2008 census data may be reliably compared, but the 2006 census substantially underestimated ungulate numbers due to low snow depths.
2.10.5 Summary
Habitat relationships for ungulates in the Peace River in winter are well understood and observed numbers are significantly influenced by snow conditions. Both winter mortality and changes to hunting regulations can alter the populations substantially over short time periods (1 to 2 years). The number of deer counted has fluctuated substantially due to changes in their population size and seasonal distribution. Numbers of moose have remained fairly stable and
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2.11 RARE ECOSYSTEMS
Five rare ecological communities are expected to occur in the BWBSmw1 subzone (BC CDC 2009). The Peace River corridor is a unique feature on the landscape and plant communities associated with the river valley may also be unique in the region. Work was required in 2008 to determine the occurrence and abundance of rare ecological communities in the study area.
2.11.1 Introduction
An ecological community is defined as “the assemblage of species that co-occur in defined areas at certain times and that have the potential to interact with each other” (McPeek and Miller 1996, cited in BC CDC 2004). The BC CDC lists rare ecological communities on the provincial Red and Blue lists and provides information on the ecosystems (e.g., site series) that can be associated with those rare ecological communities (BC CDC 2009). Structural stage can also be associated with rare communities, since specific structural stages are often more likely to contain rare communities. For instance, old forests (e.g., structural stage 7) are more likely to contain forested rare communities since they contain the climax plant communities (RISC 2006).
There are three Red-listed and two Blue-listed communities defined for the BWBSmw1 subzone variant (Table 2.11.1a). Two of the communities are non-forested (‘00’ site series).
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Table 2.11.1a. Red- or Blue-listed ecological communities potentially occurring in the BWBSmw1 (BC CDC 2009).
Site Series English Name Scientific Name BC Status Number Arctic rush - Nuttall's alkaligrass - Juncus arcticus - Puccinellia nuttalliana seablite - Suaeda calceoliformis Red 00 mat muhly - arctic rush - Nevada Muhlenbergia richardsonis - Juncus bluegrass arcticus - Poa secunda ssp. juncifolia Red 00 white spruce / red swamp currant Picea glauca / Ribes triste / / oak fern Gymnocarpium dryopteris Blue 05 white spruce / red swamp currant Picea glauca / Ribes triste / Mertensia / tall bluebells paniculata Blue 06 (balsam poplar, black Populus balsamifera ( ssp . balsamifera, cottonwood) - spruces / red-osier ssp . trichocarpa) - Picea spp . / Cornus dogwood stolonifera Red 09
2.11.2 Background
No work documenting rare communities within the study area has been completed. A summary of the plant species associated with each rare community and the environmental conditions that support these communities are presented below.
Arctic rush – Nuttall’s alkaligrass – seablite and Mat muhly – arctic rush – Nevada bluegrass
No detailed information is available, from either the CDC or NatureServe, that describes the species composition or ecological conditions that are associated with these two rare ecological communities. Both community names indicate that the communities occur in herbaceous wetlands with alkaline, saline conditions. Within the study area, Sedge Wetland (SE) habitats are the most likely to contain this community.
White spruce / red swamp current / oak fern
NatureServe (2009) describes the vegetative community for this ecological community as follows:
The open canopy is dominated by white spruce (Picea glauca), very occasionally with lodgepole pine (Pinus contorta). The shrub layer is of moderately high cover, comprised of a diversity of species including some or all of high-bush cranberry (Viburnum edule), black twinberry (Lonicera involucrata), prickly rose
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(Rosa acicularis), red swamp current (Ribes triste) and black gooseberry (Ribes lacustre). The herb layer is rich and diverse, including common mitrewort (Mitella nuda), bunchberry (Cornus canadensis), trailing raspberry (Rubus pubescens), twinflower (Linnaea borealis), palmate coltsfoot (Petasites frigidus var. palmatus), and tall bluebells (Mertensia paniculata), sometimes with high cover of bluejoint (Calamagrostis canadensis) or wild sarsaparilla (Aralia nudicaulis), and low cover of pink wintergreen (Pyrola asarifolia). Numerous other herb species occur less commonly on these sites. The moss layer is dominated by high cover of step moss (Hylocomium splendens) with lesser amounts of Schreber’s red stem (Pleurozium schreberi) and knight’s plume (Ptilium crista-castrensis). Leafy moss (Mnium) species are sometimes present with low cover.
These communities are usually located in subhygric to mesic sites with medium to fine-textured soils and a rich nutrient regime. They are listed as occurring within the 05 site series of the BWBSmw1 (mapcode SO), which usually occurs on northerly aspects (Delong 1990).
White spruce / red swamp current / tall bluebells
NatureServe (2009) describes the vegetative community for this ecological community as follows:
The open canopy is dominated by white spruce (Picea glauca), very occasionally with lodgepole pine (Pinus contorta). The shrub layer is of moderately high cover, comprised of a diversity of species including some or all of high-bush cranberry (Viburnum edule), black twinberry (Lonicera involucrate), prickly rose (Rosa acicularis), red swamp current (Ribes triste) and black gooseberry (Ribes lacustre. The herb layer is rich and diverse, including common mitrewort (Mitella nuda), bunchberry (Cornus canadensis), trailing raspberry (Rubus pubescens), twinflower (Linnaea borealis), palmate coltsfoot (Petasites frigidus var. palmatus), and tall bluebells (Mertensia paniculata), sometimes with high cover of bluejoint (Calamagrostis canadensis) or wild sarsaparilla (Aralia nudicaulis), and low cover of pink wintergreen (Pyrola asarifolia) sometimes. Numerous other herb species occur less commonly on these sites. The moss layer is dominated by high cover of step moss (Hylocomium splendens) with lesser amounts of Schreber’s red
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stem (Pleurozium schreberi) and knight’s plume (Ptilium crista-castrensis). Leafy moss (Mnium) species are sometimes present with low cover.
These communities, similar to the previous, are usually located in subhygric to mesic sites with medium- to fine-textured soils and a rich nutrient regime. They are listed to occur within the 06 site series of the BWBSmw1 (mapcode SC), which usually does not occur on northerly aspects and often has seepage water (Delong 1990).
Balsam poplar, black cottonwood - spruces / red-osier dogwood
No information is available, from either the CDC or NatureServe, that describes the vegetative species or ecological conditions that are associated with this rare ecological community. This community is listed as occurring within the 09 site series of the BWBSmw1 (mapcode Fm02).
2.11.3 Methods
The potential for rare ecological communities to occur within the study area was assessed following methods outlined in the BC Resource Inventory Standards Committee’s (RISC) Standard for Mapping Ecosystems at Risk in British Columbia: An Approach to Mapping Ecosystems at Risk and Other Sensitive Ecosystems (2006). Information on the site series that potentially support rare communities was gathered from the BC CDC (2009) and NatureServe (2009), and used in conjunction with structural stage information to assign a rank to each TEM map unit within the study area (Table 2.11.3a). A four-class ranking scheme (high, moderate, low, or none, RIC 1999a) was used to rank the potential for an ecological community to occur in each site series / structural stage combination. Ecosystems with a high ranking had the highest potential to contain a rare ecological community, while ecosystems ranked low had a lower potential. Ecosystems ranked as none were not expected to contain a rare community. This ranking system predicts the potential for a community to occur in a specific site series and structural stage combination, but does not confirm that the ecosystem is present. The actual occurrence of rare ecological communities can only be determined during site visits. Targeted searches for rare ecosystems were not completed since the information available for each rare community is not sufficient to allow field identification. If detailed descriptions become available, the existing field data from TEM map truthing should be reviewed to determine if any rare ecosystems were detected during previous field work.
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Table 2.11.3a. Ranking assigned to site series and structural stage combinations in the TEM map area.
English Name TEM Site Series Structural Stage Rank Arctic rush - Nuttall's alkaligrass - seablite 00 (SE) 2 High mat muhly - arctic rush - Nevada 00 (SE) 2 High bluegrass 7 High white spruce / red swamp currant / oak 05 (SO) fern 6 Moderate 3-5 Low 7 High white spruce / red swamp currant / tall 06 (SC) bluebells 6 Moderate 3-5 Low 7 High (balsam poplar, black cottonwood) - 09 (Fm02) spruces / red-osier dogwood 6 Moderate 3-5 Low All other site series 1-7 None
Regional rarity was also considered during the assessment of ecological communities. The TEM map (Keystone Wildlife Research Ltd. 2006a; Appendix 3a) was reviewed to determine which ecosystems were locally rare in the mapped area. The vegetation resource inventory (VRI) map (1:250,000 mapsheet 94A) that includes the Peace River Corridor was also reviewed to give an indication of the forest composition in the region. Regional rarity was defined as ecosystem units that occur in less than 2% of the study area.
2.11.4 Results
Areas with potential to support rare ecosystems are presented in Maps 2.11.4a and 2.11.4b.
2.11.4.1. Rare Ecological Communities
In the Peace River Corridor (PRC) study area, 471 ha (of approximately 64,000 ha), or 0.7%, has a high probability of containing a rare ecological community (Table 2.11.4.1a). The potential Site C reservoir (SCR) contains 47.6 ha (0.5%) with a high potential to contain a rare ecosystem. The transmission line (TL) study area contains 315 ha (4%) with a high potential to contain a rare ecological community. Overall, 93% of the habitat present in the Peace River Corridor study area and 95% of the habitat present in the Transmission Line study area, is unlikely to contain a rare ecological community.
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Table 2.11.4.1a. Summary of area (ha) and percentage area in each study area of rare ecological community probabilities.
Area (ha) in each probability class Study Area High Moderate Low None Total PRC (+SCR) 417.1 1402.5 2230.0 52427.5 56477.1 SCR 47.6 459.7 858.6 7940.0 9305.9 TL 315.0 60.5 15.9 7098.8 7490.2 Total 732.1 1463.0 2245.9 59526.3 63967.3 Percentage of area in the PRC or TL in each probability class Study Area % High % Moderate % Low % None PRC 0.7% 2.5% 3.9% 92.8% SCR 0.5% 4.9% 9.2% 85.3% TL 4.2% 0.8% 0.2% 94.8%
Most of the high and moderate-rated areas within the transmission line study area are associated with wetlands. The high and moderate-rated areas in the Peace River Corridor and potential Site C reservoir are concentrated on the south side of the river.
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Map 2.11.4a. Areas potentially supporting rare ecosystems.
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Map 2.11.4b. Areas potentially supporting rare ecosystems.
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2.11.4.2. Regionally Rare Ecosystems
The analysis of regional rarity in the TEM map area revealed that 29 out of 40 ecosystem units in the study area comprised less than 2% of the total area (Appendix 12). The location of the study area results in relatively high proportions of anthropogenic features (14%) and river units (10%). Deciduous forests account for over 40% of the area and mixed forests account for 20%. Deciduous forests also account for 25% of the mature to old forest in the study area compared to 15% in mixed forests.
TEM map units were grouped into similar broad habitat types to allow comparison with regional mapping (Table 2.11.4.3a). Broad habitat types included: Deciduous Forest (AM:ap, BL:al, LL:ak, SC:ab, SC:ep, SH:ep, SH:ac, SW:as), Grassland/Shrubland (AS, WW), Mixed Forest (AM, BL, BT, Fm02, LL, SC, SH, SO, SW, TS), Open Water (LA, OW, PD, RE, RI), other non- forested (CB, ES, GB, RO) and Wetland (SE, WH, WS). This review indicates that wetland habitats are the least prevalent in the study areas, comprising about 3% of the total study area. Deciduous forest is the most abundance broad habitat type.
Table 2.11.4.3a. Summary of percent occurrence of forested units occurring in the TEM map area.
% of TEM mapped area in each structural stage Broad Habitat Type n/a 1 2 3 4 5 6 7 Total Anthropogenic 1.4 0.3 12.7 0.5 0.0 0.0 0.0 0.0 14.9 Deciduous Forest 0.0 0.0 0.0 4.2 12.2 20.5 5.3 0.0 42.3 Grassland/Shrubland 0.0 0.0 3.4 3.3 0.0 0.0 0.0 0.0 6.7 Mixed Forest 0.0 0.0 0.0 2.9 2.0 7.4 7.7 0.3 20.4 Open Water 9.5 0.0 0.0 0.0 0.0 0.0 0.0 0.0 9.5 Other non-forested 0.0 3.2 0.0 0.0 0.0 0.0 0.0 0.0 3.2 Wetland 0.0 0.0 1.5 1.4 0.0 0.0 0.0 0.0 2.9
Review of habitats present in the regional area (VRI mapsheet) indicates that 30% of the area is deciduous, 10% is mixed forest, 19% is coniferous forest and 40% is non-forested (Table 2.11.4.3b). Young forest makes up 23% of the forested area, with 31% in mature forest and 0% as old forest.
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Table 2.11.4.3b. Summary of percent occurrence of stand types occurring in the VRI data of the area.
Forest Age % Stand Composition (years) Broadleaf Mixed Coniferous N/A (nonforested) Total 0 0.0 0.0 0.0 40.7 40.7 1-20 0.1 0.4 0.5 0.0 1.0 21-40 2.1 0.9 0.7 0.0 3.6 41-80 13.9 3.9 5.6 0.0 23.3 81-250 14.6 4.8 12.0 0.0 31.4 250+ 0.0 0.0 0.0 0.0 0.0 Total 30.7 9.9 18.7 40.7 100.0
The relative amounts of main habitat types were compared for the Peace River Corridor and the regional study area. The Peace River Corridor has a higher proportion of deciduous (broadleaf) forests than does the regional area. This observation is supported by the fire history in the river valley, which has resulted in the loss of the coniferous component in much of the forests in the valley.
2.11.5 Summary
The five CDC-listed rare ecosystems have not been located in the study area. Because these plant communities are poorly described, their occurrence must be confirmed by the regional ecologist. There is a high likelihood that some will occur in a small portion of the study area.
3.0 CONCLUSION
In 2008, surveys were completed for raptor and heron nests, amphibians, owls, songbirds, butterflies, dragonflies, rare vascular plants, bats, waterfowl and water-associated birds and ungulates. A desktop analysis was also completed to identify rare ecosystems. This field program was a continuation of the 2005/2006 programs and was intended to fill information gaps from the previous years' surveys.
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5.0 PERSONAL COMMUNICATIONS
Hilton, S. Biologist and Manager. Keystone Wildlife Research Ltd. 2009.
Kinsey, S. Biologist. Alpine Environmental Services. Personal Communication to L. Andrusiak, 2008.
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6.0 APPENDICES
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Appendix 1. Summary of proposal for 2008 wildlife and plant surveys in the Peace River area.
BC Hydro and Power Authority is taking a stage-by-stage approach to the evaluation of Site C. At the end of each stage of the process, BC Hydro will make a recommendation to the provincial government about whether to proceed to the next stage of project planning and development. BC Hydro has asked Keystone Wildlife Research to complete Wildlife and Terrestrial studies during 2008 and 2009 for the Site C project. These studies are a component of Stage 2: Project Definition and Consultation.
Wildlife assessments of the Site C project have been completed three times between 1976 and 1993 (Blood 1979; Penner 1976; Simpson 1991). Some additional work has been carried out by BC Hydro and others since 1993 (Fraker and Hawkes 2000; Robertson 1999; Robertson et al. 1996). A field program was initiated in 2005 (Hawkes et al. 2006) and 2006 (Keystone Wildlife Research Ltd. 2006) to fill information gaps for significant species that are known to be present and investigate the presence of other listed species. The proposed 2008/2009 field surveys are a continuation of the 2005/2006 programs and are intended to fill information gaps from the previous years' surveys. Overall, the field program will provide information to support an environmental impact assessment.
The objectives of the 2008/2009 field program are to:
Determine the presence, and relative abundance where possible, of target taxa within the study area;
Develop habitat suitability ratings for previously unidentified target taxa (species that have recently been re-classified as at risk by the Conservation Data Centre or Committee on the Status of Endangered Wildlife in Canada);
Determine the presence of rare plants within the study area; and
Determine the potential for rare plant communities to occur within the study area.
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Appendix 2. Potential VEC list for terrestrial wildlife in the Peace River Valley.
CWS Priority COSEWIC SARA Provincial region BCCF Scientific Name English Name Status* Schedule Status 6** Priority Class Special Bufo borealis Western Toad Concern 1 Yellow 2 Amphibian Aegolius funereus Boreal Owl Not at Risk Yellow S Birds Ammodramus leconteii Le Conte's Sparrow Blue M 4 Birds Ammodramus Nelson's Sharp- nelsoni tailed Sparrow Not at Risk Red H 2 Birds Ardea herodias herodias Great Blue Heron Blue 2 Birds Special Asio flammeus Short-eared Owl Concern 3 Blue H 2 Birds Botaurus lentiginosus American Bittern Blue H 2 Birds Bubo virginianus Great Horned Owl Yellow Birds Broad-winged Buteo platypterus Hawk Blue M 4 Birds Olive-sided Contopus cooperi Flycatcher Threatened Yellow H Birds Coturnicops Special noveboracensis Yellow Rail Concern 1 Red M 1 Birds Bay-breasted Dendroica castanea Warbler Red H 2 Birds Dendroica tigrina Cape May Warbler Red M 2 Birds Black-throated H Dendroica virens Green Warbler Blue 2 Birds Euphagus carolinus Rusty Blackbird Blue H 2 Birds Grus canadensis Sandhill Crane Not at Risk Blue 2 Birds Haliaeetus leucocephalus Bald Eagle*** Yellow Birds Hirundo rustica Barn Swallow Blue M 2 Birds Connecticut M Oporornis agilis Warbler Red 2 Birds Strix nebulosa Great Gray Owl Not at Risk Yellow M Birds Wilsonia canadensis Canada Warbler Threatened Blue H 2 Birds Arctic Skipper, Carterocephalus mandan palaemon mandan subspecies Blue 4 Insects Common Wood- Cercyonis pegala nymph, nephele nephele subspecies Blue 4 Insects
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CWS Priority COSEWIC SARA Provincial region BCCF Scientific Name English Name Status* Schedule Status 6** Priority Class Coenagrion angulatum Prairie Bluet Blue 4 Insects Common Ringlet, Coenonympha tullia benjamini benjamini subspecies Blue 4 Insects Enallagma hageni Hagen's Bluet Blue 4 Insects Beaverpond Epitheca canis Baskettail Blue 4 Insects Hesperia assiniboia Assiniboine Skipper Red 3 Insects Oeneis alberta Alberta Arctic Red 3 Insects Oeneis uhleri Uhler's Arctic Blue 4 Insects Old World Papilio machaon Swallowtail, pikei pikei subspecies Blue 3 Insects Phyciodes batesii Tawny Crescent Blue 4 Insects Arctic Blue, Plebejus glandon lacustris lacustris subspecies Blue 4 Insects Pyrgus communis Checkered Skipper Blue Insects Satyrium liparops Striped Hairstreak Red 3 Insects Coral Hairstreak, Satyrium titus titus titus subspecies Red 3 Insects Aphrodite Fritillary, Speyeria aphrodite manitoba manitoba subspecies Blue 4 Insects Great Spangled Fritillary, Speyeria cybele pseudocarpenteri pseudocarpenteri subspecies Red 3 Insects Martes pennanti Fisher Blue 2 Mammals Myotis septentrionalis Northern Myotis Blue 2 Mammals Castor canadensis Beaver*** Yellow Mammals Alces americanus Moose*** Yellow Mammals Odocoileus hemionus Mule Deer*** Yellow Mammals Cervus canadensis Elk*** Yellow Mammals *NAR =Not At Risk, SC =Special Concern; **H =High, M =Medium, S =Stewardship; *** Regional concern.
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Appendix 3a. TEM map legend for the Peace River Corridor and the Transmission Line (Keystone Wildlife Research Ltd. 2008a).
Map Code Site Series # Ecosystem Name Forested Units AM 01 White spruce-Trembling aspen - Step moss AM: ap $01 $ Trembling aspen - Creamy peavine (seral association) AMy: ap $01 $ Trembling aspen - Creamy peavine, moist (seral association) AMk: ap $01 $ Trembling aspen - Creamy peavine, cool aspect (seral association) AMw: ap $01 $ Trembling aspen - Creamy peavine, warm aspect (seral association) AS 00 White spruce-Trembling aspen - Soopolallie BL 04 Black spruce - Lingonberry - Coltsfoot BL: al $04 $ Trembling aspen - Labrador tea (seral association) BT 08 Black spruce - Labrador tea - Sphagnum Fm02 09 Black cottonwood - White spruce - Red-osier dogwood LL 02 Lodgepole pine - Lingonberry - Velvet-leaved blueberry LL: ak $02 $ Trembling aspen - Kinnikinnick (seral association) SC 06 White spruce - Currant - Bluebells SC: ab $05 $Trembling aspen - Black Twinberry (seral association) SC: ep $05 $ Paper birch - Red-osier dogwood (seral association) SE 00 Sedge Wetland SH 07 White spruce - Currant - Horsetail SH: ac $07 $Balsam poplar - Cow parsnip (seral association) SH: ep $07 $ Paper birch - Common paper birch -Dogwood (seral association) SO 05 White spruce - Currant - Oak fern SW 03 White spruce - Wildrye - Peavine SW: as $03 $Trembling aspen - Soopolallie (seral association) TS 10 Tamarack - Sedge - Fen WH 00 Willow - Horsetail - Sedge - Riparian Wetland WS 00 Willow - Sedge - Wetland WW 00 Fuzzy-spiked Wildrye - Wolf willow Nonvegetated/Anthropogenic Units CB 00 Cutbank CF 00 Cultivated field (incl. pastures) ES 00 Exposed soil GB 00 Gravel bar GP 00 Gravel Pit LA 00 Lake MI 00 Mine OW 00 Shallow open water PD 00 Pond RE 00 Reservoir RI 00 River RN 00 Railway RO 00 Rock RW 00 Rural July 2009 -257-
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Map Code Site Series # Ecosystem Name RY 00 Reclaimed Garbage Dump RZ 00 Road surface UR 00 Urban
Appendix 3b. Structural stage definitions (RIC 1998a). Structural Definition Stage 1 Sparse/bryoid (< 20 yrs since major disturbance unless disclimax ecosystem) 1a Sparse (less than 10% vegetation cover) 1b Bryoid (bryophyte and lichen-dominated communities (>50% of total vegetation cover)) 2 Herb (< 20 yrs old unless disclimax) 2a Forb-dominated (dominated by non-graminoid herbs) 2b Graminoid-dominated (dominated by grasses, sedges, reeds and rushes) 2d Dwarf Shrub (dominated by dwarf woody species) 3 Shrub (shrubs <10 m tall, < 20 yrs old for forested sites) 3a Low Shrub (shrubs < 2 m tall ) 3b Tall Shrub (shrubs 2-10 m tall ) 4 Pole /Sapling (trees > 10 m tall & usually < 40 yrs old) 5 Young Forest (trees > 10 m tall & 40-80 yrs old) 6 Mature Forest (trees > 10 m tall; 80-140 yrs old) 7 Old Forest (trees > 10 m tall; >140 yrs old)
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Appendix 4a. Summary of pond-breeding amphibian survey effort in the Peace River Corridor in 2008. Wetland Label Date Total Search Time** (hr:min) R8* 11-Jun-08 0:42 27-May-08 1:46 R9 11-Jun-08 0:28 RB23* 23-Jun-08 1:10 RB27a* 09-Jun-08 0:48 26-May-08 1:32 RB9* 10-Jun-08 0:30 21-Jun-08 1:10 24-Jun-08 3:10 WAT* 13-Aug-08 6:36 16-Aug-08 2:30 WBF 27-May-08 1:00 WR 27-May-08 0:40 27-May-08 0:20 WS 11-Jun-08 0:12 Total 22:34 *indicates site is in the potential Site C reservoir area; **Total search time is total survey time X number of surveyors (2).
Appendix 4b. Summary of pond-breeding amphibian survey effort on the Transmission Line in 2008. Wetland Label Date Total Search Time* (hr:min) TC_1a 10-May-08 1:30 TC_1b 10-May-08 1:20 TC_2 10-May-08 0:40 TC_3 10-May-08 0:16 TC_4 10-May-08 0:20 TC_5 10-May-08 1:20 TC_6 10-May-08 0:34 10-May-08 0:34 TC_7 12-Aug-08 0:32 TC_8 10-May-08 0:14 10-May-08 4:40 19-May-08 0:36 01-Jun-08 0:10 TC_9 02-Jun-08 0:20 28-Jun-08 0:12 27-Jul-08 0:30 12-Aug-08 1:00
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Wetland Label Date Total Search Time* (hr:min) TC_10 11-May-08 2:50 TC_11 11-May-08 0:46 TC_12 11-May-08 0:20 TC_13 11-May-08 3:10 TC_14 11-May-08 0:24 TC_15 11-May-08 0:02 TC_16 11-May-08 1:48 TC_17 11-May-08 0:02 TC_18 11-May-08 0:02 TC_19 11-May-08 0:50 11-May-08 1:00 TC_20 19-May-08 1:10 TC_21 12-May-08 0:30 TC_22 12-May-08 0:30 12-May-08 0:46 TC_23 13-Jun-08 0:54 TC_24 19-May-08 0:02 TC_25 19-May-08 0:36 TC_26 19-May-08 1:00 19-May-08 0:42 TC_27 29-Jul-08 0:40 TC_28 23-May-08 0:02 TC_29 02-Jun-08 0:24 TC_30 03-Jun-08 0:30 TC_31 03-Jun-08 0:38 TC_32 03-Jun-08 0:32 TC_33 03-Jun-08 0:16 TC_35 05-Jun-08 0:10 05-Jun-08 1:20 TC_36 27-Jun-08 1:30 TC_37 12-Jun-08 2:50 TC_38 13-Jun-08 3:00 TC_39 26-Jun-08 0:38 03-Jun-08 0:30 27-Jun-08 0:34 TC_40 28-Jul-08 0:30 13-Aug-08 0:40 TC_41 28-Jun-08 0:30 03-Jun-08 0:40 28-Jun-08 0:20 TC_42 28-Jul-08 1:20 13-Aug-08 0:30
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Wetland Label Date Total Search Time* (hr:min) 27-Jul-08 1:00 TC_43 13-Aug-08 0:42 Total 51:58 * Total search time is total survey time X number of surveyors (2).
Appendix 4c. Amphibian species detected during wetland surveys in the Peace River Corridor in 2008. Boreal Unknown Wetland Western Toad Chorus Wood Frog Total Date Frog Label Frog Adult Juvenile Tadpole Adult Adult Juvenile Tadpole Unknown Adult R8* 11-Jun 13 1 14 27-May 3 3 R9 11-Jun 1 4 5 RB23* 23-Jun 20113 1 20114 RB27a* 9-Jun 257 257 26-May 3 2 5 RB9* 10-Jun 2 2 21-Jun 1 1 700 5 7 714 WAT* 24-Jun 6 6 WBF 27-May 5 10000 5 2 10012 WR 27-May 2 1 1 3 7 27-May 1 1 WS 11-Jun 102 102 Total 9 5 31071 6 9 33 102 1 6 31242 *indicates site is in the potential Site C reservoir area.
Appendix 4d. Amphibian species detected during wetland surveys in the Transmission Line study area in 2008. Boreal Transect Unknown Western Toad Chorus Wood Frog Segment Date Frog Total Frog Label Adult Juvenile Tadpole Adult Egg Adult Egg Juvenile Tadpole Unknown Adult TC_10 11-May 4 5 1 10 TC_11 11-May 5 1 1 7 TC_12 11-May 4 15 19 TC_13 11-May 6 2 3 11 TC_14 11-May 5 5 TC_16 11-May 5 3 8 TC_19 11-May 10 1 13 24 TC_1a 10-May 14 3 17 TC_1b 10-May 4 1 11 16 TC_2 10-May 1 1 TC_20 11-May 1 3 4
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Boreal Transect Unknown Western Toad Chorus Wood Frog Segment Date Frog Total Frog Label Adult Juvenile Tadpole Adult Egg Adult Egg Juvenile Tadpole Unknown Adult TC_21 12-May 10 10 TC_22 12-May 1 2 12-May 3 10 4 17 TC_23 13-Jun 1 1 4 TC_24 19-May 1 1 2 TC_25 19-May 2 2 19-May 1 1 TC_27 29-Jul 3 3 TC_31 3-Jun 1 2 9 TC_32 3-Jun 13 1 14 TC_33 3-Jun 1 1 5-Jun 1 10 1 12 TC_36 27-Jun 1 4 TC_37 12-Jun 16 1 2 2 103 TC_38 13-Jun 1 30000 1 30005 TC_39 26-Jun 22 4 4 30 3-Jun 1000 1000 27-Jun 15100 15101 TC_40 28-Jun 2 2 28-Jul 50 16 67 13-Aug 3 1 4 TC_41 28-Jun 50 51 3-Jun 2 20 22 28-Jun 100 103 TC_42 28-Jul 1 2 3 6 13-Aug 1 1 3 27-Jul 400 3 3 406 TC_43 13-Aug 15 1 2 19 TC_5 10-May 7 2 15 24 TC_6 10-May 2 2 TC_7 10-May 5 5 10-May 2 7 6 15 19-May 5000 5000 TC_9 1-Jun 4 4 28-Jun 1 1 Total 7 1510 45105 96 1 71 72 25 5175 6 3 52176
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Appendix 5a. Owl survey transects completed in 2008. Study Area Transect Total Survey Total Stations Target Species Visit Date Name Label Time (hrs:min) Surveyed 0 Boreal Owl 15-May-08 2:15 9 0 Boreal Owl 8-Jun-08 2:15 9 0 Boreal Owl 26-Jun-08 2:14 9 0 Great Gray Owl 13-May-08 2:00 8 0 Great Gray Owl 10-Jun-08 2:00 8 0 Great Horned Owl 14-May-08 2:30 10 0 Great Horned Owl 9-Jun-08 2:42 10 1 Boreal Owl 18-May-08 2:20 9 1 Boreal Owl 29-May-08 2:00 8 1 Boreal Owl 24-Jun-08 1:52 8 1 Great Gray Owl 16-May-08 2:02 8 1 Great Gray Owl 30-May-08 2:00 8 1 Great Horned Owl 17-May-08 2:32 9 1 Great Horned Owl 31-May-08 2:15 9 5 Boreal Owl 17-May-08 1:45 7 Peace River Corridor 5 Boreal Owl 26-May-08 2:01 8 5 Boreal Owl 25-Jun-08 2:00 8 5 Great Gray Owl 16-May-08 1:45 7 5 Great Gray Owl 28-May-08 2:00 8 5 Great Horned Owl 18-May-08 2:00 8 5 Great Horned Owl 27-May-08 2:14 9 6 Boreal Owl 14-May-08 2:08 8 6 Boreal Owl 27-Jun-08 1:56 8 6 Great Gray Owl 13-May-08 1:44 7 6 Great Horned Owl 15-May-08 2:22 9 7 Boreal Owl 6-May-08 2:10 8 7 Boreal Owl 13-Jun-08 1:16 5 7 Boreal Owl 17-Jun-08 1:30 6 7 Great Gray Owl 5-May-08 2:00 7 7 Great Gray Owl 12-Jun-08 2:06 8 7 Great Gray Owl 16-Jun-08 1:30 6 PRC Total 63:24 249 Transmission 2 Boreal Owl 7-May-08 1:30 6 Line 2 Boreal Owl 14-Jun-08 1:30 6 2 Boreal Owl 19-Jun-08 1:39 7 2 Great Gray Owl 8-May-08 1:45 7 2 Great Gray Owl 15-Jun-08 1:32 6 2 Great Gray Owl 18-Jun-08 1:30 6 8 Boreal Owl 10-May-08 2:15 9 8 Boreal Owl 12-Jun-08 2:19 9 8 Boreal Owl 25-Jun-08 1:45 7 8 Great Gray Owl 9-May-08 2:00 8 8 Great Gray Owl 13-Jun-08 1:15 5 8 Great Gray Owl 24-Jun-08 1:46 7
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Study Area Transect Total Survey Total Stations Target Species Visit Date Name Label Time (hrs:min) Surveyed 10 Boreal Owl 7-May-08 2:11 8 10 Boreal Owl 13-Jun-08 2:08 8 10* Boreal Owl 22-Jun-08 1:07 6 10 Great Gray Owl 8-May-08 1:45 7 10 Great Gray Owl 12-Jun-08 1:47 7 10 Great Gray Owl 23-Jun-08 1:44 7 TL Total 31:28 126 Total 94:52 375 *inclement weather was experienced during this survey
Appendix 5b. Results of owl surveys completed in the PRC in 2008. Species Transect Label Date Total Detections 13-May-08 1 14-May-08 2 0 08-Jun-08 3 09-Jun-08 2 26-Jun-08 1 17-May-08 4 18-May-08 3 19-May-08 2 1 29-May-08 3 Barred Owl 31-May-08 2 25-Jun-08 1 18-May-08 1 26-May-08 2 5 27-May-08 1 28-May-08 1 13-May-08 1 6 16-May-08 3 7 17-Jun-08 1 Barred Owl Total 34 Boreal Owl 5 26-May-08 1* Boreal Owl Total 1 0 13-May-08 1* 16-May-08 1* 5 26-May-08 1 28-May-08 1* Great Gray Owl 6 13-May-08 1* 05-May-08 1* 7 12-Jun-08 1* 16-Jun-08 1* Great Gray Owl Total 8 Great Horned Owl 0 14-May-08 1* 1 31-May-08 2*
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Species Transect Label Date Total Detections 5 27-May-08 1* 6 27-Jun-08 1 7 05-May-08 2 7 06-May-08 1 7 16-Jun-08 2 7 17-Jun-08 1 Great Horned Owl Total 11 17-May-08 1 1 18-May-08 1 Northern Saw-whet Owl 19-May-08 1 06-May-08 3 7 13-Jun-08 1 Northern Saw-whet Owl Total 7 5 16-May-08 1 Unidentified Owl 7 06-May-08 1 Unidentified Owl Total 2 Owls Total 63 *detection occurred during targeted surveys for that species.
Appendix 5c. Results of owl surveys completed in the TL in 2008. Species Transect Label Date Total Detections 07-May-08 1 2 14-Jun-08 1 Barred Owl 07-May-08 2 10 08-May-08 1 Barred Owl Total 5 Great Gray Owl 8 05-May-08 1* Great Gray Owl Total 1 07-May-08 2 Northern Saw-whet 2 14-Jun-08 1 Owl 15-Jun-08 3 10 08-May-08 3 Northern Saw-whet Owl Total 9 Owls Total 15 *detection occurred during targeted surveys for that species.
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Appendix 6a. Detailed summary of breeding bird survey effort in the Peace River Corridor in 2008. Transect Date Surveyed Total Time Surveyed hrs:min Number point count stations 30-May-08 5:06 17 12 8-Jun-08 4:23 18 20-Jun-08 4:00 18 28-May-08 3:49 18 13 4-Jun-08 3:42 18 27-Jun-08 3:12 18 29-May-08 6:26 9 A 8-Jun-08 3:35 11 20-Jun-08 3:31 11 28-May-08 5:51 16 B 6-Jun-08 0:00* 0* 25-Jun-08 4:30 16 31-May-08 5:12 16 C 8-Jun-08 0:00* 0* 23-Jun-08 4:05 16 1-Jun-08 4:30 12 E 9-Jun-08 4:05 13 19-Jun-08 4:06 13 2-Jun-08 3:50 12 F 9-Jun-08 4:15 14 19-Jun-08 3:41 14 25-May-08 4:40 13 G 7-Jun-08 3:38 16 24-Jun-08 3:35 16 26-May-08 5:07 15 H 10-Jun-08 4:05 15 21-Jun-08 4:37 15 25-May-08 4:12 15 J 7-Jun-08 3:45 15 24-Jun-08 3:51 15 26-May-08 4:52 14 K 10-Jun-08 4:52 12 21-Jun-08 4:00 14 27-May-08 5:28 13 L 11-Jun-08 3:55 13 22-Jun-08 3:26 12 27-May-08 4:16 14 N 11-Jun-08 4:14 14 22-Jun-08 1:30* 5* Q 28-May-08 3:20 14 July 2009 -266-
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Transect Date Surveyed Total Time Surveyed hrs:min Number point count stations 6-Jun-08 3:30 14 23-Jun-08 3:00 14 24-May-08 0:00* 0* X 5-Jun-08 3:00 10 26-Jun-08 3:45 10 Total 172:27 588 *not completed due to poor weather.
Appendix 6b. Detailed summary of breeding bird survey effort for the Transmission Line in 2008. Number point count Transect Date Surveyed Total Time Surveyed hrs:min stations 23-May-08 3:33 12 8 12-Jun-08 3:40 14 26-Jun-08 3:11 14 22-May-08 3:35 12 9 2-Jun-08 3:30 16 28-Jun-08 3:10 15 23-May-08 4:40 14 10 12-Jun-08 3:55 14 27-Jun-08 3:20 14 24-May-08 0:00* 0* 11 5-Jun-08 4:50 17 25-Jun-08 4:14 17 22-May-08 3:39 10 14 3-Jun-08 3:13 13 28-Jun-08 2:41 13 Total 51:12 195 *not completed due to poor weather.
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Appendix 6c. Passerine and upland game bird species detected during 2005, 2006 and 2008 wildlife surveys. Study area and year English Name Scientific Name BC PRC Periphery PRC PRC TL Status 2005 2005 2006 2008 2008 Empidonax Alder Flycatcher Yellow X X X X X alnorum Corvus American Crow Yellow X X X X brachyrhynchos American Pipit Anthus rubescens Yellow X* X* X* American Redstart Setophaga ruticilla Yellow X X X X X American Robin Turdus migratorius Yellow X X X X X American Three-toed Picoides dorsalis Yellow X X X X X Woodpecker American Tree Sparrow Spizella arborea Yellow X* X* X* Barn Swallow Hirundo rustica Blue X X* Baltimore Oriole Icterus galbula Yellow X X X X Black-and-white Warbler Mniotilta varia Yellow X X X X X Dendroica Bay-breasted Warbler Red X castanea Black-billed Magpie Pica hudsonia Yellow X X X X X* Black-capped Chickadee Poecile atricapillus Yellow X X X X X Belted Kingfisher Megaceryle alcyon Yellow X X X X Brown-headed Cowbird Molothrus ater Yellow X X X X X Blue-headed Vireo Vireo solitarius Yellow X X X X X Blackpoll Warbler Dendroica striata Yellow X X X Bank Swallow Riparia riparia Yellow X X X* Black Swift Cypseloides niger Yellow X* Blue Jay Cyanocitta cristata Yellow X X X X X* Bombycilla Bohemian Waxwing Yellow X* garrulus Boreal Chickadee Poecile hudsonica Yellow X X X X X Euphagus Brewer's Blackbird Yellow X X cyanocephalus Brown Creeper Certhia americana Yellow X X Black-throated Green Dendroica virens Blue X X X X X Warbler Calliope Hummingbird Stellula calliope Yellow X Cape May Warbler Dendroica tigrina Red X Wilsonia Canada Warbler Blue X X X X canadensis Clay-colored Sparrow Spizella pallida Yellow X X X X X Bombycilla Cedar Waxwing Yellow X X X X X* cedrorum Chipping Sparrow Spizella passerina Yellow X X X X X Petrochelidon Cliff Swallow Yellow X X* X* pyrrhonota Common Grackle Quiscalus quiscula Yellow X X X*
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Study area and year English Name Scientific Name BC PRC Periphery PRC PRC TL Status 2005 2005 2006 2008 2008 Common Nighthawk Chordeiles minor Yellow X* X X Common Raven Corvus corax Yellow X X X X X Common Redpoll Carduelis flammea Yellow X* X* Connecticut Warbler Oporornis agilis Red X X X X X Common Yellowthroat Geothlypis trichas Yellow X X X X X Dark-eyed Junco Junco hyemalis Yellow X X X X X Picoides Downy Woodpecker Yellow X X X X X pubescens Eastern Kingbird Tyrannus tyrannus Yellow X X X Eastern Phoebe Sayornis phoebe Yellow X X X European Starling Sturnus vulgaris Exotic X X X Coccothraustes Evening Grosbeak Yellow X X X X* vespertinus Fox Sparrow Passerella iliaca Yellow X X X X X* Golden-crowned Kinglet Regulus satrapa Yellow X X X X Zonotrichia Golden-crowned Sparrow Yellow X* atricapilla Dumetella Gray Catbird Yellow X X carolinensis Perisoreus Gray Jay Yellow X X X X X canadensis Empidonax Hammond's Flycatcher Yellow X X X hammondii Hairy Woodpecker Picoides villosus Yellow X X X X X Hermit Thrush Catharus guttatus Yellow X X X X X Eremophilla Horned Lark Yellow X* alpestris House Sparrow Passer domesticus Exotic X* House Wren Troglodytes aedon Yellow X X X X Calcarius Lapland Longspur Yellow X* lapponicus Ammodramus Le Conte's Sparrow Blue X X X X leconteii Empidonax Least Flycatcher Yellow X X X X X minimus Lincoln's Sparrow Melospiza lincolnii Yellow X X X X X Cistothorus Marsh Wren Yellow X X X X* palustris Dendroica Magnolia Warbler Yellow X X X X X magnolia Mourning Dove Zenaida macroura Yellow X X Oporornis Mourning Warbler Yellow X X X X philadelphia Nelson’s Sharp-tailed Ammodramus Red X* Sparrow nelsoni Northern Flicker Colaptes auratus Yellow X X X X X
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Study area and year English Name Scientific Name BC PRC Periphery PRC PRC TL Status 2005 2005 2006 2008 2008 Northern Shrike Lanius excubitor Yellow X Seiurus Northern Waterthrush Yellow X X X X X noveboracensis Northern Rough-winged Stelgidopteryx Yellow X X Swallow serripennis Orange-crowned Warbler Vermivora celata Yellow X X X X X Olive-sided Flycatcher Contopus cooperi Yellow X X X X X Ovenbird Seiurus aurocapilla Yellow X X X X X Dendroica Palm Warbler Yellow X* palmarum Vireo Philadelphia Vireo Yellow X X X philadelphicus Pine Grosbeak Pinicola enucleator Yellow X* X* Pine Siskin Carduelis pinus Yellow X X X X X Pileated Woodpecker Dryocopus pileatus Yellow X X X X Pacific-slope Flycatcher Empidonax difficilis Yellow X X X X Carpodacus Purple Finch Yellow X X X X purpureus Pheucticus Rose-breasted Grosbeak Yellow X X X X X ludovicianus Red-breasted Nuthatch Sitta canadensis Yellow X X X X X Ruby-crowned Kinglet Regulus calendula Yellow X X X X X Red Crossbill Loxia curvirostra Yellow X X* Red-eyed Vireo Vireo olivaceus Yellow X X X X X Agelaius Red-winged Blackbird Yellow X* X* phoeniceus Ruby-throated Archilochus Accident X Hummingbird colubris al Euphagus Rusty Blackbird Blue X X X X carolinus Ruffed Grouse Bonasa umbellus Yellow X X X X X Agelaius Red-winged Blackbird Yellow X X X X X phoeniceus Say's Phoebe Sayornis saya Yellow X Passerculus Savannah Sparrow Yellow X X X X X* sandwichensis Song Sparrow Melospiza melodia Yellow X X X X X* Falcipennis Spruce Grouse Yellow X* canadensis Tympanuchus Sharp-tailed Grouse Yellow X* X* phasianellus Plectrophenax Snow Bunting Yellow X* nivalis Melospiza Swamp Sparrow Yellow X X X georgiana Swainson's Thrush Catharus ustulatus Yellow X X X X X
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Study area and year English Name Scientific Name BC PRC Periphery PRC PRC TL Status 2005 2005 2006 2008 2008 Vermivora Tennessee Warbler Yellow X X X X X peregrina Myadestes Townsend's Solitaire Yellow X townsendi Dendroica Townsend's Warbler Yellow X townsendi Tachycineta Tree Swallow Yellow X X X X bicolor Varied Thrush Ixoreus naevius Yellow X X X* X* X Pooecetes Vesper Sparrow Yellow X X X X gramineus Tachycineta Violet -green Swallow Yellow X X thalassina Warbling Vireo Vireo gilvus Yellow X X X X X White-breasted Nuthatch Sitta carolinensis Yellow X X* X Zonotrichia White-crowned Sparrow Yellow X X* X leucophrys Piranga Western Tanager Yellow X X X X X ludoviciana Wilson's Warbler Wilsonia pusilla Yellow X X X X Troglodytes Winter Wren Yellow X X X X X troglodytes Zonotrichia White-throated Sparrow Yellow X X X X X albicollis White-winged Crossbill Loxia leucoptera Yellow X X X X X Contopus Western Wood-Pewee Yellow X X X sordidulus Empidonax Yellow-bellied Flycatcher Yellow X X X flaviventris Yellow-bellied Sapsucker Sphyrapicus varius Yellow X X X X X Dendroica Yellow Warbler Yellow X X X X X petechia Dendroica Yellow-rumped Warbler Yellow X X X X X coronata X’ = species detected; ‘X*’ = incidental observation only.
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Appendix 7. Butterfly taxa detected during butterfly surveys in 2005, 2006 and 2008. PRC PRC TL Scientific Name Common Name BC Status 2005 2006 2008 2008 Aglais milberti Milbert's Tortoiseshell Yellow X X Amblyscirtes vialis Roadside Skipper Yellow X X Boloria bellona Meadow Fritillary Yellow X Boloria chariclea Arctic Fritillary Yellow X Arctic Skipper, magnus Carterocephalus palaemon Yellow X X subspecies Carterocephalus palaemon Arctic Skipper, mandan Blue X X mandan subspecies Celastrina lucia Boreal Spring Azure Yellow X X X Cercyonis oetus Small Woodnymph Yellow X X X2 Cercyonis pegala nephele Common Woodnymph Blue X X X2 Charidryas palla Northern Checkerspot Yellow X X2 Clossiana bellona Meadow Fritillary Yellow X X Clossiana eunomia Bog Fritillary Yellow X X Clossiana frigga Frigga Fritillary Yellow X Clossiana grandis Grand Fritillary Yellow X X Clossiana selene Silver-bordered Fritillary Yellow X X3 X
Coenonympha tullia Common Ringlet, benjamini 2 Blue X X X X benjamini subspecies Colias christina Christina Sulphur Yellow X X X3 X Colias gigantea Giant Sulphur Yellow X X X Colias interior Pink-edged Sulphur Yellow X Colias philodice Clouded Sulphur Yellow X X X2 X Erebia epipsodea Common Alpine Yellow X X X2 X Erynnis icelus Dreamy Duskywing Yellow X X Erynnis persius Persius Duskywing Yellow X X X Euchloe ausonides Large Marble Yellow X X2 Everes amyntula Western Tailed Blue Yellow X X X2 X Glaucopsyche lygdamus Silvery Blue Yellow X1 X X2 X Hesperia assiniboia Assiniboian Skipper Red X X X2 X Hesperia manitoba Common Branded Skipper Yellow X Limenitis arthemis White Admiral Yellow X X X2 X Lycaeides idas Northern Blue Yellow X X X3 Lycaena dorcas Bog Copper Yellow X X3 X Lycaena helloides Purplish Copper Yellow X3
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PRC PRC TL Scientific Name Common Name BC Status 2005 2006 2008 2008 Lycaena hyllus Bronze Copper Blue X X3 Nymphalis antiopa Mourning Cloak Yellow X X X3 Nymphalis milberti Milbert’s Tortoiseshell Yellow X Oarisma garita Garita Skipperling Yellow X1 Oeneis alberta Alberta Arctic Red X Oeneis uhleri Uhler's Arctic Blue X X2 Papilio canadensis Canadian Tiger Swallowtail Yellow X X X2 X Baird's Swallowtail, pikei Papilio machaon pikei Blue X X X subspecies 3 Papilio rutulus Western Tiger Swallowtail Yellow X1 Papilio zelicaon Anise Swallowtail Yellow X X Phyciodes batesii Tawny Crescent Blue X X2 X Phyciodes cocyta Pearl Crescent Yellow X X X2 X Phyciodes pulchellus Field Crescent Yellow X X X3 X Pieris oleracea Mustard White Yellow X X X3 X Pieris rapae Cabbage White Yellow X X X2
Arctic Blue, lacustris 2 Plebejus glandon lacustris Blue X X subspecies Plebejus saepiolus Greenish Blue Yellow X X X2 X Polites mystic Long Dash Skipper Yellow X3 X Polites peckius Peck's Skipper Yellow X Polygonia faunus Green Comma Yellow X X Polygonia progne Grey Comma Yellow X X3 X Polygonia satyrus Satyr Anglewing Yellow X X X2 X Pontia occidentalis Western White Yellow X X2 Roddia vaualbum Compton Tortoiseshell Yellow X X3 X Satyrium liparops Striped Hairstreak Red X X Coral Hairstreak, titus Satyrium titus Red X X X subspecies Speyeria aphrodite manitoba Aphrodite Fritillary Blue X X X3 Speyeria atlantis Atlantis Fritillary Yellow X1 X X3 X
Speyeria cybele 2 Great Spangled Fritillary Red X X X X pseudocarpenteri Speyeria hesperis Northwestern Fritillary Yellow X X X2 X Speyeria mormonia Mormon Fritillary Yellow X X Thorybes pylades Northern Cloudywing Yellow X X X2 Vanessa cardui Painted Lady Yellow X
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PRC PRC TL Scientific Name Common Name BC Status 2005 2006 2008 2008 Total 41 50 46 32 1Identification not confirmed; 2found in the PRC and SCR; 3found only in the SCR.
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Appendix 8a. Rare vascular plant taxa potentially present in the study area. BC Scientific Name English Name General Habitat Justification Status Suitable habitat occurs in the Fens Acorus americanus American sweet-flag Blue project area Calcareous soils in alpine meadow- alpine, or lower elevation Known from near the project Alopecurus alpinus Red foxtail shores and rock outcrops area in cool regions Anemone Meadows and woodland, Canada anemone Blue Reported from the project area canadensis on rich soil Anemone Various, mostly shaded Known within the project area virginiana var. riverbank anemone Red sites on rich soil cylindroidea Arnica chamissonis ssp . meadow arnica Blue Wet sites in full sun Known within the project area incana Artemisia herriotii River shores and soil cut- Known within the project area (A. longifolia Herriot's mugwort Red banks misapplied) Saline clay slopes Known from within the project Atriplex nuttallii Nuttall's orache Red (badland) area Reported from the project area, Boechera lignifera Sand dunes and rock woody-branched but this species is rejected (syn. Arabis outcrops, misapplied in Blue because it does not occur north rockcress BC lignifera) of southern Idaho Boechera sickle-pod rockcress Various open sites on sparsiflora (syn. Red Known within the project area well drained soil Arabis sparsiflora) Botrychium Suitable habitat occurs in the upswept moonwort Red Various habitats ascedens project area Botrychium Suitable habitat occurs in the boreal moonwort Red Various habitats boreale project area Botrychium Various habitats, dainty moonwort Blue Known within the project area crenulatum especially in meadows Botrychium Suitable habitat occurs in the western moonwort Blue Various habitats hesperium project area Botrychium Closed-canopy conifer Suitable habitat occurs in the mountain moonwort Red montanum forest project area Botrychium two-spiked Suitable habitat occurs in the Red Tall-herb meadows paradoxum moonwort project area Botrychium Suitable habitat occurs in the stalked moonwort Red Various habitats pedunculosum project area Botrychium Seeps with thin soil in full Suitable habitat occurs in the least moonwort Blue simplex sun project area Botrychium spoon-shaped Suitable habitat occurs in the Red Various habitats spathulatum moonwort project area Calamagrostis plains reedgrass Blue Grassland Known within the project area montanensis Reported from within the project Carex bicolor two-coloured sedge Blue Various wetlands area; specimens should be re- examined to confirm Bogs, fens and muskeg Carex heleonastes Known within the project area Hudson Bay sedge Blue forest Reported from within the project swollen beaked Cold wetlands in area; specimens should be re- Carex rostrata Blue calcareous regions sedge examined to confirm
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BC Scientific Name English Name General Habitat Justification Status Carex rupestris Calcareous rock Known from near the project curly sedge Blue ssp. rupestris outcrops area pointed broom Known from near the project Carex scoparia Blue Various wetlands sedge area Carex many-headed Blue Saline wetlands Known within the project area sychnocephala sedge Reported from within the project River shores, marshes, area, but this may be accounted Carex tenera tender sedge Blue fens for by Carex sp. nov. cf. tenera Carex torreyi Torrey's sedge Blue Grassland Known within the project area Open sites in various Carex vulpinoidea Known within the project area fox sedge Blue wetlands Reported from within the project Grasslands Carex xerantica dry-land sedge Red area, but this may be in error Carex sp. nov. cf. Rare Marshes Known within the project area atherodes Carex sp. nov. cf. Marshes, swales, fens, Rare Known within the project area tenera river shores Chenopodium Suitable habitat occurs in the Hian's goosefoot Red Various dry, open sites hians project area Chrysosplenium Iowa golden- Cold sites along creeks Blue Known within the project area iowense saxifrage and in bogs Cicuta sp. nov. Rare Marsh Known within the project area European water- Beaver ponds, marshes, Cicuta virosa Blue Known within the project area hemlock river shores Cirsium Various open sites on Drummond's thistle Red Known within the project area drummondii rich soil Cystopteris sp. no common name Rare Soil cut-banks, tufa Known within the project area nov. Calcareous rock Known from near the project Draba cinerea gray-leaved draba Blue outcrops area Reported from within the project Eleocharis elliptica Calcareous fens Slender spike-rush Blue area Elymus sp. nov. no common name Rare Grassland Known within the project area Epilobium Hall's willowherb Blue Various wetlands Known within the project area halleanum Epilobium small-fruited Blue Various wetlands Known within the project area leptocarpum willowherb Epilobium Rocky Mountain Reported from within the project Red Various wetlands saximontanum willowherb area Epilobium sp. Nov. no common name Rare Marsh Known within the project area Erigeron pacalis no common name Rare Grassland Known within the project area ined. Erigeron sp. nov. no common name Rare Grassland Known within the project area (aff cespitosus) Galium northern bog Bogs, fens, muskeg Blue Known within the project area labradoricum bedstraw forest Geum triflorum var. old man's whiskers Rare Grassland Known within the project area triflorum Reported from within the project Glyceria pulchella Shallow water slender mannagrass Blue area Gymnocarpium Known from near the project Forest understory jessoense ssp. Nahanni oak fern Blue area parvulum
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BC Scientific Name English Name General Habitat Justification Status Helianthus nuttallii Previous CDC records exist for Nuttall's sunflower Red Moist soil in full sun the study area, but may be in var . nuttallii error Helictotrichon spike-oat Blue Grassland Known within the project area hookeri Juncus arcticus arctic rush Blue Lake and river shorelines Known within the project area ssp. alaskanus Open sites in wetlands Reported from within the project Juncus confusus Colorado rush Red that dry in summer area, but this is probably in error Lomatium fennel-leaved Known from within the project foeniculaceum var . Red Grassland desert-parsley area foeniculaceum Various wetlands in cold Known from near the project Luzula nivalis arctic wood-rush Blue regions area Various open or lightly Known from near the project Luzula rufescens rusty wood-rush Blue wooded habitats area Malaxis white adder's-mouth Blue Muskeg forest Known within the project area brachypoda orchid Muhlenbergia marsh muhly Blue Calcareous fens Known within the project area glomerata Mulenbergia sp. no common name Rare Marl fens Known within the project area nov. Ophioglossum northern adder's- Calcareous fens and Suitable habitat occurs in the Blue pusillum tongue meadows project area Oxytropis Gravelly or sandy river Known within the project area campestris var . Davis' locoweed Blue shores davisii Oxytropis Subalpine meadows and Reported from within the project campestris var. Jordal's locoweed Blue alpine tundra area jordallii Packera plattensis Various open or lightly Known within the project area (syn. Senecio plains butterweed Blue shaded sites on rich soil plattensis) Pedicularis small-flowered parviflora var. Blue Muskeg forest Known within the project area lousewort parviflora Penstemon gracilis slender penstemon Red Grassland Known within the project area Physaria Known from near the project Grassland slopes didymocarpa var . common twinpod Blue area didymocarpa Strongly calcareous, cold Known from near the project Pinguicula villosa hairy butterwort Blue wetlands area Piptatherum Open woods, rock Suitable habitat occurs in the Canada Ryegrass Red canadense outcrops project area Platanthera no common name Rare Muskeg forest Known within the project area aplectra ined. Polemonium northern Jacob's- Reported from near the project Blue Various open habitats boreale ladder area Polemonium Reported from near the project western Jacob's- Various open sites in occidentale ssp . Blue area; reports from within the ladder wetlands occidentale project area may be in error Previous CDC records exist for Moist grassland Polygala senega Seneca-snakeroot Red the project area Polypodium Known from near the project Siberian polypody Red Rock outcrops sibiricum area
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BC Scientific Name English Name General Habitat Justification Status Prenanthes purple rattlesnake- Known from near the project racemosa ssp. Red Grassland root area multiflora Reported from near the project Pyrola elliptica Conifer forest white wintergreen Blue area Ranunculus heart-leaved Previous CDC records exist for Red Various open sites cardiophyllus buttercup the study area Ranunculus Previous CDC records exist for Moist meadows pedatifidus ssp. birdfoot buttercup Blue the study area affinis Ranunculus Known from near the project prairie buttercup Red Various open sites rhomboideus area persistent sepal Rorippa calycina Rare River shore mudflats Known within the project area yellow-cress Rosa arkansana Grassland and dry, open Known from near the project Arkansas rose Red var. arkansana forest area Known from near the project Rumex arcticus Moist, open sites arctic dock Blue area Rumex britannica British dock Rare Marshes, fens and bogs Known within the project area Salix petiolaris meadow willow Blue Shrub thickets Known within the project area Fens, meadows and Salix serissima Known within the project area autumn willow Blue shrub thickets Sarracenia common pitcher- Known from near the project purpurea ssp. Blue Bogs and fens plant area gibbosa Schizachyrium Gravelly and sandy little bluestem Red Known within the project area scoparium ground in full sun Scolochloa rivergrass Red Marshes and shores Known within the project area festucacea Selaginella Known from within the project rock selaginella Red Rock outcrops in full sun rupestris area Various open sites in Known from near the project Senecio congestus marsh fleabane Red wetlands area Silene drummondii Drummond's Grassland and rock Reported from within the project Blue var. drummondii campion outcrops area Reported from within the project Solidago nemoralis Grassland and dry, open area; specimens should be re- field goldenrod Blue forest ssp . longipetiolata examined to confirm Soil cut-banks in cold Suitable habitat occurs within Solorina sp. nov . no common name Rare sites along rivers the project area Sphenopholis Receding shorelines and slender wedgegrass Blue Known within the project area intermedia summer-dry meadows Sphenopholis Receding shorelines and prairie wedgegrass Red Known within the project area obtusata summer-dry meadows sheathing Submerged in sloughs, Known from near the project Stuckenia vaginata Blue pondweed ponds and lakes area Symphyotrichum purple-stemmed Various wetland in full puniceum var. Blue Known within the project area aster sun or light shade puniceum Townsendia Hooker's Known from near the project Red Dry grasslands hookeri townsendia area Trichophorum Strongly calcareous dwarf clubrush Blue Known within the project area pumilum wetlands Utricularia ochroleucous Submerged aquatic in Suitable habitat occurs within Blue ochroleuca bladderwort fens the project area
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BC Scientific Name English Name General Habitat Justification Status Viola renifolia var. Forest understory on rich kidney-leaved violet Rare Known within the project area nov. soil and tufa
Appendix 8b. Complete list of vascular plant species detected during rare plant surveys in 2008. BC BCCF English Name Scientific Name Status priority Comment PRC TL subalpine fir Abies lasiocarpa Yellow X Achillea millefolium yarrow var . lanulosa Yellow 6 X X Achillea millefolium yarrow x sibirica Yellow X X Siberian yarrow Achillea sibirica Yellow 4 X X Achnatherum nelsonii ssp needlegrass richardsonii Yellow X Achnatherum stiff needlegrass occidentale Yellow X Achnatherum spreading needlegrass richardsonii Yellow 4 X Aconitum mountain monkshood delphiniifolium Yellow 4 X baneberry Actaea rubra Yellow 4 X X spike bentgrass Agrostis exarata Yellow 6 X redtop Agrostis gigantea exotic Non-native X X hair bentgrass Agrostis scabra Yellow 6 X X creeping bentgrass Agrostis stolonifera exotic Non-native X X American water- plantain Alisma triviale Yellow 6 X nodding onion Allium cernuum Yellow X Allium wild chives schoenoprasum Yellow X Alnus incana ssp mountain alder tenuifolia Yellow X X Alnus viridis ssp green alder crispa Yellow X X Alopecurus little meadow-foxtail aequalis Yellow 6 X X Amelanchier saskatoon alnifolia Yellow X X Amerorchis round-leaved orchis rotundifolia Yellow 4 X X
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BC BCCF English Name Scientific Name Status priority Comment PRC TL Anaphalis pearly everlasting margaritacea Yellow 6 X Andromeda bog-rosemary polifolia Yellow 4 X X northern fairy- Androsace candelabra septentrionalis Yellow 4 X long-headed anemone Anemone cylindrica Yellow X Anemone multifida cut-leaved anemone var multifida Yellow X X Anemone patens prairie crocus ssp multifida Yellow X Anemone virginiana var. riverbank anemone cylindroidea Red X kneeling angelica Angelica genuflexa Yellow 6 X X silverweed Anserina argentea Yellow X Antennaria howellii Howell's pussytoes ssp canadensis Yellow X Antennaria field pussytoes neglecta Yellow 4 X Antennaria Nuttall's pussytoes parvifolia Yellow 4 X Antennaria pussytoes parvifolia x howellii Yellow X Antennaria showy pussytoes pulcherrima Yellow X rosy pussytoes Antennaria rosea Yellow 6 X X Apocynum androsaemifolium ssp spreading dogbane androsaemifolium Yellow X Apocynum hemp cannabinum Yellow 4 X Apocynum no prairie Indian-hemp sibiricum status X blue columbine Aquilegia brevistyla Yellow 4 X X Arabis hirsuta var hairy rockcress pycnocarpa Yellow X wild sarsaparilla Aralia nudicaulis Yellow 4 X X burdock Arctium sp. exotic Non-native X Arctostaphylos uva- kinnikinnick ursi Yellow 6 X X Arnica chamissonis meadow arnica ssp foliosa Yellow X
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BC BCCF English Name Scientific Name Status priority Comment PRC TL Arnica chamissonis meadow arnica ssp incana Blue X heart-leaved arnica Arnica cordifolia Yellow 6 X X biennial wormwood Artemisia biennis Yellow 4 X Artemisia northern wormwood campestris Yellow X Artemisia tarragon dracunculus Yellow 6 X prairie sagewort Artemisia frigida Yellow 6 X Herriot's mugwort Artemisia herriotii Red X Asparagus garden asparagus officinalis exotic Non-native X field milk-vetch Astragalus agrestis Yellow 6 X alpine milk-vetch Astragalus alpinus Yellow X Astragalus American milk-vetch americanus Yellow 4 X southern milk-vetch Astragalus australis Yellow 4 X Astragalus Canadian milk-vetch canadensis Yellow X chick-pea milk-vetch Astragalus cicer exotic Non-native X Astragalus elegant milk-vetch eucosmus Yellow 4 X Astragalus laxmannii var standing milk-vetch robustior Yellow X Astragalus no loose-flower milk-vetch multiflorus status X Athyrium filix- lady fern femina Yellow X X wild oat Avena fatua exotic Non-native X Beckmannia American sloughgrass syziygachne Yellow X X Betula glandulosa dwarf birch (syn. Betula nana) Yellow X Alaska paper birch Betula neoalaskana Yellow 4 X X water birch Betula occidentalis Yellow 4 X X paper birch Betula papyrifera Yellow X X low birch Betula pumila Yellow X X nodding beggarticks Bidens cernua Yellow 5 X X Boechera no reflexed rock-cress retrofracta status X Boechera sickle-pod rock-cress sparsiflora Red X July 2009 -281-
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BC BCCF English Name Scientific Name Status priority Comment PRC TL Botrychium rattlesnake fern virginianum Yellow 4 X X fringed brome Bromus ciliatus Yellow 4 X X smooth brome Bromus inermis exotic Non-native X X no mountain brome Bromus marginatus status X Porter's brome Bromus porteri Yellow 4 X Bromus Pumpelly brome pumpellianus Yellow 4 X X no Previously brome Bromus sp nov status undescibed? X Calamagrostis canadensis ssp bluejoint reedgrass canadensis Yellow X X Calamagrostis canadensis ssp bluejoint reedgrass langsdorfii Yellow X X Calamagrostis Lapland reedgrass lapponica Yellow 4 X Calamagrostis plains reedgrass montanensis Blue 4 X Calamagrostis pinegrass rubescens Yellow 6 X Calamagrostis stricta ssp slimstem reedgrass inexpansa Yellow X X Calamagrostis slimstem reedgrass stricta ssp stricta Yellow X X wild calla Calla palustris Yellow 4 X X spring water-starwort Callitriche palustris Yellow 4 X Campanula common harebell rotundifolia Yellow 6 X Canadanthus great northern aster modestus Yellow X X Capsella bursa- shepherd's purse pastoris exotic Non-native X Cardamine little western bitter- oligosperma var cress oligosperma Yellow X X Pennsylvanian bitter- Cardamine cress pensylvanica Yellow 4 X Carex aquatilis var water sedge aquatilis Yellow X Carex aquatilis var no water sedge substricta status X X
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BC BCCF English Name Scientific Name Status priority Comment PRC TL awned sedge Carex atherodes Yellow 4 X X black sedge Carex atratiformis Yellow 4 X golden sedge Carex aurea Yellow 4 X X hairlike sedge Carex capillaris Yellow 4 X X Carex so nov cf no Previously sedge atherodes status undescribed? X X Carex sp nov cf no Previously sedge ovalis status undescribed? X X Carex sp nov cf no Previously sedge tenera status undescribed? X low northern sedge Carex concinna Yellow 6 X X Crawford's sedge Carex crawfordii Yellow 6 X X bent sedge Carex deflexa Yellow 4 X Dewey's sedge Carex deweyana Yellow X lesser-panicled sedge Carex diandra Yellow 6 X X soft-leaved sedge Carex disperma Yellow 6 X X Douglas' sedge Carex douglasii Yellow 4 X narrow-leaved sedge Carex duriuscula Yellow 4 X thread-leaved sedge Carex filifolia Yellow 4 X no dryspike sedge Carex foenea status X Garber's sedge Carex garberi Yellow X yellow bog sedge Carex gynocrates Yellow 6 X X Hudson Bay sedge Carex heleonastes Blue 3 X Hood's sedge Carex hoodii Yellow 6 X sheep sedge Carex illota Yellow 4 X Carex inops ssp long-stoloned sedge heliophila Yellow X slender sedge Carex lasiocarpa Yellow X Carex lenticularis Kellogg's sedge var lipocarpa Yellow X bristle-stalked sedge Carex leptalea Yellow X X shore sedge Carex limosa Yellow 4 X ryegrass sedge Carex loliacea Yellow 4 X
Falkland Island sedge Carex macloviana Yellow 4 X Carex magellanica poor sedge ssp irrigua Yellow X X
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BC BCCF English Name Scientific Name Status priority Comment PRC TL few-seeded fen sedge Carex microglochin Yellow 4 X blunt sedge Carex obtusata Yellow 6 X no wooly sedge Carex pellita status X long-bracted sedge Carex retrorsa Yellow 4 X Ross' sedge Carex rossii Yellow 6 X Sartwell's sedge Carex sartwellii Yellow X X hay sedge Carex siccata Yellow 4 X awl-fruited sedge Carex stipata Yellow X Carex many-headed sedge sychnocephala Blue 4 X beaked sedge Carex utriculata Yellow 6 X X sheathed sedge Carex vaginata Yellow 4 X X green sedge Carex viridula Yellow X fox sedge Carex vulpinoidea Blue 3 X scarlet paintbrush Castilleja miniata Yellow 6 X X alpine paintbrush Castilleja rhexifolia Yellow X X sulphur paintbrush Castilleja sulphurea Yellow X X field chickweed Cerastium arvense Yellow 4 X nodding chickweed Cerastium nutans Yellow 4 X X Ceratophyllum common hornwort demersum Yellow 6 X X Chamaenerion fireweed angustifolium Yellow X X Chenopodium lamb's-quarters album exotic Non-native X Chenopodium strawberry-blite capitatum Yellow 6 X Chenopodium desert goosefoot pratericola Yellow 4 X Chenopodium red goosefoot rubrum var humile Yellow X Chenopodium red goosefoot rubrum var rubrum Yellow X Chenopodium maple-leaved goosefoot simplex Yellow 4 X Chrysosplenium Iowa golden-saxifrage iowense Blue 3 Blue listed X northern golden- Chrysosplenium saxifrage tetrandrum Yellow 6 X X
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BC BCCF English Name Scientific Name Status priority Comment PRC TL bulbous water-hemlock Cicuta bulbifera Yellow 4 X X
Douglas' water-hemlock Cicuta douglasii Yellow 6 X no Previously water-hemlock Cicuta sp nov status undescribed? X European water- hemlock Cicuta virosa Blue 3 X nodding wood-reed Cinna latifolia Yellow 6 X X enchanter's-nightshade Circaea alpina Yellow X Canada thistle Cirsium arvense exotic Non-native X X Cirsium Drummond's thistle drummondii Red 2 X X bull thistle Cirsium vulgare exotic Non-native X X Clematis occidentalis var . Columbia bower grosseserrata Yellow X Coeloglossum long-bracted frog orchid viride Yellow X X narrow-leaved collomia Collomia linearis Yellow 6 X Comandra umbellata ssp bastard toad-flax umbellata Yellow X marsh cinquefoil Comarum palustre Yellow 6 X X Canadian horseweed Conyza canadensis exotic X Corallorhiza maculata sensu spotted coralroot lato Yellow X X yellow coralroot Corallorhiza trifida Yellow 6 X bunchberry Cornus canadensis Yellow 6 X X red-osier dogwood Cornus stolonifera Yellow 6 X X golden corydalis Corydalis aurea Yellow 4 X annual hawksbeard Crepis tectorum exotic Non-native X X sparrow's-egg lady's- Cypripedium slipper passerinum Yellow 4 X X no Previously no common name Cystopteris sp nov status undescribed? X Danthonia timber oatgrass intermedia Yellow 6 X
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BC BCCF English Name Scientific Name Status priority Comment PRC TL Delphinium tall larkspur glaucum Yellow 6 X X Deschampsia cespitosa var tufted hairgrass cespitosa Yellow X Richardson's tansy Descurainea mustard incana Yellow X Descurainia northern tansy mustard sophioides exotic Non-native X Dracocephalum American dragonhead parviflorum Yellow 4 X round-leaved sundew Drosera rotundifolia Yellow X X Dryas drummondii yellow mountain-avens var tomentosa Yellow X Drymocallis arguta no cream cinquefoil ssp convallaria status X Dryopteris toothed wood fern carthusiana Yellow 4 X X spiny wood fern Dryopteris expansa Yellow 6 X X Elaeagnus silverberry commutata Yellow 4 X X Eleocharis needle spike-rush acicularis Yellow 4 X Eleocharis no redstem spikerush erythropoda status X Eleocharis creeping spike-rush macrostachya Yellow 4 X Eleocharis nipple spike-rush mamillata Yellow X X common spike-rush Eleocharis palustris Yellow 6 X X Eleocharis few-flowered spike-rush quinqueflora Yellow 4 X Elymus alaskanus Alaska wildrye ssp latiglumis Yellow X Canada wildrye Elymus canadensis Yellow 4 X no wildrye Elymus cf scribneri status X Elymus glaucus blue wildrye ssp glaucus Yellow X X Elymus glaucus blue wildrye ssp virescens Yellow X X hairy wildrye Elymus hirsutus Yellow 4 X
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BC BCCF English Name Scientific Name Status priority Comment PRC TL Unable to Determin thickspike wildrye Elymus lanceolatus Yellow e X quackgrass Elymus repens exotic Non-native X X no Previously wheatgrass Elymus sp nov status undescribed? X Elymus trachycaulis ssp slender wheatgrass subsecundus Yellow X Elymus trachycaulis ssp slender wheatgrass trachycaulis Yellow X X no Montana wildrye Elymus x albicans status X purple-leaved Epilobium ciliatum willowherb ssp ciliatum Yellow X X purple-leaved Epilobium ciliatum willowherb ssp . glandulosum Yellow X X club-fruited willowherb Epilobium clavatum Yellow 6 X Epilobium Hall's willowherb halleanum Blue 3 X Epilobium small-fruited willowherb leptocarpum Blue 3 X narrow-leaved Epilobium willowherb leptophyllum Yellow 4 Possibly rare X X swamp willowherb Epilobium palustre Yellow 4 X X no Previously No common name Epilobium sp nov status undescribed? X common horsetail Equisetum arvense Yellow 6 X X swamp horsetail Equisetum fluviatile Yellow 4 X X scouring-rush Equisetum hyemale Yellow X X Equisetum smooth scouring-rush laevigatum Yellow 4 X marsh horsetail Equisetum palustre Yellow 4 X X Equisetum meadow horsetail pratense Yellow 4 X X Equisetum dwarf scouring-rush scirpoides Yellow 4 X X Equisetum wood horsetail sylvaticum Yellow 4 X X
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BC BCCF English Name Scientific Name Status priority Comment PRC TL Equisetum variegatum ssp . northern scouring-rush variegatum Yellow X Erigeron acris var no bitter fleabane asteroides status X Erigeron tufted fleabane caespitosus Yellow X Erigeron glabellus no smooth daisy ssp pubescens status X X Erigeron spear-leaved fleabane lonchophyllus Yellow 6 X Erigeron Philadelphia fleabane philadelphicus Yellow 4 X Erigeron sp nov (aff no Previously No common name cespitosus) status undescribed? X Erigeron pacalis no Previously No common name ined. status undescribed? X rough-stemmed fleabane Erigeron strigosus Yellow X narrow-leaved cotton- Eriophorum grass angustifolium Yellow 6 X Chamisso's cotton- Eriophorum grass chamissonis Yellow X slender cotton-grass Eriophorum gracile Yellow 4 X Eriophorum sheathed cotton-grass vaginatum Yellow X Erysimum wormseed mustard cheiranthoides Yellow 4 X Erysimum small wallflower inconspicuum Yellow 4 X Euphrasia eastern eyebright nemorosa exotic Non-native X showy aster Eurybia conspicua Yellow X X subalpine aster Eurybia merita Yellow X X Fallopia wild buckwheat convolvulus exotic Non-native X Festuca cf Idaho fescue idahoensis Yellow X sheep fescue Festuca ovina exotic Non-native X meadow fescue Festuca pratensis exotic Non-native X red fescue Festuca rubra Yellow X
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BC BCCF English Name Scientific Name Status priority Comment PRC TL Festuca rubra (small flowered red fescue non-glaucous) exotic Non-native X X Festuca Rocky Mountain fescue saximontana Yellow 6 X bearded fescue Festuca subulata Yellow 4 X wood strawberry Fragaria vesca Yellow X X Fragaria virginiana wild strawberry var . glauca Yellow X X Fragaria virginiana wild strawberry ssp virginiana Yellow X X small hemp-nettle Galeopsis bifida exotic Non-native X X northern bedstraw Galium boreale Yellow 6 X X Galium northern bog bedstraw labradoricum Blue 2 X Galium trifidum ssp small bedstraw subbiflorum Yellow X X Galium trifidum ssp small bedstraw trifidum Yellow X X sweet-scented bedstraw Galium triflorum Yellow 6 X X Gaultheria creeping-snowberry hispidula Yellow 4 X Gentianella northern gentian amarella Yellow X X false toad-flax Geocaulon lividum Yellow 6 X X Bicknell's geranium Geranium bicknellii Yellow 6 X X yellow avens Geum aleppicum Yellow 4 X X Geum aleppicum x no avens macrophyllum status X X Geum large-leaved avens macrophyllum Yellow X X water avens Geum rivale Yellow 4 X Geum triflorum var . no old man's whiskers triflorum status Rare in BC? X northern mannagrass Glyceria borealis Yellow 4 X X tall mannagrass Glyceria elata Yellow 6 X reed mannagrass Glyceria grandis Yellow 6 X X fowl mannagrass Glyceria striata Yellow 6 X X Gnaphalium marsh cudweed uliginosum exotic Non-native X
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BC BCCF English Name Scientific Name Status priority Comment PRC TL Goodyera rattlesnake-plantain oblongifolia Yellow 6 X dwarf rattlesnake orchid Goodyera repens Yellow 4 X Grindelia squarrosa curly-cup gumweed ssp quasiperennis Yellow X Gymnocarpium oak fern dryopteris Yellow 4 X X nodding stickseed Hackelia deflexa Yellow X many-flowered stickseed Hackelia floribunda Yellow 4 X spurred gentian Halenia deflexa Yellow X Hedysarum alpine hedysarum alpinum Yellow 6 X X Hedysarum boreale northern hedysarum ssp . mackenzii Yellow X Helictotrichon spike-oat hookeri Blue 3 X Heracleum cow-parsnip maximum Yellow X X short-awned Hesperostipa porcupinegrass curtiseta Yellow 4 X Heuchera Richardson's alumroot richardsonii Yellow 6 X narrow-leaved Hieracium hawkweed umbellatum Yellow X X Hierochloe hirta common sweetgrass ssp . arctica Yellow X common mare's-tail Hippuris vulgaris Yellow 6 X X Hordeum jubatum foxtail barley ssp intermedium Yellow X Hordeum jubatum foxtail barley ssp jubatum Yellow X X Impatiens noli- common touch-me-not tangere Yellow 4 X X tapered rush Juncus acuminatus Yellow 4 X Juncus alpine rush alpinoarticulatus Yellow 4 X Juncus arcticus arctic rush ssp . alaskanus Blue X Juncus arcticus ssp no arctic rush sitchensis status X Baltic rush Juncus balticus Yellow 4 X X
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BC BCCF English Name Scientific Name Status priority Comment PRC TL toad rush Juncus bufonius Yellow 6 X X Dudley's rush Juncus dudleyi Yellow 4 X X tuberous rush Juncus nodosus Yellow 4 X Juniperus communis var common juniper depressus Yellow X Juniperus communis var common juniper montana Yellow X Juniperus creeping juniper horizontalis Yellow 6 X junegrass Koeleria macrantha Yellow 6 X tall blue lettuce Lactuca biennis Yellow 4 X prickly lettuce Lactuca serriola exotic Non-native X Lappula occidentalis var . western stickseed occidentalis Yellow X bristly stickseed Lappula squarrosa exotic Non-native X tamarack Larix laricina Yellow 4 X X Lathyrus creamy peavine ochroleucus Yellow 6 X X Ledum Labrador tea groenlandicum Yellow 6 X X common duckweed Lemna minor Yellow 6 X X ivy-leaved duckweed Lemna trisulca Yellow 4 X Lepidium densiflorum var . prairie pepper-grass densiflorum Yellow X Lepidium densiflorum var . prairie pepper-grass macrocarpum Yellow X fuzzy-spiked wildrye Leymus innovatus Yellow 4 X X water mudwort Limosella aquatica Yellow 4 X Dalmatian toad-flax Linaria dalmatica exotic Non-native X twinflower Linnaea borealis Yellow X X Linum lewisii ssp . western blue flax lewisii Yellow X Lithospermum yellow gromwell incisum Yellow 4 X Kalm's lobelia Lobelia kalmii Yellow 4 X glaucous-leaved Lonicera dioica var . honeysuckle glaucescens Yellow X X
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BC BCCF English Name Scientific Name Status priority Comment PRC TL Lonicera black twinberry involucrata Yellow 6 X X birds-foot trefoil Lotus corniculatus exotic Non-native X X Lycopodium stiff club-moss annotinum Yellow 6 X northern water horehound Lycopus uniflorus Yellow 4 X Lysimachia tufted loosestrife thyrsiflora Yellow 4 X X Maianthemum wild lily-of-the-valley canadense Yellow 4 X X Maianthemum false Solomon's-seal racemosum Yellow X X star-flowered false Maianthemum Solomon's-seal stellatum Yellow 6 X X three-leaved false Maianthemum Solomon's-seal trifolium Yellow 4 X X white adder's-mouth Malaxis orchid brachypoda Blue 3 X Not Matricaria No Assesse pineapple weed discoidea status d X X scentless mayweed Matricaria perforata exotic Non-native X Matteuccia ostrich fern struthiopteris Yellow X black medic Medicago lupulina exotic Non-native X Medicago sativa alfalfa var falcata exotic Non-native X Medicago sativa alfalfa var sativa exotic Non-native X X Melampyrum cow-wheat lineare Yellow X white sweet-clover Melilotus alba exotic Non-native X X yellow sweet-clover Melilotus officinalis exotic Non-native X X field mint Mentha arvensis Yellow 6 X X Menyanthes buckbean trifoliata Yellow 6 X X Mertensia paniculata var. tall bluebells paniculata Yellow X X yellow monkey-flower Mimulus guttatus Yellow 6 X common mitrewort Mitella nuda Yellow 6 X X
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BC BCCF English Name Scientific Name Status priority Comment PRC TL Moehringia blunt-leaved sandwort lateriflora Yellow 4 X X Monarda fistulosa wild bergamot var . menthaefolia Yellow X single delight Moneses uniflora Yellow 4 X Muhlenbergia marsh muhly glomerata Blue 4 X Muhlenbergia sp no Previously muhly nov status undescribed? X Myosoton water chickweed aquaticum exotic Non-native X Myriophyllum Siberian water-milfoil sibiricum Yellow 4 X Myriophyllum verticillate water-milfoil verticillatum Yellow 4 X green needlegrass Nassella viridula Yellow 4 X Unable to Determin devil's club Oplopanax horridus Yellow e X brittle prickly-pear cactus Opuntia fragilis Yellow 6 X Orobanche clustered broomrape fasciculata Yellow 4 X one-sided wintergreen Orthilia secunda Yellow X X yellow owl-clover Orthocarpus luteus Yellow 4 X Oryzopsis rough-leaved ricegrass asperifolia Yellow 4 X mountain sweet-cicely Osmorhiza berteroi Yellow 6 X X blunt-fruited sweet- Osmorhiza cicely depauperata Yellow 4 X Oxytropis campestris var . Davis' locoweed davisii Blue X Oxytropis campestris var . field locoweed cusickii Yellow X no pendant-pod locoweed Oxytropis deflexa status X X Oxytropis sericea Nelson's oxytrope var spicata Yellow X
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BC BCCF English Name Scientific Name Status priority Comment PRC TL Oxytropis showy locoweed splendens Yellow 4 X no elegant groundsel Packera indecora status X Packera no balsam groundsel paupercula status X X prairie groundsel Packera plattensis Blue X X northern grass-of- Parnassus Parnassia palustris Yellow 6 X X western bluegrass Pascopyrum smithii Yellow 6 X Pedicularis small-flowered parviflora ssp lousewort parviflora Blue X slender penstemon Penstemon gracilis Red 3 X Penstemon small-flowered procerus var . penstemon procerus Yellow X water smartweed Persicaria amphibia Yellow X X Persicaria no pale smartweed lapathifolia status X Petasites frigidus sweet coltsfoot var . palmatus Yellow X X Petasites frigidus x sweet coltsfoot sagittatus Yellow X X arrow-leaved coltsfoot Petasites sagittatus Yellow 6 X X Phalaris reed canarygrass arundinacea Yellow 6 Non-native X X common timothy Phleum pratense exotic Non-native X X white spruce Picea glauca Yellow 5 X X black spruce Picea mariana Yellow 6 X X Pinus contorta ssp lodgepole pine latifolia Yellow X X Piperia Alaska rein orchid unalascensis Yellow 6 X Piptatherum short-awned ricegrass pungens Yellow 4 X common plantain Plantago major exotic Non-native X X northern green rein Platanthera orchid aquilonis Yellow 6 X Platanthera no Previously No common name aplectra ined. status undescribed? X fragrant white rein orchid Platanthera dilatata Yellow X July 2009 -294-
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BC BCCF English Name Scientific Name Status priority Comment PRC TL Platanthera Great Lakes rein orchid huronensis Yellow 4 X X Platanthera one-leaved rein orchid obtusata Yellow X X large round-leaved rein Platanthera orchid orbiculata Yellow 4 X alpine bluegrass Poa alpina Yellow X annual bluegrass Poa annua exotic Non-native X X Poa sp nov cf no Previously No common name leptocoma status undescribed? X Canada bluegrass Poa compressa exotic Non-native X Poa cusickii ssp . Cusick's bluegrass pallida Yellow X X wood bluegrass Poa nemoralis Yellow X Poa palustris native fowl bluegrass form Yellow X X Poa palustris fowl bluegrass nonnative forms exotic Non-native X X Poa pratensis Kentucky bluegrass native forms Yellow X X Poa pratensis Kentucky bluegrass nonnative forms exotic Non-native X X rough bluegrass Poa trivialis exotic Non-native X Polygonum Blake's knotweed achoreum Yellow 4 X X Polygonum common knotweed aviculare exotic Non-native X X Polygonum cf knotweed buxiforme exotic Non-native X X Populus balsam poplar balsamifera Yellow X X Populus trembling aspen tremuloides Yellow 6 X X Potamogeton ribbon-leaf pondweed epihydrus Yellow 6 X closed-leaved Potamogeton pondweed foliosus Yellow 4 X Potamogeton grass-leaved pondweed gramineus Yellow 4 X floating-leaved Potamogeton pondweed natans Yellow 6 X Potamogeton pusillus ssp . small pondweed tenuissimus Yellow X X
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BC BCCF English Name Scientific Name Status priority Comment PRC TL Potamogeton Richardson's pondweed richardsonii Yellow 6 X biennial cinquefoil Potentilla biennis Yellow 4 X Potentilla cf no Previously No common name pensylvanica status undescribed? X woolly cinquefoil Potentilla hippiana Yellow X Norwegian cinquefoil Potentilla norvegica Yellow 6 X X Pennsylvanian Potentilla cinquefoil pensylvanica Yellow X Potentilla pretty cinquefoil pulcherrima Yellow 4 X mealy primrose Primula incana Yellow 4 X Primula nutans ? no apparently Siberian primrose (past flower) status rare in BC X Prosartes rough-fruited fairybells trachycarpa Yellow 6 X X self-heal Prunella vulgaris Yellow X X Prunus pin cherry pennsylvanica Yellow 4 X choke cherry Prunus virginiana Yellow X weeping alkaligrass Puccinellia distans exotic Non-native X Puccinellia Nuttall's alkaligrass nuttalliana Yellow 4 X pink wintergreen Pyrola asarifolia Yellow 6 X X green wintergreen Pyrola chlorantha Yellow 6 X X lesser wintergreen Pyrola minor Yellow 4 X Ranunculus white water-buttercup aquatilis Yellow X Ranunculus shore buttercup cymbalaria Yellow 6 X Ranunculus lesser spearwort flammula Yellow 6 X small yellow water- Ranunculus buttercup gmelinii Yellow 6 X X Ranunculus Lapland buttercup lapponicus Yellow X Ranunculus Macoun's buttercup macounii Yellow 6 X X Ranunculus Pennsylvania buttercup pensylvanicus Yellow 4 X Ranunculus celery-leaved buttercup scleratus Yellow X X
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BC BCCF English Name Scientific Name Status priority Comment PRC TL yellow rattle Rhinanthus minor Yellow 4 X X skunk currant Ribes glandulosum Yellow 4 X Ribes hudsonianum var . northern blackcurrant hudsonianum Yellow X X Ribes hudsonianum var . northern blackcurrant petiolare Yellow X X black gooseberry Ribes lacustre Yellow 6 X X trailing black currant Ribes laxiflorum Yellow 6 X X Ribes oxyacanthoides ssp . northern gooseberry oxyacanthoides Yellow X X red swamp currant Ribes triste Yellow 4 X X Newly found for BC, persistent sepal no globally rare yellowcress Rorippa calycina status species X blunt-leaved yellowcress Rorippa curvipes Yellow X western yellow cress Rorippa curvisiliqua Yellow 6 X Rorippa palustris marsh yellow cress ssp hispida Yellow X Rorippa palustris marsh yellow cress ssp palustris Yellow X X prickly rose Rosa acicularis Yellow X X Nootka rose Rosa nutkana Yellow X Rosa woodsii ssp prairie rose ultramontana Yellow X Rubus arcticus ssp . nagoonberry acaulis Yellow X X Rubus cloudberry chamaemorus Yellow 4 X red raspberry Rubus idaeus yellow X X thimbleberry Rubus parviflorus Yellow X dwarf red raspberry Rubus pubescens Yellow X X
Possibly rare, not previously no known from British dock Rumex brittanica status BC X
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BC BCCF English Name Scientific Name Status priority Comment PRC TL Rumex sp nov cf no Previously dock mexicanus status undescribed? X curled dock Rumex crispus exotic Non-native X X no American golden dock Rumex fueginus status X no western dock Rumex occidentalis status X arum-leaved arrowhead Sagittaria cuneata Yellow 6 X Salix alaxensis var Alaska willow alaxensis Yellow X X Salix alaxensis var Alaska willow longistylis Yellow X northern bush willow Salix arbusculoides Yellow 6 X X Salix Athabasca willow athabascensis Yellow 4 X X Bebb's willow Salix bebbiana Yellow 6 X X sage willow Salix candida Yellow 6 X under-green willow Salix commutata Yellow 4 X X pussy willow Salix discolor Yellow 6 X X Salix Drummond's willow drummondiana Yellow 6 X X narrow-leaf willow Salix exigua Yellow X grey-leaved willow Salix glauca Yellow X Salix lucida ssp . whiplash willow caudata Yellow X X Salix lucida ssp . Pacific willow lasiandra Yellow X X no yellow willow Salix lutea status X MacCalla's willow Salix maccalliana Yellow 6 X X Salix no Mackenzie's willow mackenzieana status X X dusky willow Salix melanopsis? Yellow X bilberry willow Salix myrtillifolia Yellow 6 X X bog willow Salix pedicellaris Yellow 4 X X meadow willow Salix petiolaris Blue 3 X plane-leaved willow Salix planifolia Yellow 6 X X Salix serviceberry willow pseudomonticola Yellow 4 X X Salix tall blueberry willow pseudomyrsinites Yellow 4 X X Scouler's willow Salix scouleriana Yellow 6 X July 2009 -298-
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BC BCCF English Name Scientific Name Status priority Comment PRC TL autumn willow Salix serissima Blue 3 X rock willow Salix vestita Yellow 6 X Sambucus elderberry racemosa Yellow X Sanicula black sanicle marilandica Yellow 4 X X Schizachne false melic purpurascens Yellow 4 X X Schoenoplectus hard-stemmed bulrush acutus ssp acutus Yellow X Schoenoplectus soft-stemmed bulrush tabernaemontani Yellow 6 X Scirpus small-flowered bulrush microcarpus Yellow 6 X X Scolochloa rivergrass festucacea Red 3 X Scutellaria marsh skullcap galericulata Yellow 4 X X Scutellaria blue skullcap lateriflora Yellow 4 X Senecio dryland ragwort eremophilus Yellow X X common groundsel Senecio vulgaris exotic Non-native X Shepherdia soopolallie canadensis Yellow 6 X X Sisymbrium tall tumble-mustard altissimum exotic Non-native X Loesel's tumble- mustard Sisymbrium loeselii exotic Non-native X mountain blue-eyed- Sisyrinchium grass montanum Yellow 4 X hemlock water-parsnip Sium suave Yellow 6 X X Solidago lepida var Canada goldenrod lepida Yellow X X Solidago lepida var Canada goldenrod salebrosa Yellow X X Solidago missouriensis var . Missouri goldenrod missouriensis Yellow X Solidago simplex mountain goldenrod var simplex Yellow X perennial sow-thistle Sonchus arvensis exotic Non-native X X prickly sow-thistle Sonchus asper exotic Non-native X
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BC BCCF English Name Scientific Name Status priority Comment PRC TL common sow-thistle Sonchus oleraceus exotic Non-native X Sorbus sp nov cf no showy mountain-ash decora status X X western mountain-ash Sorbus scopulina Yellow X Sparganium narrow-leaved bur-reed angustifolium Yellow 6 X Sparganium emersed bur-reed emersum Yellow 6 X X Sparganium northern bur-reed hyperboreum Yellow 4 X X small bur-reed Sparganium natans Yellow 6 X X Sphenopholis slender wedgegrass intermedia Blue X birch-leaved spirea Spiraea betulifolia Yellow X X Spiranthes hooded ladies' tresses romanzoffiana Yellow 4 X X great duckweed Spirodela polyrhiza Yellow X swamp hedge-nettle Stachys palustris Yellow X boreal starwort Stellaria borealis Yellow X X northern starwort Stellaria calycantha Yellow 4 X long-leaved starwort Stellaria longifolia Yellow 4 X Stellaria longipes long-stalked starwort var . longipes Yellow X common chickweed Stellaria media exotic Non-native X Streptopus amplexifolius var . clasping twistedstalk amplexifolius Yellow X Streptopus amplexifolius var . clasping twistedstalk chalazatus Yellow X slender-leaved Stuckenia filiformis pondweed ssp . alpina Yellow X slender-leaved Stuckenia filiformis pondweed ssp . occidentalis Yellow X fennel-leaved pondweed Stuckenia pectinata Yellow 4 X Symphoricarpos common snowberry albus Yellow X X Symphoricarpos western snowberry occidentalis Yellow 4 X X Symphyotrichum northern bog aster boreale Yellow X X
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BC BCCF English Name Scientific Name Status priority Comment PRC TL Symphyotrichum rayless alkali aster ciliatum Yellow X X Symphyotrichum Lindley's aster ciliolatum Yellow X X Symphyotrichum Eaton's aster eatonii Yellow X Symphyotrichum ericoides ssp tufted white prairie aster pansus Yellow X Symphyotrichum lanceolatum var no New to BC, white panicle aster lanceolatum status rare X Symphyotrichum no purplestem aster puniceum status X X Symphyotrichum spathulatum ssp no western mountain aster spathulatum status X Taraxacum common dandelion officinale exotic Non-native X X Thalictrum western meadowrue occidentale Yellow 6 X X few-flowered Thalictrum meadowrue sparsiflorum Yellow 4 X X Thalictrum veiny meadowrue venulosum Yellow 4 X Thinopyrum tall wheatgrass ponticum exotic Non-native X field pennycress Thlaspi arvense exotic Non-native X X Torreyochloa weak false-manna pauciflora Yellow X X yellow salsify Tragopogon dubius exotic Non-native X X Trichophorum dwarf clubrush pumilum Blue 3 X alsike clover Trifolium hybridum exotic Non-native X X red clover Trifolium pratense exotic Non-native X X white clover Trifolium repens exotic Non-native X X seaside arrow-grass Triglochin maritima Yellow X no marsh arrow-grass Triglochin palustris status X spike trisetum Trisetum spicatum Yellow 6 X no tower rockcress Turritis glabra status X common cattail Typha latifolia Yellow 6 X X stinging nettle Urtica dioica Yellow X X
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BC BCCF English Name Scientific Name Status priority Comment PRC TL Utricularia greater bladderwort macrorhiza Yellow X lesser bladderwort Utricularia minor Yellow 6 X X Vaccinium dwarf blueberry caespitosum Yellow X X Vaccinium velvet-leaved blueberry myrtilloides Yellow 4 X Vaccinium small cranberry oxycoccos Yellow X X Vaccinium vitis- lingonberry idaea Yellow X X Veronica no American brooklime americana status X X Veronica anagallis- blue water speedwell aquatica exotic X long-leaf speedwell Veronica longifolia exotic Non-native X purslane speedwell Veronica peregrina exotic X highbush-cranberry Viburnum edule Yellow 4 X X American vetch Vicia americana Yellow 6 X X early blue violet Viola adunca Yellow X Canada violet Viola canadensis Yellow X X Viola renifolia var no Previously No common name nov status undescribed? X small white violet Viola macloskeyi Yellow 4 X northern bog violet Viola nephrophylla Yellow X marsh violet Viola palustris Yellow X X kidney-leaved violet Viola renifolia Yellow 4 X X Zannichellia horned pondweed palustris Yellow 4 X heart-leaved Alexanders Zizia aptera Yellow 4 X
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Appendix 8c. Descriptions of rare plant taxa located in the study area in 2008.
(Note: these descriptions have been simplified but complete botanical descriptions have also been prepared.)
Anemone virginiana (L.) var. cylindroidea B. Boivin
English Name: Riverbank anemone.
Description: Perennial herbaceous plant with one or few erect stems up to 1 m tall; leaves dark green, deeply divided into three (sometimes more), large leaflets; flowers 1-4 cm wide, with five white, greenish, yellow or reddish sepals and no petals; fruits small and nut-like, in tight, head- like clusters.
Global Range: Southern boreal North America, forming a narrow arc from northern British Columbia, south to Minnesota and east to Quebec.
Ranking: Currently ranked as G5T4T5 S1, but the subnational ranking should be raised based on the number of populations found in the project area; Red-listed.
Significance: Previously known from the Peace Lowland.
Global Habitat: Dry woods, sandy ridges and grasslands, on high-pH soils.
Local Habitat: Riparian forest, aspen forest, mixed conifer-deciduous forest, grasslands, roadsides.
TEM Habitat Type: Observed in the BWBSmw1 AM and FM02 habitat types, and in the transition between the BWBSmw1 WW and SW habitat types. This plant has a broad range of available habitats, and its occurrences cannot be predicted by these habitat types.
Local Occurrence: Found in rare plant transects 3, 5, 6, 9, 11w, 11e, and 26, where observed to occur as single or few plants scattered in various microhabitats.
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Notes: This is one of our largest, showiest species of Anemone in British Columbia. Small specimens dwarfed by drought conditions can easily be confused with Anemone cylindrica .
References: Dutton et al. 1997; Douglas et al. 1999; British Columbia Ministry of Environment 2008.
Arnica chamissonis Less. ssp . incana (A. Gray) Hultén
English Name: “Meadow arnica” is applied to the species, inclusive of subspecies. In British Columbia, no English name exists for the subspecies.
Description: A short-rhizomatous perennial with tall, erect stems; leaves lance-shaped or narrowly elliptical, entire, positioned in pairs along the stem; flowers in daisy-like heads with large yellow ray flowers in a ring surrounding the small, inconspicuous disc flowers; fruits similar to sunflower seeds, blackish.
Global Range: Found along the Pacific Slope from British Columbia to California, rarely east to Montana.
Ranking: G5T3T5 S2S3; Blue-listed.
Significance: Previously known from the Peace Lowland; the Peace population is the only one known from east of the Rocky Mountain crest.
Global Habitat: Marshes and lakeshores.
Local Habitat: Meadowy fringe of an aspen-spruce forest, where it grades into an open marsh; moist, rich soil.
TEM Habitat Type: Observed on the edge of the BWBSmw1 AM habitat type, but actually in the transition between this habitat type and the SE type.
Local Occurrence: Found in rare plant transect RP06, where limited to a small area.
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Notes: The most recent taxonomic study on the genus Arnica did not accept the subspecies of A. chamissonis as valid taxa. The only trait that separates ssp . incana from the other subspecies is the degree of hairiness (woolly hairs so dense as to make the plants appear grey in ssp . incana , sparser woolly hairs and a green colour in the other subspecies). This trait could easily have evolved more than once, making ssp . incana a dubious taxon.
References: Douglas et al. 1998a; Hitchcock & Cronquist 1973; Scoggan 1976; Wolf 2006; British Columbia Ministry of Environment 2008.
Artemisia herriotii Rydb. ( Artemisia longifolia misapplied in BC)
English Name: No English name exists. The Latin name suggests the English name “Herriot’s mugwort”.
Description: A medium-sized to very tall, aromatic herbaceous plant with numerous stems emerging from a root crown, not rhizomatous; leaves linear to narrowly elliptical or oblanceolate, with few or no lobes, the lower surface silvery with woolly hairs, the upper surface glossy and dark green when mature; inflorescence a large, dense panicle of vase-shaped flower heads 3-4 mm long, the individual flowers brownish and inconspicuous.
Global Range: The southern boreal of interior North America, from northeast BC, scattered southward through Alberta and southern Saskatchewan to South Dakota and Wisconsin, probably also in Manitoba.
Ranking: Not ranked in NatureServe, but the suggested ranking is G3 S2; Red-listed. NOTE: this species should receive the subnational ranking given to Artemisia longifolia , since all occurrences of that species in the province are actually A. herriotii , and so the only change needed is to change the name on these Element Occurrences.
Significance: Not previously known from British Columbia. This is a globally rare species. Older collections from the province are known, but these were misnamed as either A. longifolia, A. ludoviciana , A. tilesii , or A. suksdorfii .
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Global Habitat: Open to lightly shaded riparian corridor habitats along rivers and larger creeks, less often in grassland habitat.
Local Habitat: As with the global habitat.
TEM Habitat Type: Observed in the BWBSmw1 WH, WW, and Active Channel habitat types. Of these, only the Active Channel habitat type can be used as an accurate predictor of occurrences, though only the rarely flooded portions of this habitat are occupied.
Local Occurrence: Found in rare plant transects 8w, 9, 11w, 11e, 15, 25, and 26, where often found in extensive areas.
Notes: In British Columbia, populations of this species are misnamed as Artemisia longifolia. Artemisia longifolia does not occur in British Columbia, it is known from southern Alberta and Manitoba, south to Colorado and South Dakota.
References: Rydberg 1910; Keck 1946; Breitung 1957; Scoggan 1976; Douglas et al. 1998a; Schultz 2006.
Boechera sparsiflora (Nutt.) Dorn (Syn. Arabis sparsiflora)
English Name: Sickle-pod rockcress
Description: A single-stemmed plant from a leaf rosette, growing to as much as 1.5 m tall; rosette leaves narrowly oblanceolate; stem leaves narrowly arrow-shaped; flowers small, white, creamy yellowish or purple, in a tall, narrow raceme; fruits linear, generally downwardly arched, on a short stem that spreads or arcs out from the main stem.
Global Range: British Columbia and the Yukon south to northeastern California and Wyoming. This range will likely contract once the species is split into additional species.
Ranking: Currently ranked as G5 S1, but this ranking should change based on recent taxonomic revisions; Red-listed.
Significance: Previously reported from the project area.
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Global Habitat: In open, dry forest, rock outcrops, fine scree, river gravel bars, grassland, and sagebrush steppe.
Local Habitat: Forest clearings, grassland, and gravel bars.
TEM Habitat Type: Observed in the BWBSmw1 AM, WW, and Active Channel habitat types. This species’ requirements seem to be only full sun and coarse soils, so the TEM habitat types are poor predictors of occurrences.
Local Occurrence: Found in rare plant transects 1, 4, 5, 11w, 11e, 13, and 26.
Notes: Species of the genus Boechera have traditionally been placed in Arabis , which is dissimilar in morphology and is not closely related (Al-Shehbaz 2003). The move of most of our British Columbia “Arabis” species to Boechera is accompanied by a revision of our species in recent work by Ihasan Al-Shehbaz. With this revision, it is likely that most of the populations attributable to “ Arabis sparsiflora ” by use of the keys in the Illustrated Flora of BC (Douglas et al. 1998b) will be other species.
References: Douglas et al. 1998b; British Columbia Ministry of Environment 2008.
Calamagrostis montanensis (Scribn.) Vasey
English Name: Plains reedgrass.
Description: A medium-sized grass with narrow leaves, usually bunch-forming, but with rhizomes; inflorescence narrow and erect; flowers highly modified into a pair of glumes and a pair of lemmas, the lemmas with a short, bent awn and with straight hairs about 1/3 the length of the lemmas.
Global Range: Central North America from BC and Manitoba south to Idaho and Minnesota.
Ranking: G5 S3 (the subnational ranking is not based on observed populations, but rather on predicted abundance); Blue-listed.
Significance: Previously known in the Peace Lowland.
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Global Habitat: Grassland on heavy, high-pH soil.
Local Habitat: Open grassland on south-facing slopes.
TEM Habitat Type: Observed in the BWBSmw1 WW habitat type.
Local Occurrence: Found in rare plant transects RP09 and RP26.
Notes: This species has an appearance similar to that of the more common and widespread grass Koeleria macrantha , so it may be overlooked, and some reported populations of it could be misnamed K. macrantha .
References: Hitchcock 1971; Hitchcock & Cronquist 1973; Douglas et al. 2001b; British Columbia Ministry of Environment 2008.
Carex heleonastes L. f.
English Name: Hudson Bay sedge.
Description: A grass-like herbaceous plant forming loose bunches of erect stems; leaves crowded at the base, narrow; inflorescence a spike of oval flower heads, each flower highly modified into a light brown, elliptical, pocket-bread like perigynium surrounding the single- seeded fruit.
Global Range: Boreal regions of North America and Eurasia.
Ranking: G4 S2S3; Blue-listed.
Significance: Not previously known from the Peace Lowland, but known elsewhere in northeast BC.
Global Habitat: Bogs, mires, muskeg forest, and cold meadows at low elevations.
Local Habitat: Open muskeg forest.
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TEM Habitat Type: Observed in the BWBSmw1 TS habitat type, but this species’ habitat requirements are not those that define the TS.
Local Occurrence: Found in rare plant transect RP06.
References: Douglas et al. 2001a; Toivonen 2002; British Columbia Ministry of Environment 2008.
Carex sychnocephala J. Carey
English Name: Many-headed sedge.
Description: A small to medium sized clump-forming grass-like plant; leaves and stems deep green, with abundant leaves crowded at the base; flowers awl-shaped surrounding a flattened, single-seeded fruit, the inflorescence formed of tight clusters of flower heads surrounded by long, leafy bracts.
Global Range: Northern temperate and boreal North America.
Ranking: G4 S3; Blue-listed.
Significance: Not previously known in the B.C. Peace Lowland.
Global Habitat: Wet or seasonally wet habitats where soils are calcareous or moderately saline.
Local Habitat: Open, drier portions of a calcareous marsh, with some minor encrustation of salts at the soil surface.
TEM Habitat Type: Observed in the BWBSmw1 SE habitat type, which encompasses a wide array of wetland types. The wetland classification of MacKenzie & Moran (2004) does not provide a wetland habitat type that resembles this site.
Local Occurrence: Found in rare plant transect RP06.
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References: Douglas et al. 2001a; Mastrogiuseppe 2002; British Columbia Ministry of Environment 2008.
Carex vulpinoidea Michaux
English Name: Fox sedge.
Description: A medium to large sized, clump-forming, grass-like herbaceous plant with yellowish-green leaves crowded toward the base; flowers highly modified into egg-shaped, flattened, ensheathing perigynia surrounding a small, one-seeded fruit.
Global Range: Widespread in southern boreal to subtropical North America, south to northern Mexico.
Ranking: G5 S2S3; Blue-listed.
Significance: Not previously known in northern BC. This population is highly isolated, the nearest populations being in southern BC and southern Alberta.
Global Habitat: Open sites in seasonally wet meadows, marshes, and ditches.
Local Habitat: Cobbly margins of a shallow pool in the dry channel between a large slough and the open river channel.
TEM Habitat Type: Observed in the ‘Active Channel’ habitat type.
Local Occurrence: Found in rare plant transect RP11e.
References: Douglas et al. 2001a; Standley 2002; British Columbia Ministry of Environment 2008.
Carex sp. nov. ( cf. Carex atherodes Spreng.)
English Name: No English name exists.
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Description: A tall, grass-like herbaceous plant that spreads by its rhizomes to form dense stands; leaves dark green, with a sheath around the stem, the sheath with dense hairs, and a dark purple colouration at its apex; the inflorescence of oval-shaped spikelets widely separated on a long spike.
Global Range: Thus far known only within the project area.
Ranking: The range of this taxon is not yet known, but at present, it is known from only two populations, which would place it at G1 S1.
Significance: Previously undescribed , and thus far known only within the project area.
Global Habitat: More persistently wet areas of marshes.
Local Habitat: Same as the global habitat.
TEM Habitat Type: Observed in the BWBSmw1 SE habitat type, though this type encompasses many wetland habitats.
Local Occurrence: Found in rare plant transects RP06 and RP20.
Notes: This species is closely related to the common and widespread Carex atherodes , and may be only a form of it, though perhaps one that could be named as a new varietal taxon.
References: Reznicek & Catling 2002.
Carex sp. nov. cf. tenera (intermediate between C. tenera Dewey and C. crawfordii Fernald)
English Name: No English name exists.
Description: A medium-sized, clump-forming, grass-like plant having yellowish green leaves crowded around the base of the plant; flowers highly modified into an ensheathing, lance- shaped perigynium that surrounds a small single-seeded fruit.
Global Range: Thus far known only from the project area.
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Ranking: The range of this taxon is not yet known, but at present, it is known from only six populations, which would place it at G1 S2.
Significance: Possibly a new species to science.
Global Habitat: Various open sites in wetlands, as in marshes, swales and along river shores.
Local Habitat: Same as the global habitat.
TEM Habitat Type: Observed in the BWBSmw1 SW, WHa, SE and ‘Active Channel’ habitat types, the former two of which have little to do with the microhabitat requirements of this species in these sites, and the latter two of which are poor surrogates for this species’ rather broad requirements of wet or moist, silty soil with no apparent salt concentration.
Local Occurrence: Found in rare plant transects 1, 5, 6, 11w, 11e, and 24.
Notes: This species is intermediate in its morphology between Carex crawfordii and Carex tenera . Carex tenera is Blue-listed in British Columbia, and has been reported from the project area. These reports may actually represent this intermediate species. Typical Carex tenera is known elsewhere in B.C. Carex crawfordii is common and widespread in the province.
References: Mastrogiuseppe et al. 2002.
Chrysosplenium iowense Rydb.
English Name: Iowa golden-saxifrage.
Description: A small, delicate, perennial herbaceous plant with dark green kidney-shaped leaves arranged alternately on the stem; leaf upper surface veiny; flowers greenish yellow, in flat-topped clusters, often with outer flowers somewhat larger than those in the centre of the cluster; inflorescence leaves bract-like, bright yellow-green; sepals four in number, spreading outward, rounded, in one smaller and one larger pair; petals absent; anthers 2-8 in number; fruits thin-walled, splitting widely into two, the dark brown seeds held in one cluster for each of the two fruit halves.
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Global Range: Northeast BC and the adjacent Northwest Territories, eastward through boreal regions to Manitoba and Minnesota, south to Iowa.
Ranking: G3? S2S3; Blue-listed.
Significance: Previously known in the Peace Lowland. This is a globally rare species.
Global Habitat: Said to grow along creeks, in meadows, bogs, and springs. Some of these habitats may be incorrectly reported, based on misidentified populations of Chrysosplenium tetrandrum .
Local Habitat: Along cold-water spring outflow on shale.
TEM Habitat Type: Found in the BWBSmw1 SW habitat, but the characteristics used to define this habitat have little to do with the habitat requirement of this species.
Local Occurrence: Found in rare plant transect RP08w.
Notes: Chrysosplenium iowense does not prefer nitrogen-enriched sites, but appears to require cold, high-pH water, as along spring outflow coming from calcareous soil and shale beds.
References: Douglas et al. 2000; British Columbia Ministry of Environment 2008; Centre for Plant Conservation 2008; Levsen & Mort 2008.
Cicuta virosa L.
English Name: European water-hemlock.
Description: A perennial herbaceous plant growing from tubers; leaves compound with widely angled, serrated, narrowly elliptic or lance-shaped leaflets, deep green; stems up to one metre tall; flowers in round clusters in which the branches all emerge from the same terminal point of the stem; petals white or pinkish; fruits round, or slightly wider than high.
Global Range: Boreal and north temperate portions of Eurasia and North America.
Ranking: G4G5 S2S3; Blue-listed.
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Significance: Previously known from the Peace Lowland.
Global Habitat: Marshes and shore lines.
Local Habitat: Found in an old, marshy beaver pond.
TEM Habitat Type: Observed in the BWBSmw1 SE habitat, which does not differentiate between various marsh, sedge meadow, shoreline and beaver pond habitats. The classification of MacKenzie & Moran (2004) gives a somewhat close match in the Wm01 type, which is dominated by Carex utriculata and Calamagrostis canadensis .
Local Occurrence: Found in rare plant transect 25.
Notes: This species is deadly toxic. It is tolerant of the rapid hydrological changes in beaver ponds and receding shorelines, and it may disappear from more stable wetland habitats, where it may first function as a pioneer species, later to be excluded by a more climactic vegetation. The form observed in the project, and those seen by the lead botanist elsewhere in British Columbia, has broad leaflets, over 2 cm wide. Most populations in North America have leaflets less than 1 cm wide. This characteristic is the basis for the varietal taxon var. latisecta Celikovski, which is so far only known in central and eastern Eurasia. Most North American populations reported as Cicuta virosa may best be split off as the North American endemic C. mackenzieana , but the population in the project area clearly does not fit with that species.
References: Douglas et al . 1998a; British Columbia Ministry of Environment 2008.
Cicuta sp. nov.
English Name: No English name exists.
Description: A tall herbaceous perennial with abundant leaves along the stem, the leaves twice compound with lanceolate, dark green, serrated leaflets; inflorescence with 30-60 branches, all emerging from the same terminal points of the stems; flowers greenish, the petals abruptly narrowed to a stalked base; young fruits narrowly triangular.
Global Range: Thus far known only from a single plant in the Watson Slough. July 2009 -314-
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Ranking: Only a single plant known globally, so G1 S1.
Significance: Previously undescribed .
Global Habitat: Margin of a ditch in the transition between open marsh and spruce/birch/aspen forest.
Local Habitat: Same as the global habitat.
TEM Habitat Type: Found in the SE habitat type. However, this habitat type is too general, and unites many dissimilar wetland types. The classification of MacKenzie & Moran (2004) does not describe any wetland type that would be a good match.
Local Occurrence: Found in rare plant transect RP06.
Notes: Only a single plant was found despite extensive searching, and upon revisiting it in September, we found that it had been killed by trampling. It was growing on the steep edge of a ditch, so when it was trampled it broke at the root and the whole plant died, though any underground tubers may regenerate vegetative growth in the next year. This plant is likely to be deadly toxic, as are all members of the genus Cicuta . There are no similar species in the North American or Eurasian floras. Cicuta is a small genus of between three and seven species, depending on the classification. All of these species have been accounted for in consideration of the correct placement of the Watson Slough plant.
References: Fernald 1950; Hitchcock & Cronquist 1973; Scoggan 1979; Hickman 1993; Cody 1996; She & Watson 2008.
Cirsium drummondii Torr. & A. Gray
English Name: Drummond’s thistle.
Description: A large, prickly, biennial or short-lived perennial herbaceous plant with a very wide basal rosette; stems as much as three metres tall, terminating in large flower heads with prickly bracts; flowers long tube-shaped, reddish purple, very showy.
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Global Range: British Columbia east to Ontario and south to Wyoming.
Ranking: G5 S1; Red-listed.
Significance: Known in British Columbia only in the Peace Lowland.
Global Habitat: Meadows, roadsides and forest clearings.
Local Habitat: Same as the global habitat.
TEM Habitat Type: Observed in the BWBSmw1 AM habitat type, as well as unclassified human-disturbed habitat in the heavily grazed cleared area below powerlines.
Local Occurrence: Found in rare plant transects RP06 and RP20.
Notes: This is a particularly showy, garden-worthy native thistle species.
References: Douglas et al . 1998a; British Columbia Ministry of Environment 2008.
Cystopteris sp. nov.
English Name: No English name exists.
Description: A small fern growing from scaly, creeping rhizomes; leaves somewhat firm, ascending or drooping, twice divided into small leaflets, with tufts of hair-like scales at the attachment point of the primary leaflets; spore capsules ensheathed when young in a pocket- like flap.
Global Range: Thus far known only in the project area, plus one population from the Rocky Mountains.
Ranking: Not known.
Significance: Previously undescribed .
Global Habitat: On tufa and soil cut-banks.
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Local Habitat: Same as the global habitat.
TEM Habitat Type: Observed in the BWBSmw1 SW habitat type; this habitat type is defined using characteristics that have little to do with the larger-scale habitat requirements of this fern.
Local Occurrence: Found in rare plant transects 2, 3, 7, 8e, and 23.
Notes: Cystopteris in western Canada requires taxonomic work. It appears that more than one undescribed species exists in the area.
References: Lellinger 1985; Cody & Britton 1989.
Elymus sp. nov .
English Name: No English name exists.
Description: A rhizomatous grass with stems to 8 dm high; leaves stiff, 2-7 mm wide, flat or somewhat incurled, evenly dispersed up the stem, inflorescence a dense spike with one spikelet per node, the spikelets about twice as long as the internode, making the spike appear dense.
Global Range: Known thus far only from the project area.
Ranking: Known from only two populations, so initially, this would be ranked G1 S1.
Significance: Previously undescribed , and not known from outside the project area.
Global Habitat: Open grasslands on deep, rich soil on south slopes.
Local Habitat: Same as the global habitat
TEM Habitat Type: Observed in the BWBSmw1 WW habitat type.
Local Occurrence: Found in rare plant transects RP04 and RP09.
Notes: . That this plant could be a hybrid of Elymus lanceolatus and Pascopyrum smithii (Elymus-Pascopyrum hybrids are known) was considered, but rejected since the anthers and
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References: Hitchcock & Cronquist 1973; Scoggan 1978; Barkworth & Dewey 1985; Cody 1996; Douglas et al. 2001b; Barkworth et al. 2008.
Epilobium halleanum Hausskn.
English Name: Hall’s willowherb.
Description: A small to medium sized, slender herbaceous plant growing from bulb-like turions from underground; leaves dark green, broadly lance-shaped, partly opposite on the stem and partly alternate; stems more or less square in cross-section, hairy in lines that extend downward from the corners of the leaf bases; inflorescence usually nodding in the bud, somewhat leafy; flowers at the tips of ensheathed ovaries, small, the petals notched, white or pinkish; fruits 2.5-6 cm long, narrowly club-shaped, splitting down the middle into four portions when dry, releasing the small, plumed seeds.
Global Range: Western and central North America.
Ranking: G5 S2S3; Blue-listed.
Significance: Not previously known from the B.C. Peace Lowland.
Global Habitat: Open sites in various wetland types, usually on humus-rich soil.
Local Habitat: Found in open muskeg forest of short-stature trees, on high-pH, peaty soil.
TEM Habitat Type: Found in the BWBSmw1 TS habitat type, but the species can occur in a wide variety of habitat types, preferably in marshes and seeps, so the TS should not be used to predict occurrences of this species.
Local Occurrence: Found in rare plant transect RP06.
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References: Douglas et al. 1999a; Wagner & Hoch 2005; British Columbia Ministry of Environment 2008.
Epilobium leptocarpum Hausskn.
English Name: Small-flowered willowherb.
Description: A small to medium sized, slender herbaceous plant growing from bulb-like turions from underground; leaves yellowish to medium green, broadly elliptical or ovate to lance- shaped, partly opposite on the stem and partly alternate; stems more or less square in cross- section, hairy in lines that extend downward from the corners of the leaf bases; inflorescence usually nodding in the bud, somewhat leafy; flowers at the tips of ensheathed ovaries, small, the petals notched, white or pinkish; fruits 2.5-8 cm long, narrowly club-shaped and held on long stalks, splitting down the middle into four portions when dry, releasing the small, plumed seeds.
Global Range: Northwestern North America, from southern Alaska through British Columbia and western Alberta, to northern Oregon, Idaho and northwest Montana.
Ranking: G5 S2S3; Blue-listed.
Significance: Previously known from the Peace Lowland in B.C.
Global Habitat: Various wetlands in full sun to partial shade, generally at upper elevations or other areas with cool temperatures.
Local Habitat: Sparser-vegetated portions of an open marsh of tall sedges, periodically flooded.
TEM Habitat Type: Observed in the BWBSmw1 SE habitat type, which includes many types of marsh, shoreline, and sedge meadow vegetation; the classification of MacKenzie & Moran (2004) does not provide a particularly good match of this marsh vegetation type.
Local Occurrence: Found in rare plant transect RP06.
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References: Douglas et al. 1999a; Wagner & Hoch 2005; British Columbia Ministry of Environment 2008.
Epilobium sp . nov.
English Name: No English name exists.
Description: Medium-sized, perennial, herbaceous plants with few ascending stems that are evenly covered in spreading, glandular hairs, hairs not in vertical lines from the leaf bases, no strigillose hairs present; Inflorescence erect in the bud; flowers exerted on stalks; petals notched, pinkish, small; fruits glandular hairy, spreading somewhat out from the stem, splitting vertically into four parts when dry, releasing the plumed seeds.
Global Range: Thus far known only from the project area.
Ranking: Only a single population known, which would give a ranking of G1 S1.
Significance: Previously undescribed .
Global Habitat: Found in seasonally moist soil in a small gully at edge of a marsh and an aspen grove. However, the habitat requirements for the species are not likely to be so specific.
Local Habitat: Same as for the global habitat.
TEM Habitat Type: Observed in the BWBSmw1 AMy:ap habitat type, though this type does not describe the localized habitat of the plant community in which the Epilobium occurs.
Local Occurrence: Found in rare plant transect RP06, where limited to a small area.
Notes: This species differs from others Epilobia in British Columbia having glandular hairs all around the stems, in that it is a slender perennial with elliptical leaves, and not clump-forming nor decumbent at the stem base. More work is needed.
References: Douglas et al. 1999a; Wagner & Hoch 2005.
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Erigeron sp. nov (aff . E. cespitosus )
English Name: No English name exists.
Description: Perennial, small, daisy-like herbaceous plant with a ropy rootstock that terminates in a branched caudex; stems unbranched, ascending or spreading, up to 2 dm high, leaves narrowly elliptical or oblanceolate, flowers in daisy-like heads that are single or few at the stem tips; ray flowers white or slightly pinkish, remaining straight, not curling upon drying; disc flowers inconspicuous, with a soft, non-indurate tube.
Global Range: Thus far known only from the project area.
Ranking: Only two populations are known, so this would be ranked as G1 S1.
Significance: Potentially a new species to science.
Global Habitat: Open grassland in areas with no shade, and minimal root competition.
Local Habitat: Same as for the global habitat.
TEM Habitat Type: Observed in the BWBSmw1 WW habitat type.
Local Occurrence: Found in rare plant transects RP01 and RP04.
Notes: This species comes close to Erigeron caespitosus , but differs in several characteristics.
References: Nesom 2006.
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Erigeron sp. nov (provisionally to be called Erigeron pacalis )
English Name: No English name exists.
Description: Small, daisy-like, perennial herbaceous plant from a taproot; stem base strongly purple-pigmented, the upper portion of the stem with sparse to dense contorted hairs of even lengths, upper portions also with minute glandular hairs; leaves mostly basal, the basal leaves narrowly oblanceolate to spatulate, one-nerved; flowers in a single head at the tip of a stem 3-5 cm high; ray flowers white, straight, not reflexing or curling upon drying; disc flowers inconspicuous, tubular, not hardened, glabrous; fruit fused onto the single seed, tipped with a plume of minutely barbed hairs.
Global Range: Thus far known only from a single collection.
Ranking: Since this is known from only a single collection, the ranking should be G1 S1.
Significance: Previously undescribed , not known from outside the project area.
Global Habitat: Open grassland in areas with no shade, and minimal root competition.
Local Habitat: Same as for the global habitat.
TEM Habitat Type: Observed in the BWBSmw1 WW habitat type.
Local Occurrence: Found in rare plant transect RP07.
Notes: This species is a stand-out in British Columbia’s flora, having a unique set of characteristics among the province’s Erigeron species.
References: Cronquist 1947; Nesom 2006.
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Galium labradoricum (Wieg.) Wieg.
English Name: Northern bog bedstraw.
Description: Wirey, perennial plant from a slender creeping rhizome; stems ascending or erect, simple or branched above, smooth, up to 30 cm tall; leaves in whorls of 4, oblanceolate or spatulate, rounded at the tips, deep green; flowers white, about 2.5 mm wide, with four petals; fruits round, smooth nutlets in pairs, dark brown.
Global Range: Across boreal North America, south to north-temperate eastern North America.
Ranking: G5 S2S3; Blue-listed.
Significance: Previously known from the Peace Lowland.
Global Habitat: Bogs, muskeg forest and swamps.
Local Habitat: Boggy clearings in muskeg forest.
TEM Habitat Type: Observed in clearings in the BWBSmw1 TS habitat type. The TS type does not accurately describe the ecological requirements of this species.
Local Occurrence: Found in rare plant transect RP21.
Notes: The similar-appearing Galium brandagei may account for some reports of G. labradoricum in British Columbia. This species is rarely found in the western Canadian boreal forests, but is not yet known in British Columbia. It may also account for the population reported here. Flowering material is needed to resolve this.
References: Fernald 1950; Cody 1996; Douglas et al. 1999b; British Columbia Ministry of Environment 2008.
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Geum triflorum Pursh var. triflorum
English Name: No English names exist in British Columbia for the varieties of this species. “Old man’s whiskers” is applied widely in the province to the species inclusive of variety, while east of the Rocky Mountains, the name “prairie smoke” is often applied, and that would better refer to the variety present in the Peace Valley.
Description: An herbaceous perennial plant with winter-green basal leaves that are divided into numerous hand-shaped segments
Global Range: Northeastern British Columbia through the Prairies to the Great Lakes, south to Colorado, Illinois and Ohio.
Ranking: The varieties are not ranked in BC, though they are recognized in the Conservation Data Centre’s list of plants of the province. The ranking should be G5T5 S2S3.
Significance: Previously known in the Peace Lowland, which is the variety’s only range in the province.
Global Habitat: Open grassland, rock outcrops, and forest clearings, always in full sun on well- drained, calcareous soil.
Local Habitat: Open grassland and forest clearings.
TEM Habitat Type: Observed in the BWBSmw1 WW habitat type.
Local Occurrence: Found in rare plant transects RP04, RP05, RP09, RP013, and RP026.
Notes: Geum triflorum is represented in the province by two varieties, var . ciliatum , and var . triflorum . The former occurs on the Pacific slope and is common in the province, while the latter occurs only east of the Rocky Mountain crest and is rare.
References: Fernald 1950; Douglas et al. 1999b; British Columbia Ministry of Environment 2008.
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Helictotrichon hookeri (Scribn.) Henr.
English Name: Spike-oat.
Description: A medium-sized bunch-forming grass
Global Range: Northern prairies of North America, south through the High Plains of the U.S. Rocky Mountains to New Mexico.
Ranking: G5 S2S3; Blue-listed.
Significance: Previously known from the Peace Lowland.
Global Habitat: Open, dry grassland.
Local Habitat: Same as for the global habitat.
TEM Habitat Type: Observed in the BWBSmw1 WW habitat type.
Local Occurrence: Found in rare plant transect RP04.
References: Hitchcock 1971; Douglas et al. 2001b; British Columbia Ministry of Environment 2008.
Juncus arcticus Willd. ssp. alaskanus (Hultén) S. Welsh
English Name: The name “Arctic rush” is applied to the species, inclusive of varieties, but this is particularly problematic since there are varying classifications of the genus that sometimes place other species (i.e., Juncus balticus ) under Juncus arcticus , so then, “Baltic rush” would become “Arctic rush”?
Description: A rhizomatous, grass-like, perennial plant with stiffly erect, round stems
Global Range: Arctic and boreal regions of North America and eastern Eurasia.
Ranking: G5T4T5 S2S3; Blue-listed.
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Significance: Not previously known from the Peace Lowland.
Global Habitat: Wet meadows and streambanks.
Local Habitat: Graminoid-dominated fringe of river upper shoreline habitat.
TEM Habitat Type: Observed in what would classify (loosely) as the ‘Active Channel’ or SE habitat type. The wetland classification of MacKenzie & Moran (2004) does not give a similar habitat type to that observed.
Local Occurrence: Found in rare plant transect RP01.
References: Brooks & Clemants 2000; Douglas et al. 2001a; British Columbia Ministry of Environment 2008.
Malaxis brachypoda (A. Gray) Fernald (syn. Malaxis monophyllos var. brachypoda )
English Name: White adder’s mouth orchid, or one-leaved malaxis.
Description: A small orchid growing from bulb-like swollen leaf bases, producing a single leaf per year; leaf yellowish green, tongue-shaped, somewhat succulent; flowers numerous in a raceme on a leafless stalk, the individual flowers 2-4 mm wide, the flower stalk twisted 180º so that the flowers are upside-down; petals and sepals greenish, narrowly lance-shaped.
Global Range: Across southern boreal to north-temperate North America.
Ranking: G4Q S2S3; Blue-listed.
Significance: Not previously known from the Peace Lowland.
Global Habitat: Swamps and bogs, usually in calcareous regions.
Local Habitat: On firmer, humus-rich soil in muskeg forest, under a fairly open canopy.
TEM Habitat Type: Observed in the BWBSmw1 BT habitat type.
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Local Occurrence: Found in rare plant transect RP22.
References: Catling & Magrath 2002; Douglas et al. 2001b; British Columbia Ministry of Environment 2008.
Muhlenbergia glomerata (Willd.) Trin.
English Name: Marsh muhly or spike muhly.
Description: A tufted, rhizomatous, greyish-green, perennial grass up to one metre tall
Global Range: Southern boreal North America, scattered sporadically southward to Nevada, Colorado, and Virginia.
Ranking: G5 S3; Blue-listed.
Significance: Not previously known in the British Columbia Peace Lowland.
Global Habitat: Alkaline wetlands, less often on gravelly slopes or around hot springs.
Local Habitat: Growing around open areas of marl fens, where forming hummocks along with its codominant species Carex viridula, Muhlenbergia sp. nov., and Trichophorum pumilum .
TEM Habitat Type: Observed in a wetland type (marl fen) for which there is no corresponding type in the classification of British Columbia wetlands (MacKenzie & Moran 2004).
Local Occurrence: Found in rare plant transect RP05.
References: Douglas et al. 2001b; Peterson 2005; British Columbia Ministry of Environment 2008.
Muhlenbergia sp. nov.
English Name: No English name exists.
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Description: A slender, wiry, tufted grass with runners (stolons); stems branching; leaves thin and flat or folded.
Global Range: Thus far known only from the project area.
Ranking: Being that this species is known only from a single site, it should be ranked G1 S1.
Significance: Previously undescribed .
Global Habitat: On hummocks around marl fens.
Local Habitat: As for the global habitat.
TEM Habitat Type: Observed in a wetland type (marl fen) for which there is no corresponding type in the classification of British Columbia wetlands (MacKenzie & Moran 2004).
Local Occurrence: Found in rare plant transect RP05.
Notes: Materials collected in a marl fen in RP05 are intermediate in characteristics between M. cuspidata , M. filiformis, and M. richardsonis .
References: Peterson 2005.
Oxytropis campestris (L.) DC. var. davisii S. Welsh (syn. Oxytropis jordalii var. davisii )
English Name: “Jordal’s locoweed” is applied to the species, inclusive of varieties, but this does not allow the two varieties to be distinguished. No English name is available for var. davisii .
Description: A small, herbaceous perennial plant forming patches from a branched root crown; leaves silvery with woolly hairs, split into numerous leaflets, many of which are clustered in fours, others in twos; flowers in head-like clusters at the top of a leafless stalk; sepals fused into a tube covered in white and black hairs; petals pink, purple or creamy whitish.
Global Range: A regional endemic of northwest Alberta west to northeast British Columbia and adjacent Northwest Territories.
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Ranking: G5T3 S3; Blue-listed.
Significance: A regional endemic, previously known from the project area.
Global Habitat: River gravel bars, grassland, and forest clearings, always on coarse soils.
Local Habitat: River gravel bars.
TEM Habitat Type: Observed in the BWBSmw1 ‘Active Channel’ habitat type, which appears to be a good predictor of occurrences of this plant.
Local Occurrence: Found in rare plant transects RP8w, RP09, RP11e, and RP15.
References: Douglas et al. 1999a; British Columbia Ministry of Environment 2008.
Packera plattensis (Nutt.) W.A. Weber & A. Löve (syn. Senecio plattensis )
English Name: Plains butterweed.
Description: A small perennial plant growing from fibrous roots and sometimes rhizomatous; flowers in up to twenty or so daisy-like heads with yellow ray flowers and inconspicuous disc flowers.
Global Range: Temperate to southern boreal eastern and central North America, peripheral in northwest North America.
Ranking: G5 S2S3; Blue-listed.
Significance: Previously known in the Peace Lowland.
Global Habitat: Grassland, meadows, river banks, open woods, disturbed areas, always on high-pH soils, especially over limestone.
Local Habitat: River shoreline, aspen forest, and willow swale habitats.
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TEM Habitat Type: Observed in the BWBSmw1 AM, SW, AMy:ap, SE and ‘Active Channel’ habitat types. These types do not effectively describe the actual habitat requirements of this species. These requirements are broad, being only that it be moist, high-pH soil and full sun or partial shade.
Local Occurrence: Found in rare plant transects RP02, RP05, RP06, RP08w, RP09, RP11w, RP11e, and RP20.
Notes: The British Columbia Conservation Data Centre lists this species as Senecio plattensis . Most other members of the Natural Heritage Network in North America list it as Packera . Packera species do not belong in Senecio .
References: Douglas et al . 1998a; Trock 2006; British Columbia Ministry of Environment 2008.
Pedicularis parviflora Smith ex Rees ssp. parviflora
English Name: Small-flowered lousewort.
Description: A tall, slender herbaceous perennial with long branches emerging from near the base; leaves divided and toothed into narrow segments, mostly alternate on the stem, flowers in long, sparse spikes.
Global Range: Sparsely scattered through boreal North America as far east as Quebec, also in northeast Asia.
Ranking: G4T4 S3; Blue-listed.
Significance: Previously known from the Peace Lowland.
Global Habitat: Bogs and muskeg forest.
Local Habitat: On firm soil adjacent to a frequently used moose trail in mature muskeg forest.
TEM Habitat Type: Observed in the BWBSmw1 BT habitat type, but this species could occupy additional habitat types.
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Local Occurrence: Found in rare plant transect RP21.
Notes: Two forms of this species are sometimes recognized as separate species, the coastal form has undivided bract leaves and occurs in northeast Asia, and reaches into coastal Alaska and northwest British Columbia. The form found in the project area has deeply divided bracteating leaves and is a rarer species, found sporadically in interior boreal North America from interior Alaska and B.C. to Quebec. This latter form is named Pedicularis macrodonta by some, and further study of specimens may find that this split is merited.
References: Douglas et al. 2000; British Columbia Ministry of Environment 2008.
Penstemon gracilis Nutt .
English Name: Slender penstemon.
Description: A perennial herbaceous plant growing as single or few stems from a subterranean root crown; leaves opposite on the stem; flowers numerous in narrow arrays, the petals pale purple, fused, forming a long tube with distinct upper and lower halves, the lower half with thin purple penciling.
Global Range: Throughout the Canadian Prairies and U.S. Great Plains.
Ranking: G5 S2; Red-listed.
Significance: Known in British Columbia only in the Peace Lowland.
Global Habitat: Open grassland, usually on sandy or gravelly soil.
Local Habitat: Open grassland, on loamy soil.
TEM Habitat Type: Observed in the BWBSmw1 WW habitat type.
Local Occurrence: Found in rare plant transect RP26.
References: Strickler 1997; Douglas et al. 2000; British Columbia Ministry of Environment 2008.
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Platanthera aplectra ined.
English Name: No English name exists.
Description: A medium-sized herbaceous perennial orchid with small, narrow, tuberous roots; stem single, with tongue-shaped leaves diminishing in size upward; flowers pale green, in a long raceme, with three sepals and three petals, the upper one sepal and upper two petals cupping together to form a hood, the lower two sepals spreading out like wings, and the lower petal modified into a pear-shaped ‘lip’.
Global Range: So far known only from the project area.
Ranking: A single population known, so this would be G1 S1.
Significance: A putative new species.
Global Habitat: Open-canopy muskeg forest of small stature, but very old trees.
Local Habitat: Same as for the global habitat.
TEM Habitat Type: Observed within the BWBSmw1 TS habitat type.
Local Occurrence: Found in rare plant transects RP05 and RP06.
Notes: This is a putative new species. It is provisionally hereby named Platanthera acentron , which refers to the spurless morphology of the flowers.
This is clearly a close relative of Platanthera aquilonis , and probably evolved from it. Herbarium specimens of Platanthera need to be examined from western boreal Canada to see if this species occurs elsewhere. Plants of Platanthera aplectra occurred only within RP05. Platanthera aquilonis was encountered both in RP05 and in other transects. Like P. aquilonis , plants of P. aplectra occurred in peaty wetlands in open sites or light shade.
References: Sheviak 2002.
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Rorippa calycina (Engelm.) Rydb. sensu stricto
English Name: Persistent-sepal yellowcress, Hayden’s yellowcress.
Description: A biennial or short-lived perennial growing from a slender rhizome; vegetative parts covered in stiff, spreading hairs; leaves deeply lobed and divided, with ear-shaped lobes at the base where it attaches to the stem; flowers with four yellow petals; fruits egg-shaped, with sparse to dense hairs that are expanded at the base.
Global Range: Very sporadic on the High Plains of the United States in Montana, North Dakota, and Wyoming; also reported for Idaho, but this may be based on the similar species Rorippa columbiae.
Ranking: Ranked in NatureServe as G3. Not previously known in British Columbia. This should be ranked G3 S1 in the province.
Significance: Not previously known to occur in British Columbia. This is a globally rare and declining native species. Not previously known in the Peace Lowlands.
Global Habitat: Along shores of major rivers and lakes.
TEM Local Habitat: On sparsely vegetated muddy cobble bars.
Habitat Type: Observed in the ‘Active Channel’ habitat type.
Local Occurrence: Found in rare plant transects RP08w, RP08e, and RP11w, where very few individual plants were observed, and all within very small areas.
Notes: The species under consideration here is exclusive of Rorippa columbiae , another rare species that is sometimes treated as Rorippa calycina ssp . columbiae . The North Dakota population of Rorippa calycina is presumed extinct. In Montana, it is known from three historic populations and one recent observation, but none of these populations could be relocated in more recent surveys, and it is presumed extinct in the state. It is not known whether the population in the McKenzie River Delta found in the 1960’s still exists, but the species has not turned up in plant inventories along the McKenzie River or its tributaries since. The species’ greatest historic abundance is in Wyoming, and that state is now the only known current range
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The Montana Natural Heritage Program cites numerous possible factors in the disappearance of this species from its former range. Lead among them is the possibility that artificial hydrological conditions on managed rivers floods or desiccates this species at the wrong times of the year or for too long a period, or that the invasive non-native plants that frequent reservoir shorelines could outcompete it. They also state that certain management strategies in maintaining river levels could allow the species to persist along reservoirs, but no data exist that compare this species’ population dynamics before and after dam construction since the tracking of rare species in the U.S. started after the establishment of the dams in question. Overgrazing is also a possible cause for the loss of R. calycina populations.
References: Rocky Mountain Herbarium 2005; Montana Natural Heritage Program 2008; NatureServe Explorer 2008; Northern Prairie Wildlife Research Centre 2008.
Rumex britannica L.
English Name: English dock.
Description: A tall perennial herbaceous plant from a thick root stock; leaves present both at the base and up the stalk, egg-shaped to lance-shaped; inflorescence a large plume-like array, the individual flowers greenish, with six tepals (undifferentiated petals and sepals at flowering time.
Global Range: Throughout temperate and boreal regions of the central and eastern U.S., also in Eurasia.
Ranking: Ranked in NatureServe as G5. The observations in the project area suggest that this species should be initially ranked G5 S2S3 in British Columbia.
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Significance: Not previously known from British Columbia. Not previously known from the Peace Lowland.
Global Habitat: Marshes, shores and wet meadows.
Local Habitat: In marshes and bogs.
TEM Habitat Type: Observed in the BWBSmw1 SE, WS, and AMy:ap habitat types.
Local Occurrence: Found in rare plant transects RP19, RP20, RP21, and RP22.
Notes: This species could easily be confused with the more widespread Rumex occidentalis . North American populations of this species have often been called R. orbicularis . Though this species is currently known in British Columbia from the four populations herein reported, it could quickly become more widely known in northeastern portions of the province once it is sought. It does not appear in the Illustrated Flora of British Columbia and this species is known only in southern portions of Alberta.
References: Mosyakin 2005; NatureServe Explorer 2008.
Salix petiolaris Sm.
English Name: Meadow willow.
Description: A tall shrub with several, flexible stems; twigs yellowish, with sparse to moderately dense hairs; leaves narrow, bamboo-like, toothed along the margins, the lower surface with a waxy coating, with a few silky white and copper-coloured hairs or hairs absent, the upper surface medium to dark green, smooth or hairless, often shiny; flowers in dense spikes, the petals and sepals absent, formed of just a woolly ovary with a dark bract at the base, the inflorescences produced as the leaves emerge or shortly before, held at the tips of leafy twigs near the branch tips.
Global Range: Boreal and northern temperate regions of central and eastern North America.
Ranking: G5 S2S3; Blue-listed.
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Significance: Previously known in the Peace Lowland.
Global Habitat: Various open sites with moist soil.
Local Habitat: Found in the forest clearing along an old logging road.
TEM Habitat Type: Observed in a roadside habitat
Local Occurrence: Found in rare plant transect RP21.
References: Douglas et al. 2000; British Columbia Ministry of Environment 2008.
Salix serissima (L.H. Bailey) Fernald
English Name: Autumn willow.
Description: A large shrub with numerous, flexible stems; twigs bright yellow-brown or red- brown, hairless; leaves variable in shape, generally elliptic or lance-shaped, the lower surface sometimes with a waxy coating, hairless, upper surface very glossy, the margins toothed; flowers in dense spikes, the petals and sepals absent, formed of just a hairless, red-brown ovary with a light-coloured, deciduous bract at the base, the inflorescences produced in summer, fruits maturing as the leaves turn colour in autumn.
Global Range: Across boreal and north temperate regions of central and eastern North America.
Ranking: G4 S2S3; Blue-listed.
Significance: Previously known in the Peace Lowland.
Global Habitat: Fens and bogs, where calcareous.
Local Habitat: Transition between marsh and muskeg forest habitats.
TEM Habitat Type: Recorded within a BWBSmw1 TS habitat type, but the population was on the margins of this habitat. The TS should not be used to predict occurrences of this species.
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Local Occurrence: Found in rare plant transect RP06.
References: Fernald 1950; Douglas et al. 2000; British Columbia Ministry of Environment 2008.
Scolochloa festucacea (Willd.) Link
English Name: Rivergrass.
Description: A tall grass with stems arising singly from long rhizomes; leaves long, flat, 5-10 mm wide, roughened on the upper surface, dark green; flowers arrayed in large, dense but open panicles.
Global Range: Scattered around the southern boreal and temperate Northern Hemisphere; in North America, it is found mostly in the western and central southern boreal forest and Canadian Prairies.
Ranking: G5 S2; Red-listed.
Significance: Previously known in the Peace Lowland.
Global Habitat: Marshes and in shallow water along lake shores.
Local Habitat: Open marsh and marshy clearings in forest.
TEM Habitat Type: Observed in the SE wetland type. However, this habitat definition encompasses many wetland types and is not specifically tied to occurrences of S. festucacea .
Local Occurrence: Found in rare plant transects RP05 and RP06.
Notes: This species has been thought by some to be introduced in North America, but this is a view from the U.S., where the plant is rare and often occurs in disturbed lakeshore habitats. Its distribution in Canada and the U.S. Dakotas is clearly that of a native species, and within that region, it grows mostly in wild habitats. Scolochloa is a monotypic genus, that is, it has only this one species worldwide.
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References: Douglas et al. 2001b; Barkworth 2008; British Columbia Ministry of Environment 2008.
Sphenopholis intermedia (Rydb.) Rydb.
English Name: Slender wedgegrass.
Description: A clump-forming grass with abundant leaves crowded around the base; leaves flat or curled inward from the sides, deep green; inflorescences plume-like, with a few gaps with the bare stem showing through, but otherwise densely packed with florets, often nodding; flowers pale green.
Global Range: Throughout most of temperate and boreal North America, but nearly absent from Pacific coastal regions, most common in the east.
Ranking: G5 S3; Blue-listed. This ranking should be G4 S2S3. This species depends on vulnerable habitats.
Significance: Previously known from the Peace Lowland.
Global Habitat: Wet to damp sites in full sun, that have high clay content in the soil and where desiccation occurs late in the season.
Local Habitat: Open-water slough margins on silty, cobbly ground, and on muddy outflow from a spring adjacent to an open-water slough.
TEM Habitat Type: Observed in the ‘Active Channel’ habitat type, though the actual habitat of this plant is much more specific than that.
Local Occurrence: Found in rare plant transects RP08e and RP11w.
Notes: This is a very attractive grass, and one that is declining throughout its range. It is declining particularly in the western U.S. and southwest Canada, where it is being displaced by aggressive non-native plants, especially Phalaris arundinacea (reed canary grass).
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References: Douglas et al. 2001b; Daniel 2008; British Columbia Ministry of Environment 2008.
Symphyotrichum puniceum L. var. puniceum (syn. Aster puniceus var. puniceus )
English Name: Purple-stemmed aster.
Description: A medium-sized perennial herbaceous plant; stems purplish, shaggy with spreading hairs; leaves all on the stems, none basal at flowering time, their bases flanged around the stem, lance shaped, shaggy-hairy, spreading out at wide angles; flowers in daisy-like heads, with purple ray flowers in a ring around the yellow disc flowers.
Global Range: Eastern and central temperate to southern boreal North America, scattered into the western boreal to northern British Columbia.
Ranking: G5T5 S2S3; Blue-listed.
Significance: Previously known in the Peace Lowland, which, with the Liard River drainage, is its only range in British Columbia.
Global Habitat: A wide variety of wetland and forest-edge habitats.
Local Habitat: Various open sites with moist, peaty soil.
TEM Habitat Type: Observed in the BWBSmw1 AMy:ap, SE, SW, and TS habitat types.
Local Occurrence: Found in rare plant transects RP3, RP19, RP20, RP23, RP25, and RP26.
References: Brouillet et al. 2006; Douglas et al. 1998a; British Columbia Ministry of Environment 2008.
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Trichophorum pumilum (Vahl.) Schintz & Thell.
English Name: Dwarf clubrush.
Description: A tufted grass-like plant with slender, round stems; leaves reduced in size and inconspicuous; flowers lacking petals and sepals, the inflorescence reduced to merely a few small, inconspicuous bracts sheathing the single-seeded fruits.
Global Range: Boreal western North America, Europe and central Asia, also in Quebec.
Ranking: G5 S2S3; Blue-listed.
Significance: Not previously known in the Peace Lowland.
Global Habitat: Strongly calcareous muskeg forest, bogs, riverbanks, springs and marl fens.
Local Habitat: One of the dominant species around open marl fens, where forming tussocks along with Carex viridula and Muhlenbergia glomerata .
TEM Habitat Type: Observed in a wetland type (marl fen) for which there is no corresponding type in the classification of British Columbia wetlands (MacKenzie & Moran 2004).
Local Occurrence: Found in rare plant transect RP05.
References: Crins 2002; Douglas et al. 2001a; British Columbia Ministry of Environment 2008.
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Viola renifolia A. Gray var. nov .
English Name: No English name exists.
Description: A perennial herbaceous plant growing from a slender, creeping rhizome; leaves all growing directly from the rhizome, kidney-shaped to broadly heart-shaped, dark green; flowers not observed, probably white; fruits single at the tip of a leafless stalk, the fruit wall pale yellow- green with purple spots; seeds pale tan, with a small, white waxy mass (caruncle) at the narrower end.
Global Range: Thus far known only from the project area. It is unlikely, given the extent of potential habitat across the western North American southern boreal region, that this variety is endemic to the Peace Lowland. Herbarium study is needed to see if it has been overlooked.
Ranking: Unknown at this time; the species, inclusive, is ranked G5.
Significance: Previously undescribed .
Global Habitat: Moist, lightly shaded sites in a variety of habitats.
Local Habitat: Same as for the global habitat.
TEM Habitat Type: Observed in the BWBSmw1 AM and SW habitat types.
Local Occurrence: Found in rare plant transects RP03, RP04, and RP06.
Notes: This is clearly Viola renifolia , but differs from typical widespread V. renifolia in having a spotted, pale yellow-green fruit as opposed to an unspotted pale brown fruit. The seeds are pale tan and have a small, inconspicuous caruncle while typical V. renifolia has seeds mottled pale tan and darker brown and have a conspicuous caruncle.
References: Fernald 1950; Little 2008.
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Appendix 9a. Bat capture sampling effort.
Table 9a-1. Summary of bat sampling effort and capture rates for each sampling site in the Peace River Corridor from 2005, 2006, and 2008. Number Number of nights of bats Net Net Bats per Sample Period Sample Station sampled captured hours nights Net night Blackfoot 1 0 9.0 5.5 0.00 Cache Creek 1 4 17.5 9 0.44 Farrell Creek 1 1 16.2 9 0.11 Gravel Pit 1 1 1 10.0 7.5 0.13 Aug 22 -29, 1 2005 Halfway River 1 0 9.3 7.5 0.00 Lynx Creek 1 1 16.0 9 0.11 Peace Island Channel 1 0 4.5 6 0.00 Peace Island Wetland 1 1 9.8 5.5 0.18 Sample Period Total 8 8 92.3 59 0.14 Alces River 4 4 19.6 17.5 0.23 Cache Creek 2 6 26.2 20.5 0.29 Jul 10-17, 2006 Johnson Backchannel 1 0 13.8 11.5 0.00 Peace Island Wetland 1 2 4 18.1 16.5 0.24 Sample Period Total 7 14 77.7 66 0.21 Cache Creek 1 3 6 18.3 20.5 0.29 Jul 8 - Aug 4, Farrell Creek 1 2 5 12.1 13.5 0.37 2006 Lynx Creek 2 2 12.0 20.5 0.10 Sample Period Total 7 13 42.4 54.5 0.24 Alces River 1 1 11.5 5.0 0.20 Cache Creek 3 9 57.2 21.0 0.43 Cottonwood Campsite 1 8 30.0 10.0 0.80 Farrell Creek 2 3 49 69.3 20.0 2.45 Limestone Campsite 1 0 24.9 6.0 0.00 Jul 15 – 23, 2008 Lynx Creek 1 2 24.5 9.0 0.22 Moberly Backchannel 1 0 20 10.0 0.00 Watson Slough 1 0 12.3 8.5 0.00 Sample Period Total 12 69 249.7 89.5 0.77 Sample period excluding captures at Farrell Creek night roost 9 20 180.4 69.5 0.29
Total 34 104 462.1 269 0.39 Total excluding sampling at night roost 31 55 392.8 249 0.22 Total excluding night roost and nights with poor conditions 27 49 345.6 207 0.24 1indicates sample stations with inclement weather conditions; 2sampling at night roost.
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Appendix 9b. Bat acoustic sampling
Table 9b-1. The total number of passes and buzzes identified for the Myotis and big bat species groups, by sampling session, using a 2-hour sample period. Session Myotis bats Big bats All bats All All Pass Buzz All calls Pass Buzz Pass Buzz calls calls 1: July 1425 82 1507 417 13 430 1842 95 1937 2: August 323 20 343 128 3 131 451 23 474 Total 1748 102 1850 545 16 561 2293 118 2411
500 120 a) Myotis b) Big bats 400 100 80 300 60 200 40 100 Number of calls Number of calls 20
0 0
OW = 7 RI = 8 BK = 5 OW = 7 RI = 8 BK = 5 Riparian habitat group Riparian habitat group
(Sample sizes for each group are given on the X-axis)
Figure 9b-1. Box plots for the number of calls recorded in 2 hours from a) Myotis and b) big bats at non-forested/ riparian habitat types.
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100%
5 4 4 2 2 75% 4 6 50% 5 4
25% 4 4 2 Percentage of sites Percentage
3 3 1 2 0% DRc/d MEc/d SO MOc: other Fm02 MOd: other Grouped habitat type
(Sample sizes are shown for each combination of structural stage).
Figure 9b-2. The percentage of acoustic sampling sites in each structural stage, within each forested habitat group
200
150
100
50 Number of calls
0
stage 4 = 9 stage 5 = 15 stage 6 = 13 Structural stage
(Sample sizes for each group are given on the X-axis)
Figure 9b-3. Activity of all bats in forested sites in structural stages 4, 5, and 6.
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140 Session 1 120 Session 2
100
80
60 Number of calls
40
20 Farrell Watson Site
Figure 9b-4. Bat activity at two sites, Farrell Ck and Watson Slough, which were sampled in Session 1 in mid-July and Session 2 in late August 2008.
Appendix 9c. Radio-telemetry.
Table. 9c-1. Species, gender, reproductive condition, duration of monitoring, number of roosts found and roost area for bats with 3 or more roosts, for bats radio-tagged in the Peace River Corridor in 2006 and 2008. Reproductive Days Minimum # Roost Year ID Species Sex condition tracked roosts used area (ha) 2006 BIG Big brown bat M Not-reproductive 1 14 3 3.3 2006 HER Hoary bat F Reproductive – L 2 13 1 2006 CAC Hoary bat M Not-reproductive 0 0 2006 LIZ Little brown myotis F Reproductive – P 3 17 1 2006 NOR Little brown myotis F Reproductive - L 10 4 0.5 2006 FAR Little brown myotis F Reproductive - L 14 3 12.4 2006 FAW Little brown myotis F Not-reproductive 7 2 2006 WIL Little brown myotis M Not-reproductive 12 3 0.1 2006 LYN Little brown myotis M Not-reproductive 15 1 2006 BUN Northern myotis F Reproductive - L 17 1 2006 CLO Silver-haired bat F Reproductive - L 17 4 1.1
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Reproductive Days Minimum # Roost Year ID Species Sex condition tracked roosts used area (ha) 2006 FRO Silver-haired bat F Reproductive - P 0 0 2008 SWE Big brown bat F Reproductive - L 14 5 3.6 2008 GOO Big brown bat M Not-reproductive 14 3 21.9 2008 BET Little brown myotis F Reproductive - L 11 6 29.2 2008 OPA Little brown myotis F Reproductive - L 2 1 2008 RUB Little brown myotis F Reproductive - L 9 3 0.2 2008 LUC Little brown myotis F Reproductive - L 12 2 2008 BAB Little brown myotis F Reproductive - P 0 0 2008 MOL Little brown myotis F Reproductive - P 0 0 2008 ALN Little brown myotis M Not-reproductive 7 1 2008 PRI Long-legged myotis F Reproductive - P 0 0 2008 VIC Long-legged myotis F Reproductive - P 0 0 2008 SAL Northern myotis F Reproductive - P 0 0 2008 LIL Silver-haired bat F Reproductive - P 13 3 0.2 1Apparently reproductively capable, not currently in a state of potency, 2Reproductive – L : lactating 3Reproductive – P : pregnant
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Appendix 10a. Number of waterfowl surveys completed in the Peace River Corridor study area in 2008. Site C Transect Stratum May June July Aug. Sept. Oct. Total Reservoir Label River Partial All 1 1 1 1 1 1 6 River Partial 8 19 2 29 Segment Yes RB1 1 1 1 1 2 6 Yes RB10 1 2 1 2 2 8 Yes RB11 1 2 1 4 Yes RB12 1 1 1 2 5 Yes RB13 1 1 Yes RB14 1 1 1 3 3 9 No RB15 1 1 2 No RB16 1 1 1 1 4 No RB17 1 2 1 3 7 No RB18 1 2 2 2 2 9 No RB19 1 1 2 1 5 Yes RB2 1 1 1 1 4 No RB20 1 1 1 1 4 No RB21 1 1 2 No RB22 1 1 1 3 Yes RB23 1 1 2 4 Backchannel No RB24 1 1 1 3 No RB25 1 1 No RB26 1 1 Yes RB27 1 1 1 1 4 Yes RB28 1 1 1 3 Yes RB3 1 1 1 2 5 Yes RB30 1 1 2 Yes RB31 1 1 2 Yes RB32 1 1 2 Yes RB33 1 1 2 Yes RB34 1 1 No RB35 1 1 2 Yes RB5 1 1 1 2 5 Yes RB6 1 1 1 1 2 6 Yes RB8 1 1 1 3 Yes RB9 1 3 1 1 1 2 9 No 7-1 1 1 Yes WAT 2 4 2 2 10 Wetland No WBF 1 1 No WR 1 1 No WS 1 1 2 Total 15 33 25 28 35 42 178
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Appendix 10b. Number of waterfowl surveys completed in the transmission line study area in 2008. Transect Stratum May June July Aug. Sept. Oct. Total Label BL 1 1 3 3 8 MK 2 2 4 Lake TC_44 3 1 4 WoL 1 1 2 Wetland TC_10 1 1 TC_11 1 1 TC_12 1 1 TC_13 1 1 TC_14 1 1 TC_15 1 1 TC_16 1 1 TC_17 1 1 TC_18 1 1 TC_19 1 1 TC_1a 1 1 TC_1b 1 1 TC_2 1 1 TC_20 2 2 1 5 TC_21 1 1 TC_22 1 1 TC_23 1 1 1 3 TC_24 1 1 TC_25 1 1 TC_26 1 1 2 TC_27 1 1 1 3 TC_28 1 1 TC_29 1 1 TC_3 1 1 TC_30 1 1 TC_31 1 1 TC_32 1 1 TC_33 1 1 TC_35 1 1 TC_36 2 2 TC_37 1 1 TC_38 1 1 1 3 TC_4 1 1
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Transect Stratum May June July Aug. Sept. Oct. Total Label TC_40 2 1 1 4 TC_41 1 1 TC_42 2 1 1 4 TC_43 1 1 2 TC_5 1 1 TC_6 1 1 TC_7 1 1 2 TC_8 1 1 TC_9 2 3 1 1 7 TC_Mrsh 1 1 Total 32 20 5 5 15 10 87
Appendix 10c. Number of waterfowl and water-associated birds detected during waterfowl surveys in 2008, in the PRC and TL study areas. English Name Scientific Name BC Status PCR* SCR* TL Total American Coot Fulica americana Yellow 13 13 268 281 American Wigeon Anas americana Yellow 337 305 77 414 Arctic Tern Sterna paradisaea Yellow 1 1 Barrow's Goldeneye Bucephala islandica Yellow 6 6 8 14 Belted Kingfisher Megaceryle alcyon Yellow 79 47 79 Black Tern Chlidonias niger Yellow 5 5 24 29 Blue-winged Teal Anas discors Yellow 51 44 18 69 Bonaparte's Gull Larus philadelphia Yellow 773 768 2 775 Bufflehead Bucephala albeola Yellow 52 42 117 169 Cackling Goose Branta hutchinsii Yellow 21 21 California Gull Larus californicus Blue 8 8 8 Canada Goose Branta canadensis Yellow 5190 1852 5 5195 Canvasback Aythya valisineria Yellow 16 16 Cinnamon Teal Anas cyanoptera Yellow 1 1 1 Common Goldeneye Bucephala clangula Yellow 252 178 37 289 Common Loon Gavia immer Yellow 46 40 4 50 Common Merganser Mergus merganser Yellow 508 288 508 Common Tern Sterna hirundo Yellow 1 1 1 Double-crested Cormorant Phalacrocorax auritus Blue 1 1 Franklin's Gull Larus pipixcan Yellow 5716 4559 5716 Gadwall Anas strepera Yellow 10 8 10 Glaucous Gull Larus hyperboreus Yellow 1 1 Great Blue Heron Ardea herodias Blue 1 1 Greater Scaup Aythya marila Yellow 3 3 Greater White-fronted Goose Anser albifrons Yellow 2 2 2 Greater Yellowlegs Tringa melanoleuca Yellow 3 3 3 Green-winged Teal Anas crecca Yellow 247 200 43 290 Harlequin Duck Histrionicus histrionicus Yellow 1 1 1 July 2009 -349-
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English Name Scientific Name BC Status PCR* SCR* TL Total Herring Gull Larus argentatus Yellow 142 119 1 143 Hooded Merganser Lophodytes cucullatus Yellow 1 7 8 Killdeer Charadrius vociferus Yellow 20 2 20 Least Sandpiper Calidris minutilla Yellow 2 2 2 Lesser Scaup Aythya affinis Yellow 16 13 161 177 Lesser Yellowlegs Tringa flavipes Yellow 2 2 8 10 Long-billed Dowitcher Limnodromus scolopaceus Yellow 3 3 Long-tailed Duck Clangula hyemalis Unknown 7 7 3 10 Mallard Anas platyrhynchos Yellow 2370 1080 455 2825 Mew Gull Larus canus Yellow 2 1 2 Northern Pintail Anas acuta Yellow 118 75 14 132 Northern Shoveller Anas clypeata Yellow 58 39 12 70 Pacific Loon Gavia pacifica Yellow 9 4 9 Pectoral Sandpiper Calidris melanotos Yellow 8 8 Red-throated Loon Gavia stellata Yellow 4 4 4 Ring-billed Gull Larus delawarensis Yellow 1706 1560 1706 Ring-necked Duck Aythya collaris Yellow 100 100 366 466 Ruddy Duck Oxyura jamaicensis Yellow 3 2 5 Sabine's Gull Xema sabini Yellow 2 2 1 3 Sandhill Crane Grus canadensis Blue 37 37 Solitary Sandpiper Tringa solitaria Yellow 15 15 Sora Porzana carolina Yellow 9 9 Spotted Sandpiper Actitis macularius Yellow 670 450 670 Stilt Sandpiper Calidris himantopus Yellow 1 1 1 Surf Scoter Melanitta perspicillata Blue 1 3 4 Trumpeter Swan Cygnus buccinator Yellow 141 104 31 172 Unknown Duck 156 134 204 360 Unknown Goldeneye 44 40 44 Unknown Gull 203 105 203 Unknown Teal 6 3 6 Upland Sandpiper Bartramia longicauda Red 1 1 White-winged Scoter Melanitta fusca Yellow 2 2 Wilson's Snipe Gallinago delicata Yellow 1 1 9 10 Total 19147 12219 1938 21085 *PCR includes species that were detected in the SCR, and is a total count for the study area.
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Appendix 10d. Number of waterfowl and water-associated bird species detected incidentally during surveys in 2008. English Name Scientific Name BC Status PRC TL Total American Coot Fulica americana Yellow 15 5 20 American Wigeon Anas americana Yellow 80 11 91 Barrow's Goldeneye Bucephala islandica Yellow 1 1 Black Tern Chlidonias niger Yellow 16 16 Blue-winged Teal Anas discors Yellow 59 10 69 Bonaparte's Gull Larus philadelphia Yellow 24 24 Bufflehead Bucephala albeola Yellow 45 4 49 Canada Goose Branta canadensis Yellow 828 15 843 Cinnamon Teal Anas cyanoptera Yellow 1 1 Common Goldeneye Bucephala clangula Yellow 51 51 Common Loon Gavia immer Yellow 3 7 10 Common Merganser Mergus merganser Yellow 132 132 Double-crested Cormorant Phalacrocorax auritus Blue 1 1 Franklin's Gull Larus pipixcan Yellow 1078 1078 Gadwall Anas strepera Yellow 1 1 Great Blue Heron Ardea herodias Blue 1 1 Green-winged Teal Anas crecca Yellow 43 3 46 Herring Gull Larus argentatus Yellow 36 36 Killdeer Charadrius vociferus Yellow 9 9 Lesser Yellowlegs Tringa flavipes Yellow 5 1 6 Mallard Anas platyrhynchos Yellow 140 14 154 Marbled Godwit Limosa fedoa Yellow 1 1 Northern Pintail Anas acuta Yellow 2 2 Northern Shoveller Anas clypeata Yellow 7 2 9 Pectoral Sandpiper Calidris melanotos Yellow 5 5 Pied-billed Grebe Podilymbus podiceps Yellow 3 3 Red-necked Grebe Podiceps grisegena Yellow 4 4 Ring-billed Gull Larus delawarensis Yellow 199 199 Ruddy Duck Oxyura jamaicensis Yellow 8 3 11 Sandhill Crane Grus canadensis Blue 13 2 15 Solitary Sandpiper Tringa solitaria Yellow 9 12 21 Sora Porzana carolina Yellow 52 22 74 Spotted Sandpiper Actitis macularius Yellow 64 1 65 Trumpeter Swan Cygnus buccinator Yellow 13 7 20 Unknown Duck 139 36 175 Unknown Gull 44 44 Upland Sandpiper Bartramia longicauda Red 2 2 Aechmophorus Western Grebe Red 5 5 occidentalis Wilson's Phalarope Phalaropus tricolor Yellow 6 6 Wilson's Snipe Gallinago delicata Yellow 64 41 105
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English Name Scientific Name BC Status PRC TL Total Total 3185 220 3405
Appendix 10e. Number of waterfowl and water-associated birds observed in each stratum in 2008, in the PRC study area. English Name Backchannel River Wetland Total American Coot 13 13 American Wigeon 103 227 7 337 Arctic Tern 1 1 Barrow's Goldeneye 6 6 Belted Kingfisher 33 46 79 Black Tern 5 5 Blue-winged Teal 2 41 8 51 Bonaparte's Gull 16 757 773 Bufflehead 9 41 2 52 Cackling Goose 20 1 21 California Gull 8 8 Canada Goose 1736 3453 1 5190 Cinnamon Teal 1 0 1 Common Goldeneye 123 127 2 252 Common Loon 3 43 46 Common Merganser 117 391 508 Common Tern 1 1 Franklin's Gull 500 5216 5716 Gadwall 8 2 10 Great Blue Heron 1 1 Greater White-fronted 2 2 Goose Greater Yellowlegs 1 2 3 Green-winged Teal 100 121 26 247 Harlequin Duck 1 1 Herring Gull 4 138 142 Hooded Merganser 1 1 Killdeer 4 16 20 Least Sandpiper 2 2 Lesser Scaup 9 7 16 Lesser Yellowlegs 2 2 Long-tailed Duck 7 7 Mallard 968 1371 31 2370 Mew Gull 2 2 Northern Pintail 83 26 9 118 Northern Shoveller 5 49 4 58 Pacific Loon 9 9 Red-throated Loon 4 4 Ring-billed Gull 31 1675 1706 Ring-necked Duck 100 0 100
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English Name Backchannel River Wetland Total Ruddy Duck 3 3 Sabine's Gull 2 2 Sandhill Crane 37 37 Spotted Sandpiper 136 534 670 Stilt Sandpiper 1 1 Surf Scoter 1 1 Trumpeter Swan 51 90 141 Unknown Duck 15 66 75 156 Unknown Goldeneye 44 44 Unknown Gull 40 163 203 Unknown Teal 4 2 6 Upland Sandpiper 1 1 Wilson's Snipe 1 1 Total 4218 14742 187 19147
Appendix 10f. Number of waterfowl and water-associated birds observed by stratum in 2008, in the TL study area. English Name Lake Wetland Total American Coot 268 268 American Wigeon 19 58 77 Barrow's Goldeneye 8 8 Black Tern 24 24 Blue-winged Teal 3 15 18 Bonaparte's Gull 2 2 Bufflehead 109 8 117 Canada Goose 5 5 Canvasback 5 11 16 Common Goldeneye 36 1 37 Common Loon 3 1 4 Double-crested Cormorant 1 1 Glaucous Gull 1 1 Greater Scaup 3 3 Green-winged Teal 31 12 43 Herring Gull 1 1 Hooded Merganser 4 3 7 Lesser Scaup 75 86 161 Lesser Yellowlegs 3 5 8 Long-billed Dowitcher 3 3 Long-tailed Duck 3 3 Mallard 417 38 455 Northern Pintail 13 1 14 Northern Shoveller 6 6 12 Pectoral Sandpiper 8 8 Ring-necked Duck 43 323 366 Ruddy Duck 2 2 July 2009 -353-
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English Name Lake Wetland Total Sabine's Gull 1 1 Solitary Sandpiper 1 14 15 Sora 4 5 9 Surf Scoter 3 3 Trumpeter Swan 19 12 31 Unknown Duck 204 204 White-winged Scoter 2 2 Wilson's Snipe 9 9 Total 1318 620 1938
Appendix 10g. Summary of waterfowl and water-associated species occurrence in the Peace River Corridor during surveys completed in 2005, 2006 and 2008*. Common Name Occurrence Breeding Migrant April May June July Aug. Sept. Oct.
American Coot summer visitant y y X X X X X X American Dipper vagrant n n U U American Wigeon summer visitant y y X X X X X X X Arctic Tern transient n n U Barrow's Goldeneye summer visitant p y X X X Black Tern summer visitant n y X X X Black-bellied Plover transient n y U Blue-winged Teal summer visitant p y X X X X X X Bonaparte's Gull summer visitant n y X X X X X Bufflehead summer visitant y y X X X X X X X Cackling Goose transient n y U California Gull summer visitant n y X X X X X X Canada Goose summer visitant y y X X X X X X X Caspian Tern transient n y U Cinnamon Teal vagrant n y U U Common Goldeneye summer visitant y y X X X X X X X Common Loon summer visitant p y X X X X X X X Common Merganser summer visitant y y X X X X X X X Common Tern vagrant n n U Franklin's Gull summer visitant n y X X X X X X Gadwall summer visitant p p X X X X Great Blue Heron vagrant n y U U U Greater Scaup transient n y U U Greater White-fronted transient n y U Goose Greater Yellowlegs transient n y X X X X Green-winged Teal summer visitant y y X X X X X X X
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Common Name Occurrence Breeding Migrant April May June July Aug. Sept. Oct.
Harlequin Duck transient n y U Herring Gull summer visitant n y X X X X X Hooded Merganser summer visitant p y X X X X Horned Grebe summer visitant n p U U Killdeer summer visitant y y X X X X X X X Least Sandpiper transient n y U U Lesser Scaup summer visitant y y X X X X Lesser Yellowlegs summer visitant p y X X X Long-tailed Duck transient n y U Mallard summer visitant y y X X X X X X X Marbled Godwit transient n y U Mew Gull transient n y U U Northern Pintail summer visitant p y X X X X X X Northern Shoveller summer visitant n y X X X X X Pacific Loon transient n y X X Pectoral Sandpiper transient n y U Red-necked Grebe summer visitant n y X X X X X Red-throated Loon transient n y U Ring-billed Gull summer visitant n y X X X X X X X Ring-necked Duck summer visitant p y X X X X X Ruddy Duck summer visitant y y X X Sabine's Gull transient n y U U Sandhill Crane transient n y U U Snow Goose transient n y U Solitary Sandpiper summer visitant p y X X X X Sora summer visitant y y U U Spotted Sandpiper summer visitant y p X X X X X X Stilt Sandpiper transient n y U Surf Scoter transient n y X X Trumpeter Swan summer visitant p y X X X X X X Upland Sandpiper summer visitant y y U U Western Grebe transient n n U White-winged Scoter transient n y U U Wilson’s Phalarope summer visitant y y U U Wilson's Snipe summer visitant y y X X X X X X *2006 and 2008, includes incidental observations; n-no, y-yes, p-probable, X-species detected, U-few observations recorded in one or more years.
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Appendix 11. Ungulate block counts from the three aerial censuses (1991, 2006, 2009). # of Moose # of Deer # of Elk Block # Area (ha) 2009 Search Time (min) 1991 2006 2009 1991 2006 2009 1991 2006 2009 Peace River valley bottom upstream of the Moberly River (Stratum 2) 1 1072 25 14 6 15 5 3 4 0 0 20 2 1536 40 25 18 20 21 2 32 5 23 44 3 2075 55 35 11 40 33 53 70 0 56 11 4 1838 58 24 20 22 31 19 43 2 26 15 5 1505 58 10 3 3 13 7 36 0 0 0 6 1988 53 6 8 8 78 30 18 0 0 8 Subtotals 289 114 66 108 181 114 203 7 105 98 Peace River valley bottom downstream of the Moberly River (Stratum 4) 30 1726 52 12 10 9 31 1605 42 36 3 11 32 1727 45 10 12 10 2 5 6 33 2313 75 19 30 10 19 20 35 Subtotals 214 0 29 90 0 20 34 0 25 61 South aspect breaks (Stratum 1) 78* 696 36 8 (80) 78 19 9 571 15 1 3 184 74 0 1 10 286 20 2 (241) 121 34 11 746 27 25 7 70 35 0 84 12 486 18 -ns- -ns- 293 -ns- -ns- 0 -ns- -ns- 13 492 21 8 17 4 160 97 56 22 81 33 14 897 7 -ns- -ns- 121 -ns- -ns- 0 -ns- -ns- 15 587 25 13 12 260 135 0 73 16 567 17 6 2 72 27 38 48 55 17 423 21 4 4 248 63 0 37 18 408 27 7 6 99 64 16 8 19 279 27 7 15 64 10 50 0 20 530 17 114 19 34 413 17 4 74 0 35 978 29 10 126 10 36 958 46 17 248 0 37 572 23 15 12 225 152 14 0 41 886 11 84 0 50** 753 31 9 9 99 149 0 22 Subtotals 382 75 90 115 1444 701 1423 91 159 376 North aspect breaks (Stratum 3) 22 601 14 0 52 20 0 50 23 313 10 1 0 2 24 487 8 0 0 25 669 20 9 8 3 July 2009 -356-
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# of Moose # of Deer # of Elk Block # Area (ha) 2009 Search Time (min) 1991 2006 2009 1991 2006 2009 1991 2006 2009 26 590 9 5 35 9 1 0 27 596 35 1 1 18 8 0 3 28 613 8 3 9 1 0 0 29 598 21 3 0 5 44 987 30 13 50 0 48 779 3 11 0 51 842 35 3 13 10 Subtotals 151 39 12 30 96 39 99 1 0 73 *Blocks 7 and 8 were combined in 2009; ( ) MOE count Jan 28/91; -ns- no longer suitable; **Block 50 was moved from Stratum 3 to Stratum 1 in 2009.
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Appendix 12. Summary of percent occurrence of TEM habitat units (Appendix 3a) and structural stage (Appendix 3b) in the TEM mapped area. Structural Stage Mapcode Total n/a 1-bare 2-herb 3-shrub 4-pole 5-young 6-mature 7-old AM 0.0% 0.0% 0.0% 0.2% 0.4% 2.3% 2.1% 0.0% 5.0% AM:ap 0.0% 0.0% 0.0% 3.2% 8.9% 14.9% 3.7% 0.0% 30.7% AS 0.0% 0.0% 0.0% 3.0% 0.0% 0.0% 0.0% 0.0% 3.1% BL 0.0% 0.0% 0.0% 0.0% 0.1% 0.4% 0.3% 0.0% 0.8% BL:al 0.0% 0.0% 0.0% 0.2% 0.2% 0.5% 0.1% 0.0% 1.1% BT 0.0% 0.0% 0.0% 0.1% 0.4% 0.3% 0.4% 0.0% 1.2% CB 0.0% 1.7% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 1.7% CF 0.0% 0.0% 12.7% 0.5% 0.0% 0.0% 0.0% 0.0% 13.2% ES 0.0% 0.1% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.1% Fm02 0.0% 0.0% 0.0% 1.7% 0.3% 0.7% 1.3% 0.0% 4.1% GB 0.0% 1.4% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 1.4% GP 0.0% 0.2% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.2% LA 0.1% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.1% LL 0.0% 0.0% 0.0% 0.0% 0.2% 0.4% 0.3% 0.0% 0.9% LL:ak 0.0% 0.0% 0.0% 0.0% 0.4% 0.2% 0.0% 0.0% 0.6% MI 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% OW 0.1% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.1% PD 0.1% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.1% RE 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% RI 9.3% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 9.3% RN 0.1% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.1% RO 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% RW 0.3% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.3% RY 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% RZ 0.2% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.2% SC 0.0% 0.0% 0.0% 0.0% 0.0% 0.2% 0.3% 0.0% 0.5% SC:ab 0.0% 0.0% 0.0% 0.1% 0.1% 0.4% 0.4% 0.0% 1.0% SC:ep 0.0% 0.0% 0.0% 0.1% 0.2% 0.3% 0.1% 0.0% 0.6% SE 0.0% 0.0% 1.1% 0.0% 0.0% 0.0% 0.0% 0.0% 1.1% SH 0.0% 0.0% 0.0% 0.0% 0.1% 0.3% 1.4% 0.2% 2.0% SH:ac 0.0% 0.0% 0.0% 0.3% 0.1% 0.5% 0.6% 0.0% 1.6% SH:ep 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% SO 0.0% 0.0% 0.0% 0.1% 0.1% 1.1% 0.7% 0.1% 2.0% SW 0.0% 0.0% 0.0% 0.2% 0.3% 1.8% 0.9% 0.0% 3.3% SW:as 0.0% 0.0% 0.0% 0.4% 2.4% 3.6% 0.4% 0.0% 6.8% TS 0.0% 0.0% 0.0% 0.5% 0.1% 0.0% 0.0% 0.0% 0.6% UR 0.7% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.0% 0.7% WH 0.0% 0.0% 0.4% 1.2% 0.0% 0.0% 0.0% 0.0% 1.6% WS 0.0% 0.0% 0.0% 0.3% 0.0% 0.0% 0.0% 0.0% 0.3% WW 0.0% 0.0% 3.3% 0.3% 0.0% 0.0% 0.0% 0.0% 3.6% Total 11.0% 3.5% 17.6% 12.4% 14.2% 27.9% 13.0% 0.3% 100.0%
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PEACE RIVER SITE C HYDRO PROJECT
STAGE 2
BASELINE VEGETATION AND WILDLIFE REPORT
ADDENDUM #1
PREPARED FOR BC HYDRO SITE C PROJECT BY
KEYSTONE WILDLIFE RESEARCH LTD.
2008 - 2009
PEACE RIVER SITE C HYDRO PROJECT
STAGE 2
BASELINE VEGETATION AND WILDLIFE REPORT
ADDENDUM #1
Prepared for BC Hydro Site C Project by Keystone Wildlife Research Ltd. November 2009
Lead Author: Lauren Simpson and Keith Simpson
Contributors: Kyle Simpson (Ungulates) Melissa Flint (Fisher, Sheep)
Task Lead Review by: K. Anré McIntosh
Site C Hydro Project Vegetation and Wildlife Report Addendum #1
EXECUTIVE SUMMARY
As part of Stage 2, Project Definition and Consultation, BC Hydro engaged Keystone Wildlife Research Ltd. to complete wildlife and terrestrial studies in 2008 and 2009. The scope of the project was defined as collection of baseline data on wildlife species presence, distribution and abundance. The scope of study identified various taxa for which surveys were required, including raptors and herons (nest sites), amphibians, owls, breeding birds (warblers), butterflies, dragonflies, vascular plants, bats, waterfowl, ungulates, furbearers (fishers), Stone’s sheep and rare/sensitive ecosystems. This addendum summarizes the baseline data collected in 2008/09 for fishers, ungulates and Stone’s sheep and provides a review of furbearer presence in the area. The results for the remaining surveys were reported in the 2009 Stage 2 wildlife baseline report (Keystone Wildlife Research Ltd. 2009). This document is summary report and not a potential effects assessment.
Furbearers
A fisher hair-snagging study was undertaken in the Peace River Corridor between Hudson’s Hope and the potential Site C dam site (Moberly River). Forty-eight baited hair-snagging stations were established on the north and south banks of the Peace River Corridor and along three major tributaries (Moberly River, Cache Creek and Halfway River). Each station was visited 3 times to retrieve hair samples, with an average of 26 baited days between visits, for a total of 144 station visits. In total, 519 hair samples were collected and trap failure (defined as no samples retrieved) was estimated at 15%.
Nine fishers were detected from DNA analysis of the hair samples, including seven resident males, one apparently immature male and one individual that could not be sexed. No individuals were captured on both the north and south side of the river, suggesting that the open water of the river may be a barrier to movement. Commercial trapping of furbearers appears to have a major influence on fisher numbers in the study area, since male fishers were only present at expected densities in areas where trapping
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Site C Hydro Project Vegetation and Wildlife Report Addendum #1 effort and fisher harvests have been low. The presence of 7 resident adult males suggests that there may be 28 to 35 females in the vicinity of the study area, based on 4-5 females/male. Establishing the seasonal use and importance of the riparian areas as birthing habitat would require radio-monitoring of females captured in upland areas, adjacent to the potential Site C reservoir. Changing trapping practices to avoid incidental capture of fishers in marten traps could substantially increase the abundance of fishers in the Peace River area.
Existing furbearer data from trapline records were reviewed to document historical trends in harvest. Furbearers that are trapped in the Peace River valley and surrounding plateau include snowshoe hare (Lepus americana), red squirrel (Tamiasciurus hudsonicus), Canada lynx (Lynx canadensis), American marten (Martes americana), long-tailed weasel (Mustela frenata), ermine (Mustela erminea), muskrat (Ondatra zibethicus), fisher, river otter (Lontra canadensis), red fox (Vulpes vulpes), wolverine (Gulo gulo), wolf (Canis lupus), beaver (Castor canadensis), American mink (Neovison vison) and coyote (Canis latrans). Although catch varied by year, the species harvested in greatest numbers in the Peace River area from trapline records were red squirrel, followed by long-tailed weasel, marten, beaver and muskrat.
Stone’s Sheep
Field surveys for Stone’s sheep were scheduled in response to concerns expressed by the Blueberry River First Nation regarding the potential effects of the Site C project on sheep herds in the area. Winter snow track surveys and spring use surveys were completed to identify evidence of use by resident animals. Fifteen sites identified as potential winter range were traversed in March and June of 2009. No definitive evidence of sheep was observed during surveys, but due to the similarities between deer and sheep pellets (shape and size), DNA analysis was undertaken on pellets collected at apparently suitable sites to conclusively differentiate the species. DNA analysis confirmed that all pellets analysed were from deer. It is unlikely that Stone’s sheep are wintering in proximity to the Potential Site C reservoir, although they are occasionally
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Site C Hydro Project Vegetation and Wildlife Report Addendum #1 sighted in the Peace River valley. No additional surveys are recommended since Stone’s sheep are unlikely to be affected by the Site C project, should it proceed.
Ungulate Pellet Surveys
A local study area was identified within the Peace River Corridor to focus a detailed study on ungulate winter ranges that may be affected by construction of the potential Site C dam. Twelve pellet count transects were laid out in the study area to traverse both impact and no-impact (control) areas. Pellet transect surveys for relative abundance were completed according to RIC standards between June 12 and 17, 2009. Each transect was surveyed once, after the snow had melted. In total, 196 deer pellet groups, 224 moose pellet groups and 105 elk pellet groups were counted over a total distance of 35.7 km surveyed.
The results of pellet transects indicate that there is no difference in use between impact and control areas for elk and moose, but the control areas had higher pellet density for deer, than the impact areas. This result is based on a single winter of surveys, during which snow conditions were severe and animals were using critical winter habitat. Valuable habitat that may be affected by the potential Site C dam, should it proceed, include the warm aspect slopes for deer, the Moberly River breaks for elk and the valley bottom habitat for moose. Information on habitat use in other seasons is limited and radio-tracking of females may be required to determine the importance of the area during birthing seasons.
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Acknowledgements
We thank our field personnel Keith Simpson, T. Kyle Simpson, Melissa Flint, Chris Albrecht, Rick Hopkins, Kevin McGilloway, Kevin Hazelwood, Glen Heebner, Larry Davis and Clifford Davis. We thank Blueberry River First Nations for assisting with the Stone’s sheep work, namely, Shawn Davis, Hank Apassin, Norman Yahey, Wayne Yahey, Dean Davis and George Yahey. The BC Ministry of Environment provided trapline data for the study area, and allowed the use of their fisher hair-snagging boxes. Wildlife Genetics International completed the DNA analyses for fisher and sheep.
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List of Acronyms (standard list for Project)
BC CDC – British Columbia Conservation Data Centre
BCR – Bird Conservation Region
BWBSmw1 – Peace moist, warm Boreal White and Black Spruce (subzone variant)
BCCF – BC Conservation Framework
COSEWIC – Committee on the Status of Endangered Wildlife in Canada
CWS – Canadian Wildlife Service
DPC – Peace Forest District
FSJ – Fort St. John
GIF- Ground Inspection Form
MoE – BC Ministry of Environment
MU – Management Unit
NAD – North American Datum
PEL – Peace Lowlands (ecosection)
PRC – Peace River Corridor study area
PWWCP – Peace-Williston Wildlife Compensation Program
RIC – Resources Inventory Committee (now RISC)
RISC – Resources Inventory Standards Committee (formerly RIC)
SARA – Species at Risk Act
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SCR – potential Site C reservoir area
TEM – Terrestrial Ecosystem Mapping
TL – Transmission Line study area
UTM – Universal Transverse Mercator
VEC – Valued Ecosystem Component
WHA – Wildlife Habitat Area
WHR – Wildlife Habitat Ratings
Glossary
Anthropogenic – caused by activities of people
Blue List - species and subspecies of special concern (formerly vulnerable) in British Columbia
Coniferous – needle-leaved trees (e.g. white spruce)
Deciduous – broad-leaved trees (e.g. aspen, balsam poplar)
Incidental – refers to observations of a species made outside of formal surveys targeting that species
Indigenous species – species native to BC that have not been introduced from other areas of the world
Mesic – describes ecosystems having a well-balanced or moderate moisture supply, well-drained but usually moist throughout the growing season.
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Protected Area – federal and provincial parks and ecological reserves
Red List – includes taxa considered to have- or are candidates for- official Extirpated, Endangered or Threatened Status in BC
Seral – describes an intermediate stage found in ecological succession. In the Peace River Valley, it is often used to indicate a deciduous-dominated forest.
Structural stage – numerical scale used in Terrestrial Ecosystem Mapping describing forest structure and how it changes with age. Structural stages include 1 (non- vegetated/sparse), 2 (herb), 3 (shrub), 4 (pole-sapling), 5 (young forest), 6 (mature forest) and 7 (old forest).
Subnivean – under the snow
Taxa - Plural of ‘taxon’
Taxon – refers to either a species or subspecies unit
Taxonomy – the system of classification and naming of organisms
Tufa seep – terrestrial sedimentary rock, formed by the precipitation of carbonate minerals from ambient temperature water bodies.
Transect – a linear sampling unit
Ungulate – hoofed animal (deer, moose, elk and sheep)
Yellow List – includes taxa of wildlife and plants that are not considered to be at risk in BC.
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TABLE OF CONTENTS
1.0 INTRODUCTION ...... 1 1.1.1 Permits ...... 2 1.1.2 Assumptions ...... 2 2.0 SPECIES GROUP SUMMARIES...... 2
2.1 FURBEARERS...... 2 2.1.1 Introduction...... 3 2.1.2 Background ...... 4 2.1.3 Methods...... 11 2.1.4 Results...... 17 2.1.5 Recommendations...... 25
2.2 STONE’S SHEEP ...... 26
2.2.1 Introduction...... 27 2.2.2 Background ...... 27 2.2.3 Methods...... 29 2.2.4 Results...... 31 2.2.5 Summary ...... 39
2.3 UNGULATES...... 39 2.3.1 Introduction...... 39 2.3.2 Methods...... 39 2.3.3 Results...... 43 2.3.4 Summary ...... 50 3.0 REFERENCES ...... 51 4.0 PERSONAL COMMUNICATIONS...... 55 5.0 APPENDICES ...... 56
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LIST OF TABLES
Table 2.1.2. Summary of beaver surveys completed on the Peace River between 1976 and 2006...... 10 Table 2.1.4.1a. Duration of fisher DNA hair sampling in the Peace River Corridor...... 19 Table 2.1.4.1b. Numbers of hair samples collected at fisher stations between February 10 and April 1, 2009...... 20 Table 2.1.4.1c. Sample sites and sessions where individual fishers were identified...... 22 Table 2.1.4.1d. Fisher DNA captures (2009) compared with marten and fisher trapping data (1983-2007)...... 23 Table 2.1.4.1e. Relative abundance of furbearer tracks/50 m segment in the Moberly study area...... 25 Table 2.2.4.1a. Ungulate sign found in areas traversed in winter...... 35 Table 2.2.4.1b. Ungulate sign found in areas traversed in the spring...... 35 Table 2.2.4.2. Pellet and hair samples collected during spring transects...... 37 Table 2.2.4.3. Summary of respondents that have observed Stone’s sheep in the Region or in the Peace River Valley, grouped by recreation/occupation type...... 38 Table 2.3.2.1. Differentiating pellet sign...... 42 Table 2.3.3a. Numbers of ungulate pellet groups recorded during pellet count transects completed in 2009...... 46 Table 2.3.3b. Carrying capacity (animals per km2/year) by capability class (Demarchi et al. 1983)...... 47 Table 2.3.3c. Summary of major habitat types and habitat capability sampled along pellet transects in 2009...... 47 Table 2.3.3d. Relative ungulate densities (animals/km2/6 months ± 80% confidence intervals) by habitat group...... 49
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Table 2.3.3e. Relative proportion of habitats sampled in control and impact areas...... 49 Table 2.3.3f. Mean (m) and dispersion (k) values between the impact and control areas for each ungulate species...... 50
LIST OF FIGURES
Figure 2.1.3.2a. Fisher hair-snagging box...... 14 Figure 2.1.3.1b. Fisher hair-snagging station set-up...... 15 Figure 2.3.2.1. Ungulate pellet count station with five subplots...... 41 Figure 2.3.3. Winter (Nov 2008- Apr 2009) snow depths at the Fort St John airport (695 m)...... 44
LIST OF MAPS
Map 1. Fisher hair-snagging stations...... 18 Map 2. Stone’s sheep sampling sites...... 32 Map 3. Stone’s sheep winter ranges...... 33 Map 4. Ungulate transect locations...... 45
LIST OF APPENDICES
Appendix 1. Number of times hair sample stations were baited in the Peace River Corridor during 2008 - 2009...... 56 Appendix 2. Number of hair samples collected at each hair - snagging box in the Peace River Corridor during 2009...... 58 Appendix 3. Stone’s Sheep Questionnaire...... 60 Appendix 4. Deer pellet group statistical analysis...... 61 Appendix 5. Elk pellet group statistical analysis...... 63
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Site C Hydro Project Vegetation and Wildlife Report Addendum #1
1.0 INTRODUCTION
The 2008 field program was designed to update existing information and conduct new studies on wildlife and plant resources. Taxa identified in the scope of study as requiring surveys included butterflies, passerines (especially warblers), raptors/herons (nest sites), waterfowl, herptiles, plants, owls, ungulates, fisher (Martes pennanti) and bats. Stone’s sheep (Ovis dalli stonei) were added to the scope of work due to concerns expressed by First Nations. Assessment of some species required specialist knowledge, and all required that survey sites be located appropriately. This addendum report includes the survey results for the fisher hair- snagging, furbearer data review, ungulate pellet count, and Stone’s sheep surveys completed in 2009. These results were not reported in the Stage 2 baseline terrestrial vegetation and wildlife report (Keystone Wildlife Research Ltd. 2009) because the results of the DNA analyses were not available or field surveys were not complete by the final submission deadline of July 2009. Full details of the Stage 2 field program were reported in Keystone Wildlife Research Ltd. (2009).
The methodology used included a map-based evaluation of wildlife habitat suitability for focal species and targeted wildlife surveys for particular species/species groups. The focus of the surveys was on critical habitats for rare or endangered species. Information was collected in a form that will allow a future quantitative assessment of the potential effects of the Site C project in the Peace River area, should the project proceed to Stage 3.
The objectives of the 2008/2009 field program were to:
• Determine the presence, and relative abundance where possible, of target taxa within the study area;
• Provide information on wildlife and vegetation resources (for example, those used for cultural, food, recreational and traditional use purposes) important to First Nations and other stakeholders.
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1.1.1 Permits
Baiting of fisher hair-snagging stations with road-killed ungulates was carried out under permit FJ08-48888, which authorized Keystone to possess and dispose of roadkill and dead wildlife for scientific purposes.
1.1.2 Assumptions
Fieldwork was completed according to the following assumptions:
• Terrestrial Ecosystem Mapping (TEM) is an accurate representation of the study area;
• Habitat mapping based on the TEM will provide sufficient data to analyze and quantify the potential impacts of the Site C project for VECs should the project proceed to Stage 3.
2.0 SPECIES GROUP SUMMARIES
The 2008 wildlife program was designed to address data gaps identified at the conclusion of the 2006 field program. This addendum report includes the results for baseline inventories for furbearers and ungulates.
RISC standard methodologies were used where available for all survey types. Habitat stratification was completed prior to surveys to ensure that representative sites within the study areas were selected. Scientific and common names correspond to those assigned by the BC Conservation Data Centre.
2.1 FURBEARERS
All furbearers found in the study area are regionally important because they are commercially trapped, but the fisher and the wolverine are the only furbearers classified as species at risk. Wolverines are expected to rarely use the Peace River valley based on a lack of preferred habitat (BC MWLAP 2004). There is little information on the abundance of fishers in the Peace River valley, but they are known to breed in large old balsam poplars (Populus balsamifera) in riparian habitat (Weir 1995), and forage extensively on spruce forested floodplains.
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Riparian habitat occurring within the potential project footprint may be at risk due to habitat alteration and inundation associated with the potential Site C project. Habitat analysis, trapline records, information from other nearby studies (Weir 2009), and track surveys suggested that fishers are present in the study area. One previous photo inventory using remote camera stations was unsuccessful in confirming the presence of fishers in the study area and a more extensive and intensive survey was designed in 2008/09 to:
• confirm the presence of fishers in the Peace River Valley; and
• determine if further study or inventory is warranted.
2.1.1 Introduction
Fishers have economic and First Nations significance and are provincially Blue-listed, but have been recommended for the Red list based on their low density and vulnerability to trapping. In 2006, seven remote camera bait stations maintained over a three month winter period were unsuccessful in documenting fisher presence in the Peace River Corridor study area (Keystone Wildlife Research 2006). Information from recent fisher studies in the Kiskatinaw River drainage, southeast of the potential Site C project (Weir 2005, 2006, 2007, 2008, 2009), indicated that fishers might be easily missed using standard survey techniques (RISC 1999a). During this study commercial traps were modified to exclude fisher, to reduce the trapping pressure on the fisher population during the study (Rich Weir pers. comm. 2008). Therefore, more intensive sampling was employed in 2008/09 to confirm fisher presence and estimate the number of fishers using the potential Site C reservoir area, both north and south of the river.
Genetic analysis methods using passively collected hair from fishers have been used to determine if fishers are present and to identify individuals (Weir 2006; Mowat and Paetkau 2002). Weir (2007) reported that the mark-recapture inventory completed in the Dawson Creek area was largely unsuccessful since only one of three radio-tagged fishers known to be present was detected. It was recommended that increased efficacy might be achieved by using persistent olfactory attractants and small sampling units (~20 km2) situated in biologically relevant areas.
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2.1.2 Background
Furbearers that are trapped in the Peace River and surrounding plateau include snowshoe hare (Lepus americanus), red squirrel (Tamiasciurus hudsonicus), Canada lynx (Lynx canadensis), American marten (Martes americana), long-tailed weasel (Mustela frenata), ermine (Mustela erminea), common muskrat (Ondatra zibethicus), fisher, northern river otter (Lontra canadensis), red fox (Vulpes vulpes), wolverine (Gulo gulo), grey wolf (Canis lupus), American beaver (Castor canadensis), American mink (Neovison vison) and coyote (Canis latrans) (Thurber 1973, 1976; Blood 1979). Although catch varied by year, the species harvested in greatest numbers in the Peace River area from trapping records were red squirrel, followed by long-tailed weasel, marten, beaver and muskrat (Thurber 1976; Blood 1979, 1991).
Thurber (1976) completed winter track counts for furbearers in 1974 in the Peace River valley and reviewed trapping records from 1937 to 1974. Tracks of snowshoe hare, red squirrel, weasel and coyote occurred the most frequently. In 1974 and 1975, red squirrel, muskrat, beaver and long-tailed weasel were the most common catches on traplines that bordered the Peace River and adjacent tributaries. Otters were uncommon in the area and annual harvest of wolverines between 1937 and 1974 averaged two wolverines per year.
Blood (1979) also reviewed trapper catch reports and interviewed local residents to collect data on furbearers around the Site C area. Coyotes were described as common along the Peace River corridor. Lynx densities were estimated at 0.05 lynx per km2 but fluctuate behind snowshoe hare cycles. Red squirrels dominated trapline catches in numbers and were abundant in the sampling area. Regional traplines reported mustelid catch abundances in the following order: marten, ermine, fisher, mink and wolverine. Otters have been trapped near the Peace Canyon Dam but were considered rare in the Site C area. Red foxes were also uncommon in the Site C area.
Ten years later, Blood (1991) reviewed wildlife harvest questionnaires, wildlife harvest data, and trapping records provided by trappers and fur buyers in the Peace River area. The most abundant catch in the Peace River valley was the red squirrel, followed by beaver, marten, muskrat, weasel, coyote and mink.
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Simpson (1991) completed track counts during the winter to estimate relative use among habitats in the same geographic area. Furbearer tracks were recorded in the following order of abundance: coyote, marten, weasel, fisher, lynx, wolf, mink, fox and wolverine. Tracks of mink and otters were infrequently detected but sampling mainly occurred in upland habitats rather than adjacent to the river banks where these species are expected to be most active.
Surveys were undertaken in 2006 to confirm current fisher presence in the Peace River Corridor. Snow tracking transects were completed and seven baited remote camera stations (RIC 1999a) were installed to identify sites being used by furbearers. No fishers were detected but martens were photographed at five of the seven stations (Keystone Wildlife Research Ltd. 2006).
BC Ministry of Environment (MoE) data for 12 trapping territories that intersect the potential Site C reservoir (between Hudson’s Hope and the Moberly River) were reviewed. The data file contained over 17,000 records from 1983 to 2007. The data included 14 species: black bear, beaver, coyote, fisher, lynx, marten, mink, muskrat, red fox, red squirrel, otter, weasel, wolf and wolverine. Squirrel, marten and beaver were the most frequently caught, with 10,566 squirrels, 3,198 martens and 1,711 beavers captured over 25 years. Weasels (840), coyotes (403) and muskrats (309) were also trapped in quantity, but with more annual variation over the 24 year period.
Marten
American marten were considered numerous in the Peace River valley and surrounding uplands based on the numbers caught by trappers (Thurber 1976; Blood 1979, 1991). According to the MoE trapline data, an annual average of 128 marten was caught between 1983 and 2007. The lowest catch was in 1998 with 25 martens while the highest reported catch occurred in 1988 with 289 animals harvested. During a fisher study in the Kiskatinaw Plateau in 2005, 12.8 marten were captured per 100 trapnights compared to 0.84 fishers per 100 trapnights (Weir 2006). Poole et al. (2004) studied marten habitat use and range near the Peace River Region and found that although marten preferred mature coniferous stands, they also used deciduous
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Fisher
Thurber (1976) found fisher tracks only in deciduous forest during furbearer winter track transects completed in 1974. Blood (1979) concluded that fishers inhabit the Site C area in low densities, and estimated approximately one to three animals present in total.
Thurber (1976) reviewed data for 22 traplines bordering the Peace River and adjacent tributaries, and calculated a mean annual catch of 15 fishers. Blood (1979) reviewed fur catch for 8 traplines bordering the Site C project area and calculated a mean annual catch of 18 fisher, between 1973 and 1976. The MoE trapline data indicates that, on average, six fishers were trapped per year between 1983 and 2007, with 110 fishers caught over 25 years. The highest number of recorded captures in a single year was twelve in 1988 (MoE trapline data). Fisher catch was generally higher in the 1980’s than in the 1990s and early 2000s, but there is no definite trend in fisher abundance (Figure 2.1.2). It is important to note that the numbers of animals harvested by trappers do not vary solely with animal abundance, but also reflect trapper effort, which is dependent on a variety of factors including winter weather and fur prices.
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6 Number Harvested
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0
3 4 5 6 7 8 9 0 4 5 6 7 8 9 0 1 2 5 6 7 8 8 8 8 8 8 8 9 9 9 9 9 9 9 0 0 0 0 0 0 9 9 9 9 9 9 9 9 9 9 9 9 9 9 0 0 0 0 0 0 1 1 1 1 1 1 1 1 1 1 1 1 1 1 2 2 2 2 2 2 Year
Figure 2.1.2. Numbers of fishers harvested on 15 traplines in the Peace River area between 1983 and 2007.
In 2005, a fisher telemetry study was initiated in the Kiskatinaw area, southwest of Dawson Creek, to examine fisher habitat associations and movements (Weir 2005, 2006, 2007, 2008, 2009). Six fishers were trapped and radio-tagged in 2005, 4 in 2006, 12 in 2007 and 8 in 2008. Radio-telemetry completed between 2005 and 2008 resulted in the identification of 161 resting sites and 27 reproductive dens. Fishers were found to rest in or under accumulations of coarse woody debris, subnivean cavities under shrubs, tree cavities, single pieces of coarse woody debris, platforms in coniferous trees, abandoned buildings, underground burrows, abandoned beaver lodges or magpie nests (Weir 2007). Dens were found in balsam poplar (n=11) and aspen (Populus tremuloides) trees (n=16). The mean diameter at breast height of den trees
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Site C Hydro Project Vegetation and Wildlife Report Addendum #1 was 59.1 cm for balsam poplar and 51.7 cm for trembling aspen, and all trees had some level of decay that resulted in cavities used as dens (Weir 2009).
Weir (2007) estimated fisher density in the Kiskatinaw study area to be 13.7 fishers /1000 km2. Home ranges for 17 fishers were calculated to be 32 km² (SD = 15, n = 13) for females and 199 km² (SD = 51, n = 4) for males (Weir 2009). Lower densities (8.6-11.2 / 1000 km2) and larger home ranges were documented in the Williston study area, west of the potential Site C dam site (49 km²; SD = 16, n = 6) for female fishers and 219 km² for males (n = 2); Weir and Corbould 2008).
A hair-snagging study was also completed on the Kiskatinaw Plateau (Weir 2006). Three hair- snagging sessions were completed in 46, 7x7 km grid cells between January and April 2006. Weir (2007) collected 229 hair samples at 56 sites in 35 grid cells during 3 sampling sessions. DNA analysis of hair samples identified 7 fishers (5M, 2F), 35 American martens, 8 red squirrels, 3 ermine, 3 flying squirrels (Glaucomys sabrina) and 1 black bear.
Beaver
Blood (1979) completed one aerial survey to identify beaver lodges along the Peace River (Moberly River to Hudson Hope) and ground searches of the Peace River’s major tributaries in November 1976 (Table 2.1.2). Thirty to 40 colonies were found along the Peace River and tributaries, resulting in an estimate of 150 to 200 beavers within the Peace River valley. Most beavers were found along the Peace River rather than its tributaries, due to the Peace River’s low gradient and velocity.
MoE data from 12 trapping territories adjacent to the potential Site C reservoir indicate a large decrease in numbers of beavers harvested between 1999 and 2007, compared to between 1983 and 1998. The average catch between 1983 and 1998 was 93 beavers per year, versus 25 beavers per year between 1999 and 2007. The highest beaver catch was recorded in 1987 (224 animals). The lowest beaver catch was recorded in 1990 with 11 beavers. Again, trap data reflects trapper effort (fur prices) as well as animal abundance.
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In 1990 and 1991, Simpson (1991) completed systematic aerial and boat surveys of the Peace River to record beaver food caches and lodges. They reported 76 active lodges upstream of the Moberly River and estimated a beaver population of 380 (Table 2.1.2).
Aerial surveys and ground surveys were conducted for beavers and other aquatic mammals in 1999 in the Peace River Corridor from Hudson’s Hope to the Alberta border by Fraker and Hawkes (2000). They found 128 lodges and 59 food caches and estimated that there were 59 colonies with 5.7 beavers in each colony. The population was thus estimated to be 336 animals. They reported that beavers appeared to be common downstream of Farrell Creek Ranch but uncommon upstream of this site.
Smith (2002) completed a boat survey in November 2001 between Taylor, BC and the town of Peace River, Alberta. Forty-eight beaver dens were observed with an estimated density of approximately 0.18 dens/km along the Peace River. Sixty percent of dens found were on south- facing riverbanks.
Keystone Wildlife Research Ltd. (2006) undertook a RIC (1998a) standard food cache count to verify the expected population of beavers in the Peace River Corridor. An aerial survey was flown in September 2006 and 67 active and 60 inactive lodges were recorded between Hudson’s Hope and the Moberly River. They also identified 75 active lodges and 50 inactive lodges downstream of the Moberly River. A population of 335 beavers was estimated for the Peace River between Hudson’s Hope and the Moberly River.
Overall, the beaver population in the potential Site C reservoir area appeared to increase after the construction of the WAC Bennett dam (Thurber 1979). This increase might be attributed to the regulated water levels that favour gravel deposition and island formation, thereby enhancing the area for beavers. Flow regulation also moderates the spring freshet, which may have prevented damage to existing lodges and potential associated mortality of kits.
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Table 2.1.2. Summary of beaver surveys completed on the Peace River between 1976 and 2006.
Survey Date Survey area Number of active Estimated lodges/colonies population Blood (1976) November Peace River (Hudson 30-40 150-200 1976 Hope to Moberly River) Simpson (1991) October 1990 Peace River (Hudson 76 380 Hope to Moberly River) Fraker and 1999 Peace River 59 336 Hawkes (2000) Smith (2002) November Peace River (Taylor, BC 48 n/a 2001 to Peace River Alt) Keystone Wildlife September Peace River (Hudson’s 67 335 Research Ltd. 2006 Hope to Moberly River) (2006)
Lynx
Lynx population numbers fluctuate according to snowshoe hare populations, and have historically provided a large portion of income for trappers in the Peace River area due to historically high pelt prices (Blood 1979). One lynx was observed incidentally in the potential Site C reservoir in 1973 (Thurber 1973). Blood (1979) used trapping records to estimate a density of 0.05 lynx per km2 in the Site C inundation zone. Lynx tracks, sign and observations were rarely observed during furbearer surveys completed by Simpson (1991).
MoE trapping data from 1983 to 2007 show large fluctuations in the numbers of lynx captured, from 40 lynx caught in one year to 1 lynx caught in other years. Overall, 97 lynx were trapped in the Peace Region between 1983 and 2007, with an average of six per year.
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Wolf
Blood (1979) reported that wolves use the Moberly River, Halfway River, Lynx Creek, Farrell Creek and Cache Creek, upstream from the edges of the Peace River. Wolves have also been reported to use the south bank, west of the Attachie Slide on the Peace River (1978). Blood (1979) estimated a population of 20 to 30 wolves with territories mostly outside the potential Site C reservoir. Wiacek (1998) reported that wolves are present in low numbers in the Moberly River valley but are rare in the Peace River valley because of removal near agricultural lands.
Wolves were trapped sporadically in the Peace Region between 1983 and 2007, according to MoE trapping data. Wolves were captured during only 9 of 25 years, with 1 to 2 wolves trapped in each of these years, except in 1997 when 11 wolves were trapped.
Muskrat
Muskrat habitat is limited in the Peace River Valley, but there may be some upland wetlands such as Watson's Slough that support muskrats (Blood 1979; Wiacek 1998). The MoE trapping data for trapping territories that intersect with the potential Site C reservoir indicate an average of 16 muskrats taken per year, between 1983 and 2007.
Wolverine
There is limited wolverine habitat within the Peace River area (BC MWLAP 2004). In total, 15 wolverines were reported trapped within the trapline territories intersecting the potential site C reservoir between 1983 and 2007, an average of 0.6 wolverines per year. Wolverines were reported trapped in 10 years of the 25 years for which data were available.
2.1.3 Methods
There are no provincial (RISC) standards for mustelid DNA mark-recapture surveys, but methods are under investigation (RISC 1999a). Survey methodology was based on published data and methods from a fisher hair-snagging study completed in the Kiskatinaw in 2006 (Weir 2006, 2007). The methods were further refined after consultation with fisher expert Rich Weir and review of the results of the Kiskatinaw telemetry studies (Weir 2006, 2007, 2008, 2009).
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2.1.3.1. Study Area
The study area was defined as the potential Site C reservoir and adjacent areas. This includes the Peace River between Hudson's Hope and the potential Site C dam site, as well as suitable habitat along the Halfway River, Moberly River and Cache Creek within the potential Site C reservoir area.
2.1.3.2. Hair-snagging Study
Fishers traverse their home ranges frequently and are extremely wary of new features, often avoiding them (Rich Weir pers. comm. 2008). To increase capture success, it was recommended that hair-snagging stations be installed a minimum of 2 months prior to sampling in order to habituate the fishers to the structures.
The recommended grid cell size for fisher DNA sampling is 20 km2 (4.5 X 4.5 km) (Weir 2007). That grid size corresponds to the lower known values for home range size of an adult female fisher in the Peace Region and improves the probability that resident fishers will encounter the sample station (Weir 2007). Since the objective of this study was to determine the presence and abundance of fishers in the Peace River valley, a standard grid design to sample a closed population could not be used. Grid cells were established along the length of the study area and, since the Peace River may be a barrier to movement, on both the north and south sides of the river. Two to three grid cells were also established along Cache Creek, Halfway River and the Moberly River within the potential Site C reservoir.
Rich forested site series (09, 07, 05) in older structural stages were highlighted to guide the placement of hair-snagging stations. Suitable habitat within each grid cell was identified using the TEM mapping and mature/old rich sites, riparian sites with large aspen (>50 cm diameter) or balsam poplar (>80 cm diameter) trees, and black spruce (Picea mariana) bogs were targeted. Two sites were selected within each 20 km2 cell, one on each side of the river. Ground searches were used to confirm suitability and locate features that may attract use by fishers. Topographic features such as ridges and draws may improve capture success (R. Weir, pers. comm.) and were selected within the sample grid where they were available and accessible.
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Meso-carnivore Specialist Eric Lofroth was contacted to inform the BC Ministry of Environment (MoE) of the study plans and methodology and he approved the use of their boxes (pers. comm. 2008). Fifty seasoned hair snag boxes were borrowed from the Kiskatinaw project.
Stations were set up in the fall (September-October) and pre-baited in the early winter (November-December) prior to hair snagging. Each station consisted of a 3-sided wood plank channel (open at both ends) nailed lengthwise along a tree trunk (hair-snagging box; Figure 2.1.3.1a; 2.1.3.1b). A small wooden roof and run-pole were also attached to the tree to protect the unit from rain and to provide easy access, respectively (Figure 2.1.3.1b). Early winter pre- baiting consisted of suspending (>2 m above the ground) 20 to 30 pounds of raw meat within 100 m of the station. The boxes themselves were not baited. Waste meat (beef and pork) from a local butcher, and a peanut butter cocktail (peanut butter mixed with skunk scent, fisher lure and beaver castor) were used to pre-bait the area around each station.
The hair-snagging boxes were baited between January and April, once fishers were habituated to the sites. The bait (same mixture as was used during pre-baiting) was placed in the centre of the boxes, to entice fishers to enter, and three sticky glue strips (2x4 cm) were attached inside each open end (top and bottom) to collect hair (Figure 2.1.3.1a). Each site was visited during three winter sessions (January, February and March) to collect hair samples, re-bait the boxes and replace the sticky strips. The samples collected during each session were labelled with the site number, date and position on the hair-snagging box (top centre/right/left and bottom centre/right/left). Up to six sticky strips with hair samples attached to the adhesive were collected per station per session. Sticky strips without hair were discarded.
The level of activity at each station was also recorded during each visit. The use of the bait and peanut butter cocktail was quantified as high (bait is gone or has been heavily fed upon), moderate (~50% of the bait is gone), low (bait is mostly intact with limited evidence of use) or nil (no evidence of use). The number of tracks within a 5 m radius of the hair-snagging box was also recorded, with tracks identified to species where possible.
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Figure 2.1.3.2a. Fisher hair-snagging box.
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Figure 2.1.3.1b. Fisher hair-snagging station set-up.
Analysis
The DNA analysis of the hair samples was completed in two rounds. In the first round, one sample was selected from each station/session combination, with samples preferentially selected for analysis based on hair morphology and colour (indicating fisher), and the sample quality as defined by the laboratory. In the second round, the remaining samples were prioritized to maximize the number of fishers detected. The remaining samples were prioritized based on:
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• the position of the sample in the hair snagging box; where the opposite end of the box was sampled compared to the first round;
• the detection of a fisher at the station; where stations with a previous fisher detection had lower priority.
DNA extraction was completed using QIAGEN’s DNeasy tissue kits following the manufacturer’s instructions. Ten guard hair roots were used when available, but underfur was also used. Species were differentiated using a sequence-based mtDNA analysis of a segment of the 16S rRNA gene. The sequence from the extracted DNA was compared to reference data from over 100 species of mammals, including all of the mustelids found in western Canada. Samples with mixed DNA (multiple species) were scored to indicate the confidence of the identification. Quality control procedures included confirming mixed, failed or unusual results and running a proportion of samples twice to provide a record of run-to-run consistency.
Microsatellite geneotyping using 10 markers (Lut604, Mp055, Mp144, Mp182, Mp085, Mvis72, Mp114, Mp175, Mp197, Mp059) was used to identify individual fishers. Individuals were defined for each unique multilocus genotype. Quality control procedures included culling samples that succeeded at fewer than 5 of the 10 markers, since low quality samples are prone to a high rate of genotyping error. Markers with weak results were re-analyzed until a high confidence rank was achieved at all 10 microsatellite markers (Paetkow 2003).
Analysis of gender was based on the ZFX/ZFY/SRY system that was developed for mustelids. One sample from each identified individual was selected for gender analysis. Sample selection was biased towards those samples with strong results at all 10 markers. A female control from a previous project and blank control tubes were included in the analysis to confirm results. The analysis was also repeated, using the same sample again or a second samples from a given individual, to confirm results.
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2.1.3.3. Habitat Suitability Mapping
The fisher breeds in large old cottonwoods/poplars in riparian habitat (Weir 1995), and forages extensively on spruce floodplains. Riparian areas often provide important linkages between patches of suitable late-successional forests. Habitat features that are associated with high use by fishers include large (> 35 cm) coarse woody debris that is elevated (> 25 cm) above the ground, aspen trees > 50 cm diameter with heart rot, poplar trees > 80 cm diameter, and rust brooms on black or white spruce (Picea glauca)> 50 cm across (Weir 1995). Fishers are most often found in nutrient-rich (productive) sites. Denning and resting are associated with old stands, while fishers hunt in all structural stages. Younger stands often have higher numbers of hares and grouse, which may be preferred prey. Fishers are most active from late morning to early evening but spend most of their time resting. They rest in trees in the growing season (rust brooms, tree cavities) and in subnivean cavities, under coarse woody debris, or in burrows made by other animals during the winter (Weir 1995). A draft species model and ratings table were prepared for fisher (Keystone Wildlife Research Ltd. 2008a, 2008b). The ActSw - Red- osier dogwood floodplain unit was rated High for reproducing, and dry to mesic coniferous forests were rated highest for winter feeding.
2.1.4 Results
The locations of fisher hair-snagging stations surveyed in 2009 is presented on Map 1.
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Map 1. Fisher hair-snagging stations.
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2.1.4.1. 2008 Inventory Surveys
Forty-one hair-snagging stations were established at ~4.5 km intervals on the left (north) and right (south) banks of the Peace River. An additional seven stations set up on the Moberly River (2), Halfway River (3) and Cache Creek (2) were accessed by helicopter. All 48 sites were within or close to (<500 m) the potential Site C reservoir area. Initial site selection began in September 2008 and 40 boxes were set up within or close to suitable habitat within each grid cell. An overview (helicopter) flight and installation of the remaining 8 boxes took place between October 2 and 8, 2008. Most (26) sites were accessed by boat, 15 by road and 7 by helicopter. Two sites were established at station 15R since access to the upper box was uncertain in winter, as it required climbing a steep, ice-covered slope.
A permit (#FJ08-48888) was received from MoE to bait the hair-sampling sites. Pre-baiting began on October 3, 2008 and sites were re-baited once per month until December 2009 (Appendix 1). The hair-snagging boxes were baited beginning in January and replenished monthly (February, March) when the hair samples were collected. The first hair samples were collected February 10, 2009. Forty-eight hair-snagging stations were visited during 3 sampling sessions for a total of 144 station visits (Appendix 2). Stations were operational for 26 days on average between hair collection/rebaiting visits during the 3 sampling periods (Table 2.1.4.1a; SD=4.7, n=144).
Table 2.1.4.1a. Duration of fisher DNA hair sampling in the Peace River Corridor.
Sampling Start End Number of Sites Mean Duration Session Visited (days) 1 Jan-9-09 Feb-13-09 48 30 2 Feb-13-09 Mar-10-09 48 25 3 Mar-10-09 Apr-1-09 48 22 Total 144 26
Hair samples were collected at 47 out of 48 stations, during 123 of the 144 station visits. In total, 519 hair samples were collected between February 10 and April 1 2009, with an average of 4 (range 0 to 6) samples collected per station visit (Table 2.1.4.1b). Trap failure rate was 15%, calculated as the percentage of station visits that did not result in hair samples. No fishers
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Site C Hydro Project Vegetation and Wildlife Report Addendum #1 were observed during visits to the stations, but other wildlife, including marten, were observed at the bait.
Table 2.1.4.1b. Numbers of hair samples collected at fisher stations between February 10 and April 1, 2009.
Session 1 Session 2 Session 3 Total
Number Number Number Number Number Number Number of Area stations of stations of stations of Number samples with samples with samples with samples stations collected samples collected samples collected samples collected
North (left bank) 55 16 57 13 50 17 162 20 Peace River South (right bank) Peace 87 19 93 20 93 20 273 21 River Moberly River 10 2 12 2 5 1 27 2 Cache Creek 4 1 7 2 3 1 14 2 Halfway River 14 3 15 3 14 3 43 3 Total 170 41 184 40 165 42 519 48
DNA was extracted from 259 of the 519 samples collected. Of the remainder, 249 were not selected for extraction, and 11 lacked suitable material. Marten was detected the most frequently (n=177, 71% of extracted samples), followed by fisher (n=37, 14%), short-tailed weasel (n=10, 4%) and red squirrel (n=9, 3%).
Of the 37 samples that contained fisher DNA, 7 failed at more than 5 of the 10 markers and microsatellite genotyping could not be completed. Two of the seven failed samples that contained fisher DNA appeared to have DNA from a fisher that had been identified in other samples. All but one of the failed samples originated from sample sites where a fisher had already been detected. The microsatellite genotyping succeeded in identifying 8 individuals from the 30 samples. These samples all had high confidence scores for all 10 microsatellite markers and the rate of genotyping error is < 1% per locus. Gender analysis concluded that all 8 individuals were male. The analysis was repeated to confirm this result. One additional fisher of undetermined sex was inferred based on the location of the sample station and its distance
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Site C Hydro Project Vegetation and Wildlife Report Addendum #1 from any other confirmed fisher samples. This station was near Hudson’s Hope and was identified as unique because it was over 28 km from the nearest identified individual. The sex of that animal could not be determined.
Weir (2007) reported that bait at hair-snagging stations was often not eaten and deduced that this could indicate that the olfactory attractants were not effective. Bait use (activity) was ranked as high, medium, low and nil depending on the observed use of the bait during the site visit. During 144 station visits, 77% (n=111) of the stations had high use, 8% (n=11) had moderate use and 15% (n=22) had low use. Of the stations that had high bait use, 95% also captured hair samples. This indicates that the bait was successful at attracting animals and presumably fishers when they were present. The greatest number of samples from fishers (n=16) was obtained during the last sampling session, when temperatures averaged 0°C. Average temperatures during session 1 (n=11) and 2 (n=10) were around -20°C. High bait activity was recorded at most stations during all 3 sessions and detections of furbearers were relatively constant (session 1 n=73, session 2 n=82, session 3 n=70).
The position of the sample on the box (location of the sticky pad) was also reviewed to determine whether there is any evidence that fishers prefer entering the box from the top or bottom. Fisher hair was collected slightly more frequently on sticky pads placed at the bottom of the box (n=23, 62%).
Of the nine individuals identified, three were captured in all three sessions, two were captured only in session one and four were captured only in session three (Table 2.1.4.1c). Four fishers were captured at two or more different stations and the distance travelled between stations by an individual ranged from 3.3 to 17 km. Only one identified fisher was captured at any single station, based on DNA analysis, and most multiple captures of an individual fisher were at adjacent stations that were likely within the home range of a resident adult. Only one fisher (Red2) was found within the apparent home range of another (Red1), indicating that Red2 may not be an adult resident. With the exclusion of Red2 and HHope (since the sex could not be determined), this study confirmed the presence of seven resident adult male fishers in the study area.
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Table 2.1.4.1c. Sample sites and sessions where individual fishers were identified.
Fisher Maximum Number of distance Number of Fisher DNA Sessions between Marten DNA Individual samples Detected Sample Sites stations (km) samples** HHope 1* 1 1L n/a 0 Ard1 1 1 8L n/a 3 Ard2 4 1,2,3 10L, 12Half 5.7 5 Ard3 1 3 9L n/a 2 Red1 5 3 18L, 22L, 24L 17.0 2 Red2 1 3 23L n/a 0 Red3 2 3 25L n/a 3 Mob1 11 1,2,3 18R, 21R, 22R, 23R 12.8 8 Mob2 5 1,2,3 24R, 25R 3.3 0 8L, 10L, 18L, 21R, UnID 6 1, 2, 3 22R, 20Cache n/a 12 No Fishers 1,2,3 31 other sites 158 Total 37 183 *ID assigned based on capture location not DNA analysis; ** includes samples with mixed DNA (marten + other species)
Five of the nine fishers identified were in the Cache Creek to Moberly River area, three on the north (left) bank and two on the south (right) bank. Three additional animals were identified in the Farrell Creek to Halfway River area and one near Hudson’s Hope, all on the north side. No individuals were captured on both the north and south bank of the river, indicating that the open water of the river may be a barrier to movement, at least during the winter. Some factors that may have influenced the disproportionate number of fishers captured on the north side of the river include the placement of boxes along the river, trapping effort, and the availability of habitat. The capture of seven of nine fishers on the north side is contrary to expectations based on the habitat mapping. The north side has limited forest habitat that is highly dissected by agricultural fields and natural grasslands, while the south side has mainly contiguous forested habitat and was expected to produce the majority of the fisher captures based on the quality and quantity of habitat. The scarcity of suitable habitat on the north side of the river may act to constrain movement patterns, thereby increasing the probability that a fisher would encounter a hair-snagging box placed in the limited habitat available.
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BC Ministry of Environment trapping records from 1983 to 2007 were obtained for 12 trapping territories that are adjacent to the potential Site C reservoir. The number of marten harvested provides a rough measure of trapping effort while the numbers and proportion of fishers taken provide an indication of trapping pressure on fisher populations. In total, 110 fishers were trapped, with 27 (24.5%) taken from two trapping areas that bound the south (right) bank of the Peace River, between Hudson’s Hope and Cache Creek (Table 2.1.4.1d). Marten traps were observed within these trapline areas at several sites during fisher sampling in October and November 2009. Records indicate that 303 marten were harvested on those two traplines between 1983-2007, resulting in a relatively high ratio of fisher to marten captured on those traplines (0.05 to 0.19). The river likely provides the main trapping access to these areas, resulting in concentrated trapping along the river, which overlaps the area sampled during hair snagging. No fishers were detected within those two trapline areas during the hair snagging study.
Table 2.1.4.1d. Fisher DNA captures (2009) compared with marten and fisher trapping data (1983-2007). Fisher/ Total Total marten N/S of fisher marten trapped Fisher DNA Geographic Area Peace Trapline trapped trapped ratio samples West Hudson's Hope S TR0732T001 4 239 0.02 0 HHope (upper Moberly) S TR0732T002 3 25 0.12 (not sampled) HHope to Halfway S TR0732T003 17 90 0.19 0 Halfway to Cache S TR0732T004 11 213 0.05 0 Cache to Moberly N/S TR0734T001 1 96 0.01 3 N/2 S Lower Moberly and Pine S TR0732T005 3 26 0.12 0 West HHope N TR0735T001 33 554 0.06 1* HHope to Lynx N TR0735T002 3 165 0.02 0 Lynx to Farrell N TR0735T004 14 907 0.02 0 Farrell to Halfway N TR0735T005 16 653 0.02 3 Halfway to Watson N TR0734T003 0 7 0 0 Watson to Cache N TR0734T002 5 223 0.02 0
Total 110 3198 0.03 9 *individual ID not possible, assumed unique based on distance (28 km) from others captured
A single trapping territory covers the area from Moberly River to Cache Creek on both sides of the Peace. That area accounted for 5 of the 9 individual fisher detections and trapping records
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Site C Hydro Project Vegetation and Wildlife Report Addendum #1 show that only 1 fisher and 96 marten have been trapped in this area over the last 25 years. Three additional fishers were detected between Farrell Creek and the Halfway River. The trapper in this area reports that they have not trapped for marten in the lower part of the trapline (adjacent to the Peace River, between lower Farrell Creek and Halfway) in the last 4 to 5 years, although both marten and fisher have been taken in the upland areas (Renee Ardill – pers. comm.). Trapping on the adjacent downriver trapline (Halfway to Watson) has also been very limited based on harvest data (7 marten and 0 fisher in 25 years, Table 2.1.4.1d).
Harvest data indicate that trapping effort may have a major influence on fisher numbers in the study area. Male fishers were only present at expected densities in areas where trapping effort and fisher harvests have been low. The absence of female fishers detected in the hair- snagging study was not unexpected, since sampling was confined to the edge of fisher home ranges due to the barrier presented by the river. Outside of the birthing season, fishers often move about the periphery of their home ranges, marking the edges of their territory so that interlopers are aware that a resident animal occupies the space. If the river is a barrier to movement, there is almost no possibility that transient animals will access the resident home range from the river, and it is speculated that females might not travel along the riverfront portion of their home ranges very often, because there is no need to mark this portion of their home range boundary. Females occasionally den on the periphery of their home range, and in these cases, they rarely use the denning habitat prior to whelping (R. Weir – pers. comm.).
Males usually incorporate ranges of four to five females within their home range (Weir 2009). The presence of 7 adult males suggests that there may be 28 to 35 females in the vicinity of the study area. Those females likely use the upland habitat in winter and move to the high quality denning habitat along the river in spring (April). Effective DNA sampling cannot be completed in the growing season (April or later) due to the presence of bears, which would destroy the hair snagging stations. Capture of females in the uplands during the winter and radio monitoring during the spring would be required to confirm the expected habitat use during the growing season. The Moberly to Cache and Farrell to Halfway areas, which appear to support healthy fisher populations, also contain a large portion of the potential denning habitat (based on the TEM mapping) that would be inundated should the Site C project proceed. Those areas may
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Site C Hydro Project Vegetation and Wildlife Report Addendum #1 also be providing recruits to surrounding areas that are unoccupied or have a low density of fishers due to trapping pressure.
Incidental Furbearer Observations
Furbearer tracks were also counted during the ungulate winter snow tracking. Distinguishing fisher from marten tracks can be unreliable due to the extensive overlap of track characteristics between marten and fisher (RIC 1999a). Certain traits such as shape and connectedness of palm pad components, hairiness of the track and absence of a particular toe pad in the impression may be used, but there is no widely accepted method of distinguishing between marten and fisher (Zielinski and Truex 1995). Tracks reported during surveys were identified by First Nations trappers with extensive experience in the area, but identifications of marten and fisher were subjective and the results should be interpreted with caution.
Within the Moberly study area (Map 3), 1175 marten tracks, 77 fisher tracks, 67 fox tracks, 191 wolf tracks, 75 lynx tracks and 574 coyote tracks were counted over the 112 km surveyed. The relative occurrence of tracks within the study area, potential Site C dam area and potential Site C reservoir area is shown in Table 2.1.4.1.e. Marten tracks were the most commonly detected, while lynx, fox and fisher were rare.
Table 2.1.4.1e. Relative abundance of furbearer tracks /50 m segment ± standard deviation, in the Moberly study area.
Species Study Area Control Sites Potential Dam Potential Site C Area Reservoir Area Marten 0.53 ± 0.95 0.49 ± 0.96 0.61 ± 1.14 0.38 ± 0.64 Fisher 0.03 ± 0.23 0.04 ± 0.28 0.02 ± 0.16 0.02 ± 0.15 Fox 0.03 ± 0.17 0.02 ± 0.12 0.04 ± 0.21 0.05 ± 0.22 Wolf 0.09 ± 0.71 0.12 ± 0.96 0.00 ± 0.06 0.00 ± 0.00 Lynx 0.03 ± 0.30 0.01 ± 0.14 0.10 ± 0.57 0.00 ± 0.04 Coyote 0.25 ± 0.70 0.23 ± 0.72 0.32 ± 0.74 0.23 ± 0.61
2.1.5 Recommendations
Results to date suggest that fewer fishers than expected use the reservoir area, due primarily to trapping pressure. Healthy populations are present in the Moberly to Cache and Farrell to
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Halfway areas, based on the presence of male animals in winter. Habitat analysis and habitat use data from other studies indicate that:
• females are likely denning in the potential Site C reservoir area;
• the Moberly to Cache Creek and Halfway to Farrell areas are population sources that may provide recruits to surrounding areas;
• females may use the upland habitats most of the year and move to high quality denning habitat along the river in spring.
Nine different fishers were detected, eight of which were males. Most animals were found on the north side of the river where suitable habitat was limited. This may be the result of higher trapping effort in more suitable habitat on the south side, or because the limited habitat on the north side increased the chance of a fisher encountering a bait station. Eight of the nine animals detected occurred in areas where trapping effort has been very low, compared to adjacent traplines. Based on the expected sex ratio as established by other studies, there are likely 28-35 females within the home ranges of the resident males, but their use of the potential reservoir cannot be determined using winter sampling. The use of high suitability breeding habitat in the potential Site C reservoir area would best be confirmed through radio telemetry studies of females.
Establishing the seasonal use and importance of the riparian habitats would require capture and radio-monitoring of females captured in upland areas, adjacent to the potential Site C reservoir. It is evident that changing trapping practices to avoid incidental capture of fishers in marten traps could substantially increase the abundance of fishers in the Peace River area. This may provide an effective option to offset potential impacts on fishers from the project.
2.2 STONE’S SHEEP
No inventories have been completed for Stone’s sheep in the study area. Field surveys were planned in response to concerns from the Blueberry River First Nation (Blueberry) regarding the
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Site C Hydro Project Vegetation and Wildlife Report Addendum #1 potential effects of the Site C project on sheep herds in the area. Surveys were planned at a reconnaissance level to inform the need for future surveys. A field program was designed to:
• Survey for Stone’s sheep in the Peace River Corridor at the presence/not detected level of inventory;
• Collect pellets for DNA analysis.
2.2.1 Introduction
The Stone’s sheep (Ovis dalli stonei) is a subspecies of thinhorn mountain sheep. Stone’s sheep are Yellow-listed (not considered at risk) in British Columbia because they are relatively common and their main habitats are secure (BC CDC 2008; MoE 2000). Stone’s sheep are at the southern limit of their BC range in the Peace Region, and are known to inhabit the Peace Arm of the Williston Reservoir, with a few small populations known as far south as the Pine River (Shackleton 1999).
The currently described distribution of thinhorn sheep in northeastern BC does not include the Peace River valley (Demarchi and Hartwig 2004). An estimated 50 sheep are present in MU 7- 35, (Hudson’s Hope area, north of the Peace), and except for a small herd on the Sikanni River, all sheep in the Peace zone winter in the Hart Foothills Biophysical Area (Demarchi and Hartwig 2004).
Resident animals in the Peace River Valley would be restricted to suitable winter habitat found along the side drainages, since sheep cannot tolerate the deep snow (>50 cm) on the forested plateau. The wind and sun exposure on steep, warm aspect slopes act to reduce snow depths and expose winter forage.
2.2.2 Background
The area north of the Peace Arm of the Williston Reservoir currently supports a resident population of 75 to 100 Stone’s sheep (Arthur 2003). This group represents the southernmost extent of the contiguous Stone’s sheep distribution in BC. Backmeyer (2000) reported that
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Site C Hydro Project Vegetation and Wildlife Report Addendum #1 formation of the Williston reservoir isolated some small populations of Stone’s sheep from the large contiguous populations to the north.
From 1991 to 1993, 28 sheep were transplanted from the Peace Arm population to Mt. Frank Roy, approximately 50 km southwest of Hudson’s Hope, near the headwaters of the Moberly River (Wood 1995). Some of these animals were radio-collared and monitored (Backmeyer 2000). Subsequent winter censuses conducted by the Peace Williston Wildlife Compensation Program (PWWCP) showed a declining number of animals and low recruitment rates. The last census, completed in 1996, documented only six individuals, although it was recognized that some sheep had likely moved outside the search area (Wood and Hengeveld 1998). Backmeyer (2000) reported some extensive movements by collared sheep, mainly in summer, but most animals wintered on a few alpine ridges near Mt. Monteith and Mt. Frank Roy.
One ram was captured by conservation officers in the Pine River valley west of Chetwynd in May 1994. The ram was relocated to a site near Mount Monteith where a few other Stone’s sheep had been sighted (Wood and Hengeveld 1998).
The PWWCP funded a wildlife habitat capability mapping project in the Peace Arm area in 1993. Backmeyer (1994) reported that there was very limited sheep habitat capability south of the reservoir due to a lack of winter habitat. The maximum capability rating for sheep on the Peace Arm was class 4 (low) for steep, warm aspect, dry grassland units.
BC MoE (2000) summarized the important characteristics of Stone’s sheep winter range as “treeless ranges with little or no snow cover. These are invariably located close to cliffs where the sheep can escape from wolves. Ideal winter ranges are rare, and sheep often graze them heavily. In northern British Columbia, most winter range is located on windswept ridge crests in the alpine zone from 1500 m to 2200 m in elevation.”
Backmeyer (1994) reported “there appear to be three distinct wintering strategies among sheep in the Peace Arm population: exposed alpine/subalpine sites (Butler Ridge to Nabesche Ridge), mid-elevation conifer bluffs (south end of Aylard Ridge), and low-elevation, south aspect, shrub/grasslands with adjacent escape terrain (numerous sites along Williston Reservoir)”. All
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Site C Hydro Project Vegetation and Wildlife Report Addendum #1 winter ranges designated in the area were north of the Peace Arm, between 1200 and 1900 metres in elevation (Arthur 2003). No shrub/grassland sites along the Williston Reservoir were deemed important enough to designate as sheep winter range.
2.2.3 Methods
There are no provincial standards for Stone’s sheep surveys. Inventory methods used in 2009 were based on the BC Resource Inventory Standards Committee’s Survey Methods for Ground-based Inventory Methods for Selected Ungulates: Moose, Elk, Deer (RIC 1998b). Presence/ not detected surveys were completed to assess the potential distribution of Stone’s sheep in the study area.
2.2.3.1. Inventory Methods
Representatives of the Blueberry River First Nation (Blueberry) were provided with maps of the study area. They marked areas believed to be important for sheep and identified fifteen potentially suitable areas between the Moberly River and Hudson’s Hope (Map 2). Areas with suitable habitat characteristics, according to the TEM mapping, adjacent or close to areas identified by the Blueberry, were added to field maps to assist with selection of transect routes.
Winter snow tracking surveys were undertaken to identify winter ranges of resident animals. Surveys were completed two to six days after fresh snowfalls. Two-person crews traversed through each identified area, as feasible, usually along the crest of open slopes where sheep were most likely to be wintering. UTM coordinates were recorded at 100 to 200 m intervals and signs of use (tracks, pellets) were recorded for all ungulate species encountered between waypoints.
Spring/ summer surveys focused on collecting evidence of use in and adjacent to the winter range areas. UTM coordinates were recorded at 100 to 200 m intervals and signs of use (tracks, pellets) from all ungulate species were recorded as encountered. Due to the similarities between sheep and deer tracks and pellets (size and shape), a representative sample of pellets was collected for DNA analysis.
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2.2.3.2. Pellet Analysis
DNA analysis for pellet samples was completed using QIAGEN’s DNeasy Tissue Kits. Pellets were immersed in QIAGEN’s ATL buffer for 1 hr. The pellets were then removed and the buffer solution containing the cells washed from the surface of the pellets was processed as a tissue sample. To determine species, a sequence-based analysis of the 16S rRNA mitochondrial gene was completed. Sample results were compared to reference data from over 100 mammal species found in North America, including one Stone’s sheep sample provided by Alberta Fish and Wildlife. Quality control procedures included isolation of amplified DNA and running control reactions for all extractions and amplifications. Samples with unusual results were re-analyzed.
2.2.3.3. Consultation
A survey of local residents and other knowledgeable persons (trappers, guides, hunters, landowners) was completed to confirm the presence of sheep and obtain more information on the timing of use by sheep. A questionnaire was developed to collect anecdotal evidence of sheep in the Peace River Valley (Appendix 3). Interested and willing individuals were consulted to determine if, when and where sheep have been observed in the study area.
2.2.3.4. Habitat Suitability Mapping
A draft species model and habitat suitability ratings have been prepared for Stone’s sheep. Wild sheep require steep, windblown grasslands as winter range, rough and broken terrain for security habitat during lambing, and rugged cliffs to provide escape habitat from predators (Arthur 2003). Lower-elevation grasslands may be used in early spring, when sheep are attracted to newly-sprouting grasses below the snow line. Sheep also need access to mineral licks (Demarchi and Hartwig 2004).
Grasslands and dry to mesic forests were rated up to Class 4 for security habitat in all seasons and for feeding habitat in the winter and growing season. No cliff habitat is present in the mapping.
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2.2.4 Results
The locations of Stone’s sheep surveys completed in 2009 are presented on Map 2. The locations of designated winter ranges for Stone’s sheep are presented in Map 3.
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Map 2. Stone’s sheep sampling sites.
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Map 3. Stone’s sheep winter ranges.
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2.2.4.1. 2008 Inventory Survey
Winter snow tracking surveys were completed on March 29-30 and April 9, 2009. The weather was clear to cloudy with temperatures ranging from - 5 to 5oC. Snowfalls were recorded on March 25th (4.2 cm) and April 3rd (3.4 cm).
Twelve of the 15 sites identified as potential winter range for Stone’s sheep were surveyed. Depending on the size and accessibility of the site, 1 to 15 stations were completed per site. Snow depths ranged from 0 to 60 cm, with deeper snow on the flats than on the steep slopes and crests. Snow depths on the crests, where sheep were most likely to be present, varied from 0 to 15 cm. This snow-free habitat was very limited in extent within each of the 15 areas identified. Most sites had evidence of recent use by wolves and sign of cougars was also noted. The quality of the escape terrain in all areas was considered marginal since there are no rock cliffs and the steepest open slopes consisted of slumping clay/silt banks, which were often ice- covered due to recent freeze/thaw cycles. It was hazardous to attempt to walk across the steep slopes so crews generally travelled along the crests, which had obvious game trails, and walked down ridges to promontories that provided good views of the open slopes. Overall, the habitat surveyed was not considered highly suitable for sheep.
Signs of use by ungulates (tracks, pellets, beds) were noted at all sites but no definitive signs of use by sheep were found. Deer sign (Odocoileus spp.) was found at all sites surveyed except at the Moberly River. Moose (Alces americanus) sign was found at six sites and elk (Cervus elaphus) sign was found at ten sites (Table 2.2.4.1a). Pellets were collected if their size and shape were consistent with them being from sheep or deer. Deer were observed at one site and moose were observed at two sites.
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Table 2.2.4.1a. Ungulate sign found in areas traversed in winter.
Number of Snow Sign detected? Pellet Transect # Date depth sample stations Deer Moose Elk (cm) collected 1 15 Mar 29/09 5-70 y y n n 2 15 Mar 29/09 0-50 n n y n 3 1 Not Surveyed n 4 13 Mar 30/09 0-50 y y y n 5 6 Mar 29/09 10-55 y y n n 6 12 Mar 30/09 0-45 y n y n 7 8 Mar 29/09 10-70 y n y n 8 1 Not Surveyed n 9 1 Not Surveyed n 10 6 Mar 30/09 25-55 y y y n 11 5 Mar 30/09 25-35 y n y n 12 6 Mar 30/09 0-70 y n y n 13 14 Apr 9/09 0-35 y y y n 14 3 Mar 30/09 0-55 y n y n 15 7 Mar 30/09 0-50 y y y y
All 15 pre-identified sites were re-surveyed between June 14 and 17, 2009, after the snow had melted and concentrations of pellets were exposed. All tracks observed were recorded and small pellets (possibly from sheep or deer) were collected to confirm the species. Sixteen additional spot checks were completed in the spring, at sites identified by the surveyors from the helicopter or boat (Table 2.2.4.1b). Deer and elk sign were observed at 13 and 14 of the 15 pre-identified sites, respectively. Moose sign was observed at four of the pre-identified sites.
Table 2.2.4.1b. Ungulate sign found in areas traversed in the spring.
Number of Transect or Sign observed? Pellet Transect # Date Stations Spot Check Sample Deer Moose Elk Collected 1 Spot check Jun 16/09 n n n n 1 5 Transect Jun 17/09 y n y n 2 10 Transect Jun 13/09 y y y n 3 1 Transect Jun 16/09 n n n n 4 11 Transect Jun 14/09 y y y y 5 8 Transect Jun 14/09 y n y y 6 9 Transect Jun 15/09 y n y y 7 3 Transect Jun 14/09 y y y y
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Number of Transect or Sign observed? Pellet Transect # Date Stations Spot Check Sample Deer Moose Elk Collected 7b 4 Transect Jun 17/09 y n y n 8 1 Transect Jun 16/09 n n y n 5 Transect Jun 13/09 y n y n 9 1 Spot check Jun 16/09 n n n n 9e 4 Transect Jun 15/09 y n y y 10 8 Transect Jun 15/09 y n y y 11 8 Transect Jun 13/09 y n y y 12 4 Transect Jun 14/09 y n y n 13 6 Transect Jun 15/09 y n y y 14 5 Transect Jun 13/09 y n y y 10 Transect Jun 13/09 y y y n 15 1 Spot check Jun 16/09 n y n y 16 1 Spot check Jun 16/09 n n n n 17 1 Spot check Jun 16/09 n n n n 18 1 Spot check Jun 16/09 n n n n 19 1 Spot check Jun 16/09 n n n n sc 1 1 Spot check Jun 17/09 y n n n sc 2 1 Spot check Jun 17/09 y n y n sc 3 1 Spot check Jun 17/09 y n y n sc 4 1 Spot check Jun 17/09 n n n n sc 5 1 Spot check Jun 17/09 n n n n sc 6 1 Spot check Jun 16/09 n y y n sc 7 1 Spot check Jun 16/09 n n n n
One juvenile elk and one cow elk were seen and one Northern Goshawk nest attended by a territorial pair of adults was noted. Deer were observed at two sites.
2.2.4.2. Pellet Analysis
In total, 39 pellet samples consisting of 3 to 14 pellets, and 2 hair samples were collected (Table 2.2.4.2). Samples were collected on ten different transects and one sample was collected opportunistically during a spring ungulate transect that was being completed concurrently with the Stone’s sheep transects.
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Table 2.2.4.2. Pellet and hair samples collected during spring transects.
Samples Collected Number of Samples Analyzed to Species Site Date Pellets White-tailed Label Hair Mule deer Coyote Failed Samples deer 13-Jun-09 1 1 4 14-Jun-09 6 5 1 13-Jun-09 2 2 5 14-Jun-09 4 3 1 6 15-Jun-09 1 1 7 14-Jun-09 1 1 9E 15-Jun-09 2 2 10 15-Jun-09 5 4 1 11 13-Jun-09 3 3 09-Apr-09 2 6 7 1 13 15-Jun-09 3 1 2 14 13-Jun-09 3 3 15 16-Jun-09 1 1 14 CA 14-Jun-09 1 1 Total 2 39 27 8 1 5
Both hair samples and two to eight individual pellets from each of the 39 pellet groups were analyzed (Table 2.2.4.2). Analysis of the 41 samples confirmed 27 samples to be from white- tailed deer and 8 samples to be from mule deer. Five of the pellet samples failed to produce any results. No sheep detections were confirmed in the Peace River Valley based on the genetic analysis of pellets.
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2.2.4.3. Consultation
Knowledgeable persons (trappers, guides, hunters, landowners) were contacted in the Peace River region to confirm the presence of sheep and obtain information on the timing of use. In total, 52 persons were contacted, including local trappers, hunters, landowners and other outdoors persons. Of these, 21 people did not respond or could not be reached.
Thirty-one people were interviewed in person, by telephone or through a mail-in questionnaire. All persons were contacted between April 15 and May 13, 2009 and asked a series of questions (Table 2.2.4.3, Appendix 3). Each respondent was asked about their history in the area, their recreational activities in the area and if they had any knowledge of Stone’s sheep in the area. All respondents had lived in the region between 8 and 80+ years and most self-identified as active outdoors persons.
Table 2.2.4.3. Summary of respondents that have observed Stone’s sheep in the Region or in the Peace River Valley, grouped by recreation/occupation type.
Recreation/ Number of Number respondents Number respondents that Occupation respondents that reported first hand reported first hand sheep sheep observations in observations outside the Peace River Peace River, in the Region Trappers 6 2 1 Hunters 10 2 2 Other 15 4 1
Eight of the thirty-one interviewees stated that they had seen one or more Stone’s sheep first hand within two kilometres of the Peace River valley. Most Stone’s sheep seen in the Peace River valley were observed near Hwy 29 between Bear Flats and Farrell Creek. One group of ewes and lambs was reported on the south side of the River near the Halfway confluence. Generally, respondents reported seeing sheep in the growing season. Recently (June 2009), three ewes were seen at the rest area on Highway 29 overlooking the mouth of the Halfway River. Stone’s sheep were observed individually and in small groups (2-3) grazing, bedding, travelling or dispersing. Four respondents had also seen Stone’s sheep in the region, but outside of the Peace River valley. Three respondents had heard second-hand of Stone’s sheep sightings within two kilometres of the Peace River Valley, between Farrell and Cache Creek.
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2.2.5 Summary
Based on the winter results, it is unlikely that Stone’s sheep are wintering in proximity to the potential Site C reservoir. This result is consistent with current knowledge of Stone’s sheep distribution in BC. Sheep have rarely been observed south of the Peace River and winter habitat in the area is considered marginal. Some of the recent sightings and the single ram that was harvested near Moberly Lake are believed to be the result of sheep transplantation to Mt. Frank Roy in the early nineties. Although Stone’s sheep are occasionally sighted in the Peace River valley in the growing season, they occur rarely and in small numbers.
2.3 UNGULATES
A summary of the previous ungulate studies that have been completed in the study area and the rationale for surveys are presented in Section 2.10 of Keystone Wildlife Research Ltd. (2009). This addendum provides a summary of the spring pellet surveys completed in June of 2009. The results of these surveys were not available in time for inclusion in Keystone Wildlife Research Ltd. (2009).
Ungulate pellet count transects were required in 2009 to:
• determine the relative use by ungulates of areas that may be disturbed by the potential Site C dam, compared to adjacent undisturbed habitats.
2.3.1 Introduction
Ungulates are hunted in the Peace River area and are important resources for local residents and First Nations. Species known to occur in the project area include mule deer (Odocoileus hemionus), white-tailed deer (Odocoileus virginianus), elk (Cervus canadensis) and moose (Alces americanus). These species are not provincially or federally at risk.
2.3.2 Methods
A detailed study area was identified within the Peace River Corridor to focus survey effort on ungulate winter ranges that may be affected during construction of the potential Site C dam. The study area was defined, at BC Hydro’s request, using potential footprint areas of the
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Site C Hydro Project Vegetation and Wildlife Report Addendum #1 potential dam site, disposal sites and granular investigation areas as provided in October 2008. All survey areas are within 3 km of the junction of the Moberly and Peace Rivers. Pellet transect survey methodologies followed those described in Ground-based Inventory Methods for Selected Ungulates: Moose, Elk, Deer (RIC 1998b). Data were used to provide baseline data for areas that may be affected by dam construction and for control sites, where no impacts are anticipated.
2.3.2.1. Inventory Methods
Survey methods included aerial surveys to obtain species population estimates for the identified winter ranges, track counts to provide comparative habitat use and pellet counts to determine durations of use by each species. The results of the aerial surveys and the winter track counts were reported in Keystone Wildlife Research Ltd. 2009; this addendum provides the results of the spring pellet surveys.
Winter Weather
Weather data were obtained from the Weather Office (www.weatheroffice.gc.ca) for the Fort St John airport station (ID: 1183000). Those data were used to update the Winter Severity Index (WSI; Keystone Wildlife Research Ltd. 2009) and provide snow depth information for the previous winter (2008/2009).
Pellet Surveys
Twelve transects were laid out in the study area to traverse both impact and no-impact (control) areas. Each transect was surveyed once in the spring, after the snow had melted.
Pellet transect surveys for relative abundance were completed according to Ground-based Inventory Methods for Selected Ungulates: Moose, Elk, Deer (RIC 1998b). Specifically, surveys followed the Thompson methodology as described in Stordeur (1984), one of the primary citations in the RIC standards.
Each transect consisted of stations spaced at 50 m intervals, and each station consisted of five subplots. One subplot was located centrally, at the 50 m mark, with the other four 10 m from
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Figure 2.3.2.1. Ungulate pellet count station with five subplots.
All of the pellet groups found within the five subplots were identified to species, classified as either old winter, new winter or spring (Freddy and Bowden 1983; Table 2.3.2.1) and counted.
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Pellets from white-tailed deer and mule deer could not be differentiated but were grouped together as ‘deer’. Significant trails (tracks) were also noted. Habitat information, including site series, structural stage, slope, slope position, canopy closure, aspect, percent cover of tree species by layer, and percent cover of forage (amount of browse) species by layer, was collected at 100 m intervals (i.e. every second station) or when there was a significant habitat change. Data were recorded on the standard Ground Inspection Form following provincial standards (BCMoE and BCMoF 1998).
Table 2.3.2.1. Differentiating pellet sign.
New Winter (<1 year) Old Winter (>1 year) 1. Colour usually dark, intense and uniform Colour usually faded and often “bleached” grey on at over entire pellet surface. Colour sometimes least 1 surface, resulting in a 2-tone colour effect. faded on portions of the pellet surface. 2. Sheen usually present on at least ½ of Sheen not usually present on pellet surfaces, but may pellet surface. occur on bottom or protected surfaces of pellets. 3. Cracking of pellet surface not uncommon, Cracking of pellet surface common, surface texture surface texture varied smooth to rough. usually rough. 4. Occasionally fungus or mould visibly Fungus or mould not present on pellet surfaces. present on pellet surfaces. 5. Pellets usually on surface of substrate. Pellets often embedded in duff or soil.
Limitations
The assumptions and limitations of pellet count techniques were reviewed and summarized by Neff (1968), and Kelsall and Simpson (1989). This model assumes that:
• pellet groups are deposited at random (pellet groups may not indicate relative habitat use since 30% of pellet deposition occurred while deer were travelling, which accounts for 4% of an animal’s day (Collins and Urness 1981))
• the defecation rate is accurate (constant average rate of pellet group deposition)
• no pellet groups were missed
• a pellet group was defined as >10 fecal pellets, the majority of which are inside the plot.
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• time period is well defined (old versus new winter distinction)
• size of plot is an efficient sampling unit.
The density of the ungulate species using an area can be estimated using average defecation rates from the literature, estimated duration of winter from weather data and observed pellet densities. The formula is shown below (Stordeur 1984);
wildlife population = [mean pellet groups/plot] x [size of area/size of plot] estimate (density) [deposition period] x [defecation rate]
The total observed pellet count (groups/50 m2) from each transect was used to estimate species densities (/km2). The time of deposition was assumed to be 6 months (180 days; November to April). Estimated defecation rates taken from Stordeur (1984) were: mule deer 15/day, elk 11/day, and moose 13/day. By determining the number of pellets expected to be present (defecation rate x defecation period), the number of pellets counted can be used to estimate animal density (/km2).
The negative binomial and Poisson distributions are usually used to describe the clumped distributions from count data (RIC 1998b). Data collected on transects were combined into habitat areas (warm aspects, flood plain, Moberly, and upland) relevant for the species being examined and the potential impact areas. The data was then analysed following methods from White and Eberhardt (1980). The output reveals whether pellet counts and distributions were significantly different between the control and impact (potential disturbance) areas.
2.3.3 Results
The location of ungulate pellet transects completed in 2009 is presented on Map 4.
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Winter Weather
The winter severity index (WSI; Keystone Wildlife Research Ltd. 2009) was 103, indicating that 2009 was a relatively severe winter. Snow began falling in November and was present on the ground until mid April (Figure 2.3.3). There were three periods of deep snow (>50 cm), when ungulate movements were limited: January 8th to 18th, January 28th to 29th, and Mar 18th to 31st. These snow conditions would be critical for deer, forcing them onto winter range and other areas where the snow depth is shallower (Ungulate Winter Range Technical Advisory Team 2005). These snow depths would be inhibiting for elk and nominal for moose movement, which would not affect the observed results for these species. These data confirm the deposition period of six months.
70 60 50 40 30 20
Snow depth (cm) 10 0
th th th h h
Nov 1st Jan 9th Feb 8th Apr 9th Nov 10thNov 20thNov 30thDec 10Dec 20Dec 30 Jan 19tJan 29t Feb 18thFeb 28thMar 10thMar 20thMar 30th Apr 19th
Figure 2.3.3. Winter (Nov 2008- Apr 2009) snow depths at the Fort St John airport (695 m).
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Map 4. Ungulate transect locations.
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Pellet Surveys
All 12 pellet transects were completed between June 12 and 17, 2009. No inclement weather conditions were experienced during surveys. In total, 196 deer pellet groups, 224 moose pellet groups and 105 elk pellet groups were counted over a total distance of 35.7 km. The majority of pellets were classified as new winter for all three species (Table 2.3.3a). Only new winter pellets were included in the pellet analysis to compare the relative use of habitat types and impact/control areas as they are representative of the previous winter. Moose were observed on all transects and elk and deer were observed on 11 of the 12 transects.
Table 2.3.3a. Numbers of ungulate pellet groups recorded during pellet count transects completed in 2009.
Season Deer Moose Elk Total Old Winter 11 25 2 38 Spring 18 4 18 40 New Winter 167 195 85 447 Total 196 224 105 525
Wildlife capability maps at 1:50,000 were produced for the area in the 1980s based on the biophysical habitat (Thompson and Harcombe 1980). These maps rank the habitat under optimal conditions (capability) for the various ungulate species (Table 2.3.3b, Demarchi et al. 1983). Habitat capability or suitability ratings rank the habitat against the highest capability habitat in the province (RIC 1999b). This ensures the habitat for any given species is rated consistently and uniformly from ecosystem to ecosystem and area to area across the province (RIC 1999b).
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Table 2.3.3b. Carrying capacity (animals per km2/year) by capability class (Demarchi et al. 1983).
Mule and % of Provincial Class Capability White-tailed Elk Moose Best Deer 1 Very High 76 - 150% 15.9 - 31.5 9.9 - 19.5 4.6 - 9.0 2 High 51 - 75% 10.7 - 15.8 6.5 - 9.8 3.1 - 4.5 3 Moderate 26 - 50% 5.4 - 10.6 3.4 - 6.5 1.6 - 3.0 4 Low 6 - 25% 1.2 - 5.3 0.8 - 3.3 0.4 - 1.5 5 Very low <5% <1.1 <0.7 <0.3 6 None 0% 0 0 0
In total, 220 visual plots were completed during spring surveys to record habitat attributes. The predominant habitat type present along most transects was young mesic aspen forest on gentle slopes (Table 2.3.3c). The capability classes varied between species, with the highest capability for moose assigned in the valley bottom polygons (Transect 8), deer capability highest on the warm aspect slopes (Transect 9, likely 4 and 14 as well) and elk capability also highest on warm aspect slopes, particularly around the Moberly River (Transect 9). Pellet sampling results confirmed the capability with Transect 9 having the highest density for elk, and transects 8, 10 and 13 having the higher moose densities. Transects 3, 4, 6 and 14 had higher densities of deer, but capability was not mapped on the north side of the Peace River. Transect 9 has highly capable deer habitat but only moderate densities were observed, likely due to competition with elk and the lack of cultivated fields.
Table 2.3.3c. Summary of major habitat types and habitat capability sampled along pellet transects in 2009.
Specific Habitat Structural Capability Transect Major Habitats Type Stages Class* 2 73% AM:ap Warm aspect Mostly Young N/A 37% AM:ap 3 Warm aspect Herb to Young N/A 29% WW 39% AM:ap 4 10% AMy:ap Warm aspect Shrub to Young N/A 18% WW 25% AM:ap 5 43% SH:ac Floodplain Young to Mature M3 E3 X2 11% SH
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Specific Habitat Structural Capability Transect Major Habitats Type Stages Class* 38% SH:ac 6 Floodplain Shrub to Mature N/A 51% WH 23% SH:ac 8 11% SO Floodplain Young to Mature M3 E3 X1 46% SC 56% AM:ap 1 1 2 9 Moberly Shrub to Young M E X 16% WW 49% AMk:ap 10 11% SH:ac Moberly Shrub to Young M2 E2 X2 11% AM 61% AM:ap 3 3 2 11 Cool upland Young to Mature M E X 18% AMk:ap
33% AM:ap 3 3 2 12 Cool upland Shrub to Mature M E X 20% SW:as
62% AM:ap 3 3 2 13 Cool upland Pole to Young M E X 12% AMy:ap 55% AM:ap 14 10% LL:ak Warm aspect Herb to Young N/A 10% CF *Capability classes (Thompson and Harcombe 1980) M – Mule Deer, E – Elk, X – Moose and superscripts refer to rating class (Table 2.3.3b).
Species- Specific Habitats
The twelve transects were combined for analysis based on species habitat values. Transects 2, 3, 4 and 14 were classified as warm aspect (high deer), transects 5, 6, and 8 were classified as low elevation floodplain (high moose), transects 9 and 10 were classified as Moberly (high elk), and transects 11, 12 and 13 were classified as cool aspect uplands.
The estimated deer density was highest for warm aspect slopes (Table 2.3.3d), perhaps due to the relatively low snow depths there (Figure 2.3.3). The warm aspect habitats are also located on the north side of the river, adjacent to high quality foraging habitat (cultivated fields). Elk densities were the highest around the Moberly, which is consistent with the capability mapping. Moose densities were above average along the Moberly, floodplain and upland habitats. Overall, moose density was highest since snow depths were not inhibiting for them.
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Table 2.3.3d. Relative ungulate densities (animals/km2/6 months ± 80% confidence intervals) by habitat group.
Habitat n Deer Density Elk Density Moose Density group (# pellet plots)
Floodplain 192 1.4 ± 0.8 0.6 ± 0.3 2.6 ± 0.7 Moberly 107 1.4 ± 0.3 4.9 ± 3.6 3.6 ± 1.8 Upland 177 1.1 ± 0.2 0.7 ± 0.3 2.4 ± 0.4 Warm 237 2.6 ± 0.4 0.4 ± 0.2 1.5 ± 0.5 Combined 713 1.8 ± 0.3 1.2 ± 0.6 2.3 ± 0.4
Transects were laid out to traverse both impact and control areas that were in close proximity with similar habitat types. Table 2.3.3e indicates that overall, the transects sampled roughly equivalent proportions of habitat classes in control and impact areas. This removes potential bias associated with differences in habitat between transects.
Table 2.3.3e. Relative proportion of habitats sampled in control and impact areas.
Habitat Control Impact Combined $01 AM:ap 33.1 % 43.1 % 37.3 % $01 AMk:ap 8.9 % 5.4 % 7.4 % $01 AMy:ap 3.4 % 5.4 % 4.2 % $07 SH:ac 8.2 % 17.7 % 12.2 % 00 WH 8.7 % 3.0 % 6.3 % 00 WW 8.9 % 1.3 % 5.8 % 06 SC 6.3 % 2.0 % 4.5 % Other 12.3 % 15.1 % 13.5 % (including non forested) Other (seral) 10.1 % 7.0 % 8.8 %
The pellet group data for each species were compared between impact (dam site, spoil, reservoir) and control (no-impact) areas. The binomial distribution of pellet count data was analysed using pellet analysis software (White and Eberhardt 1980). Results indicate that deer pellet counts were higher in control areas. There was no significant difference in moose or elk densities or dispersion between impact and control areas (Table 2.3.3f). The results for deer may have been influenced by the amount of warm aspect habitats sampled and higher deer
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Table 2.3.3f. Mean (m) and dispersion (k) values between the impact and control areas for each ungulate species.
Control (n=414) Impact (n=299) mi ≠ mc mi ≠ mc k ≠ k k = k Species m k m k i c i c Deer 0.32 0.7 0.12 1.1 n/a Accept Elk 0.14 0.2 0.09 0.2 Reject Reject Moose 0.29 0.6 0.25 1.4 Reject Reject
2.3.4 Summary
The results of pellet transects indicate that there is no difference in use between impact and control areas for elk and moose. The results showed that there was a difference in deer pellets between control and impact, with higher values in control areas outside the impact areas. This result is based on a single winter of surveys, during which snow conditions were severe. There are portions of valuable habitat that would be affected by the construction of the potential Site C dam, should it proceed. These areas include the warm aspect slopes for deer and the Moberly River breaks for elk. A broader study would be required to determine the relative value of these areas to others along the Peace River Corridor, and the potential impacts of habitat loss due to flooding of the potential Site C reservoir. The ungulate surveys methods (aerial counts, winter snow tracking, pellet counts) also provide a benchmark for future comparisons.
Information on habitat use in other seasons is limited, particularly regarding the significance of river islands to each species group. Radio - tracking of females during birthing seasons would provide data on the use of the islands for calving/fawning, which would enable more accurate assessment of the impact of loss of the river islands on ungulate recruitment in the Peace River valley.
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3.0 REFERENCES
Arthur, W.L. 2003. Peace Arm Stone Sheep Ungulate Winter Range (UWR) (U - 7 - 006) Report. Mackenzie Forest District, Omineca Region. Rept. to BC Ministry of Water, Land and Air Protection.
Backmeyer, R.J. May 2000. Seasonal Habitat Use and Movements of Transplanted and Source Herd Stone’s Sheep, Peace Arm of Williston Reservoir (1990 - 1994). Peace/Williston Fish and Wildlife Compensation Program Report No. 226.
Backmeyer, R.J. 1994. Peace Arm Williston Lake Wildlife Capability Ratings. Peace/Williston Fish and Wildlife Compensation Program Report No. 33.
BC Ministry of Environment. 2000. Thinhorn Sheep in BC: Ecology and Management. Brochure, BC Ministry of Environment, Victoria. B.C.
BC Ministry of Environment, Lands, and Parks, and BC Ministry of Forests. 1998. Field Manual for Describing Terrestrial Ecosystems. Land Management Handbook No. 25. Retrieved from: http://www.for.gov.bc.ca/ric/Pubs/teEcolo/fmdte/deif.htm
British Columbia Ministry of Water, Land and Air Protection. 2004. Accounts and Measures for Managing Identified Wildlife. Version 2004. Biodiversity Branch, Identified Wildlife Management Strategy, Victoria, BC.
Blood, D.A. 1991. Review of Ungulate Inventory, Game Harvest, and Trapline Catch Data for Land Surrounding the Site C Project. Second Draft. Rept. to BC Hydro and Power Authority.
Blood, D.A. 1979. Peace River Site C Hydroelectric Development Environmental and Socio - economic Assessment: Wildlife Sub - Report. Rept. to BC Hydro and Power Authority.
Collins, W.B. and J.P. Urness. 1981. Habitat preferences of mule deer as rated by pellet - group distributions. Journal of Wildlife Management 45(4): 969 - 972.
Demarchi, D.A., B. Fuhr, B.A. Pendergast, and A.C. Stewart. 1983. Wildlife Capability Classification for British Columbia: An ecological (biophysical) approach for ungulates. MoE Manual 4, BC Ministry of Environment, Province of British Columbia, Victoria.
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Demarchi, R.A. and C.L. Hartwig. 2004. Status of Thinhorn Sheep in British Columbia. B.C. Ministry of Water, Land and Air Protection, Biodiversity Branch, Victoria, BC. Wildlife Bulletin No. B - 119.
Fraker, M.A. and V.C. Hawkes (eds.). 2000. Peace River Wildlife Surveys: 1999. Prepared by TerraMar Environmental Research Ltd. and Robertson Environmental Services Ltd. for B.C. Hydro and Power Authority.
Freddy, D.J. and D.C. Bowden. 1983. Efficacy of permanent and temporary pellet plots in juniper - pinyon woodland. Journal of Wildlife Management 47(2): 512 – 516.
Kelsall, J.P. and K. Simpson. 1989. Pellet Sampling Methods for Mule Deer. Consultants report prepared for BC Ministry of Environment and Parks, Williams Lake.
Keystone Wildlife Research Ltd. 2009. Peace River Site C Hydro Project: Stage 2 baseline vegetation and wildlife report. Report to BC Hydro and Power Authority, Vancouver, BC.
Keystone Wildlife Research Ltd. 2008a. Peace River Wildlife Studies: Draft Species Accounts. Report to BC Hydro and Power Authority, Burnaby, BC.
Keystone Wildlife Research Ltd. 2008b. Terrestrial Ecosystem Mapping of the Peace River Study Area. Revised. Prepared for BC Hydro and Power Authority, Burnaby, BC.
Keystone Wildlife Research Ltd. 2006. Peace River Wildlife Surveys: 2006. Prepared for BC Hydro and Power Authority, Burnaby, BC.
Mowat, G. and D. Paetkau. 2002. Estimating marten Martes americana population size using hair capture and genetic tagging. Wildlife Biology 8:201–209.
Neff, D.J. 1968. The pellet - group count technique for big game trend, census, and distribution: a review. Journal of Wildlife Management 32(3): 597 – 614.
Paetkau, D. 2003. An empirical exploration of data quality in DNA-based population inventories. Molecular Ecology 12:1375–1387.
Poole, K.G., A.D. Porter, A. de Vries, C. Maundrell, S.D. Grindal, and C.C. St. Clair. 2004. Suitability of young deciduous - dominated forest for American marten and the effects of forest removal. Canadian Journal of Zoology 82: 423 - 435.
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Resources Inventory Committee (RIC). 1999a. Inventory Methods for Medium - sized Territorial Carnivores: Coyote, Red Fox, Lynx, Bobcat, Wolverine, Fisher & Badger. Version 2.0. Standards for Components of British Columbia's Biodiversity No. 25. BC Ministry of Environment, Lands and Parks. Resources Inventory Branch for the Terrestrial Ecosystems Task Force.
Resources Inventory Committee (RIC). 1999b. British Columbia Wildlife Habitat Ratings Standards. BC Ministry of Environment, Lands, and Parks, Resources Inventory Branch Victoria, BC.
Resources Inventory Committee (RIC). 1998a. Inventory Methods for Beaver and Muskrat. Version 2. Standards for Components of British Columbia’s Biodiversity No. 22. Province of British Columbia, Resources Inventory Committee.
Resources Inventory Committee (RIC). 1998b. Ground - Based Inventory Methods for Selected Ungulates (Moose, Elk and Deer). Version 2.0 Standards for Components of British Columbia’s Biodiversity # 33. BC Ministry of Environment, Lands and Parks. Resources Inventory Branch for the Terrestrial Ecosystems Task Force.
Shackleton, D. 1999. Hoofed Mammals of British Columbia. Royal British Columbia Museum Handbook. UBC Press, Vancouver, BC.
Simpson, K. 1991. Peace River Site C Hydroelectric Development Environmental Assessment: Consumptive Wildlife Resources. Report to BC Hydro Land Social Resources. Keystone Bio - Research, Surrey, BC.
Smith, J.K. 2002. Peace River Wildlife Survey November 2001. Report to Glacier Power Ltd. Letter.
Stordeur, L.A. (editor). 1984. Proceedings of a Seminar on Ungulate Pellet Group Sampling and Data Analysis Techniques. Research Branch, BC Ministry of Forests WHR - 7. Victoria, BC.
Thompson, C. and A.P. Harcombe. 1980. Vegetation Landscapes for the Pine - Moberly map area. http://a100.gov.bc.ca/pub/acat/public/viewReport.do?reportId=2153
Thurber Consultants Ltd. 1979. Peace River Site C Hydroelectric Development. Physical Environmental Impact Assessment. Report to BC Hydro and Power Authority.
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Thurber Consultants Ltd. 1976. Sites C & E Hydroelectric Development Proposals: Lower Peace River Environmental Study. Report to BC Hydro and Power Authority.
Thurber Consultants Ltd. 1973. Site One Development Environmental Impact Study. Report to BC Hydro and Power Authority.
Ungulate Winter Range Technical Advisory Team (UWRTAT). 2005. Desired Conditions for Mule Deer, Elk, and Moose Winter Range in the Southern Interior of British Columbia. BC Ministry of Water, Land and Air Protection, Biodiversity Branch, Victoria, BC. Wildlife Bulletin No. B - 120. 18 pp.
Weir, R. 2009. Fisher Ecology in the Kiskatinaw Plateau Ecosection. Year - end Report. Report to Louisiana - Pacific Canada Ltd, BC Ministry of Environment and EnCana.
Weir, R. 2008. Fisher Ecology in the Kiskatinaw Plateau Ecosection. Year - end Report. Report to Louisiana - Pacific Canada Ltd and BC Ministry of Environment.
Weir, R. 2007. Fisher Ecology in the Kiskatinaw Plateau Ecosection: Inventory and research year - end report. Report to Louisiana - Pacific Canada Ltd. and BC Ministry of Environment.
Weir, R. 2006. Fisher Ecology in the BWBS Zone 2006: Inventory and Research. Year - end Report. Report to Louisiana - Pacific Canada Ltd. and BC Ministry of Environment.
Weir, R. 2005. Fisher Ecology in the BWBS Zone 2005: Capture and radio - tagging. year - end report. Report to Louisiana - Pacific Canada Ltd.
Weir, R. 1995. Diet, Spatial Organization and Habitat Relationships of Fishers in South - central British Columbia. M. Sc. Thesis, Simon Fraser University.
Weir, R., and F. B. Corbould. 2008. Ecology of Fishers in the Sub - boreal Forests of Northcentral British Columbia: Final report for the Williston Fisher Inventory. Peace/Williston Fish and Wildlife Compensation Program, Prince George, British Columbia.
White, G.C. and L.E. Eberhardt. 1980. Statistical analysis of deer and elk pellet - group data. Journal of Wildlife Management 44(1):121 - 131.
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Wiacek, R. 1998. Peace River Fluctuating Flows Wildlife Impact Study. Prepared for BC Hydro. Revised by K. Simpson and L. Andrusiak, Keystone Wildlife Research Ltd.
Wood, M.D. 1995. Mount Frank Roy Stone's Sheep Transplant, March 1993. Peace/Williston Fish and Wildlife Compensation Program Report No. 47.
Wood, M.D. and P.E. Hengeveld. 1998. Mt. Frank Roy/Mt. Monteith Stone’s Sheep Transplant Evaluation. Peace/Williston Fish and Wildlife Compensation Program Report No. 174.
Zielinski, W.J., and R. L. Truex. 1995. Distinguishing tracks of closely-related species: marten and fisher. Journal of Wildlife Management 59:571-579.
4.0 PERSONAL COMMUNICATIONS
Rich Weir, Biologist, Artemis Consulting, April 2008.
Eric Lofroth, Biologist, BC Ministry of Environment, September 2008
Renee Ardill, Resident Trapper, November 2009
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5.0 APPENDICES
Appendix 1. Number of times hair sample stations were baited in the Peace River Corridor during 2008 - 2009. Station Label Oct-08 Nov-08 Dec-08 Jan-09 Feb-09 Mar-09 01L 2 2 1 1 1 2 01R 2 2 1 1 1 2 02L 2 2 1 1 1 2 02R 2 2 1 1 1 2 03L 2 2 1 1 1 2 03R 2 2 1 1 1 2 04L 2 2 1 1 1 2 04R 1 1 1 1 2 05L 2 2 1 1 1 2 05R 1 1 1 1 2 06L 1 1 1 1 2 06R 1 1 1 1 2 07L 2 2 1 1 1 2 07R 1 1 1 1 2 08L 2 2 1 1 1 2 08R 1 1 1 1 2 09L 2 1 1 1 1 2 09R 1 1 1 1 2 10L 2 1 1 1 1 2 10R 1 1 1 1 2 11L 2 1 1 1 2 11R 2 1 1 1 2 12 Halfway 2 1 1 1 1 2 13 Halfway 2 1 1 1 1 2 14 Halfway 1 1 1 1 2 15L 2 2 1 1 1 2 15R 2 1 1 1 2 15Rb 1 1 1 2 16L 2 1 1 1 2 16R 2 1 1 1 2
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Station Label Oct-08 Nov-08 Dec-08 Jan-09 Feb-09 Mar-09 17L 2 2 1 1 1 2 17R 2 1 1 1 2 18L 1 2 1 1 1 2 18R 2 1 1 1 2 19 Cache 1 1 1 1 1 2 20 Cache 1 1 1 1 2 21L 1 1 1 1 2 21R 2 1 1 1 2 22L 1 1 1 1 2 22R 2 1 1 1 2 23L 2 1 1 1 2 23R 2 1 1 1 2 24L 1 1 1 1 2 24R 2 1 1 1 2 25L 1 1 1 1 2 25R 2 1 1 1 2 26 Moberly 1 1 1 1 1 2 27 Moberly 1 1 1 1 1 2 Total 75 60 22 48 48 96
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Appendix 2. Number of hair samples collected at each hair - snagging box in the Peace River Corridor during 2009. Station Label Feb - 09 Mar - 09 Apr - 09 Total 01L 3 1 1 5 01R 4 1 5 10 02L 3 0 0 3 02R 0 5 0 5 03L 3 6 1 10 03R 0 6 1 7 04L 0 0 0 0 04R 6 6 6 18 05L 4 6 2 12 05R 6 6 6 18 06L 6 6 3 15 06R 6 5 5 16 07L 4 6 0 10 07R 6 5 6 17 08L 3 3 1 7 08R 6 6 6 18 09L 4 0 3 7 09R 6 6 5 17 10L 3 6 1 10 10R 5 6 4 15 11L 3 2 4 9 11R 6 3 6 15 12Halfway 5 3 3 11 13Halfway 5 6 6 17 14Halfway 4 6 5 15 15L 0 0 2 2 15R 1 0 2 3 15RB 6 1 6 13 16L 3 4 3 10 16R 6 5 2 13 17L 0 0 1 1 17R 1 5 5 11 18L 2 2 6 10 18R 2 6 3 11 19Cache 0 4 3 7 20Cache 4 3 0 7 21L 0 0 1 1 21R 6 3 6 15 22L 3 0 3 6 22R 4 6 5 15 23L 5 6 6 17
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Station Label Feb - 09 Mar - 09 Apr - 09 Total 23R 6 3 2 11 24L 3 3 6 12 24R 1 6 6 13 25L 3 6 6 15 25R 3 3 6 12 26Moberly 5 6 0 11 27Moberly 5 6 5 16 Total 170 184 165 519
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Appendix 3. Stone’s Sheep Questionnaire
Question Question Action Number 1 Have you ever seen or heard of Stone’s sheep • If you have seen Stone’s sheep go along or near (<2 km) the Peace River (lower to question 2. Halfway River, Cache Creek and Moberly • If you have heard of Stone’s sheep River) between Hudson Hope and Fort St. go to question 9. John? • If you have not seen or heard of sheep go to question 10 2 Where was it? Locate as specifically as possible using known landmarks for each group seen. 3 When was it? Date or best approximation 4 How many animals? Accurate count or estimate? 5 Sex and age of the groups? Count of lambs, ewes, rams or mature rams or mixed group 6 What were the animals doing when you saw them? Feeding, bedding, traveling, other 7 What type of habitat were they in? level/steep, grassland/forest 8 Any other note worthy of details of the sighting that you recollect? Predator activity, proximity to homes, agricultural land, use of domestic feed, interaction with domestic animals? 9 Who reported them to you? • Get name and phone number, call them and go to 1 • In case you cannot locate or contact the person, get some second hand details by following 2 - 8 above Information about observer 10 How long have you lived in the area? 11 How often do you travel through the Peace Valley (Hwy 29)? 12 What do you do for a living and for recreation? 13 Do you spend much time outdoors (hunting, hiking, horseback riding, boating, etc) where you might have opportunities to see sheep? 14 Do you work in the bush (driving, flying, riding, boating)? 15 What types of activities were you doing when you observed the sheep? 16 Are there any other people that you know that • Note names and contact might have seen Stone’s sheep? information.
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Appendix 4. Deer pellet group statistical analysis.
Pellet Group Data Analysis Package FORTRAN 77 Version of 15 Nov., 1984 Page 1
negative binomial frequencies read interactively
summary of frequency distributions
frequencies plot numb. i 0 1 2 3 4 5 6 ------+------1 impact i 266 29 4 0 0 0 0 2 control i 318 72 18 3 2 0 1
Pellet Group Data Analysis Package FORTRAN 77 Version of 15 Nov., 1984 Page 2
* * * * * a n a l y s i s o f n e g a t i v e b i n o m i a l p o p u l a t i o n s * * * * *
- - - separate estimates for each population - - -
population mean var(mean) lower ci upper ci k-hat var(k-hat) gof prob log-likelihood ------
1 .1237 .0005 .0818 .1657 1.1470 1.7663639 .4283 -116.5051 2 .3164 .0011 .2513 .3815 .7134 .51020291E-01 .7008 -300.0762 total -416.5813
- - - summary for populations assuming constant k - - -
population mean var(mean) lower ci upper ci k-hat var(k-hat) gof prob log-likelihood ------
1 .1237 .0005 .0807 .1668 .7489 .51461886E-01 .9124 -416.6814 2 .3164 .0011 .2518 .3811 .7489 .51461886E-01 .9124 -416.6814
- - - summary for combined populations - - -
population mean var(mean) lower ci upper ci k-hat var(k-hat) gof prob log-likelihood ------
combined populations .2356 .0005 .1935 .2777 .5960 .27469445E-01 .5814 -427.8578
- - - summary of populations assuming constant mean - - -
population mean var(mean) lower ci upper ci k-hat var(k-hat) gof prob log-likelihood ------
1 .2471 .0007 .1944 .2998 .3231 .42298584E-01 .0084 -427.4825 2 .2471 .0007 .1944 .2998 .6634 .43224825E-01 .0084 -427.4825
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Pellet Group Data Analysis Package FORTRAN 77 Version of 15 Nov., 1984 Page 3
* * * * * * * * * * * * * s u m m a r y o f t e s t r e s u l t s * * * * * * * * * * * * *
+------+ i i i m o d e l i s i i i i all populations different i i i i log likelihood is -416.581 i i i +------+ x x x x x x x x x x x x likelihood ratio test of x likelihood ratio test of all populations different x all populations different vs. x vs. separate m values, common k x separate k values, common m chi-square = .200 x chi-square = 21.802 degrees of freedom = 1 x degrees of freedom = 1 pr(larger chi-square) = .6546 x pr(larger chi-square) = .0000 x x x x x x x x x x x x +------+ x +------+ i i likelihood ratio test of i i i m o d e l i s i all populations different i m o d e l i s i i i vs. i i i separate m values, common k i all populations the same i separate k values, common m i i i chi-square = 22.553 i i i log likelihood is -416.681 i degrees of freedom = 2 i log likelihood is -427.482 i i i pr(larger chi-square) = .0000 i i +------+ x +------+ x x x x x x x x x x x x likelihood ratio test of x likelihood ratio test of separate m values, common k x separate k values, common m vs. x vs. all populations the same x all populations the same chi-square = 22.353 x chi-square = .751 degrees of freedom = 1 x degrees of freedom = 1 pr(larger chi-square) = .0000 x pr(larger chi-square) = .3863 x x x x x x x x x x x x +------+ i i i m o d e l i s i i i i all populations the same i i i i log likelihood is -427.858 i i i +------+ models are represented by boxes, with tests between models along the 'x' paths.
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Appendix 5. Elk pellet group statistical analysis.
Pellet Group Data Analysis Package FORTRAN 77 Version of 15 Nov., 1984 Page 1
negative binomial frequencies read interactively
summary of frequency distributions
frequencies plot numb. i 0 1 2 3 4 5 ------+------1 impact i 277 19 2 0 1 0 2 control i 373 31 6 2 1 1
Pellet Group Data Analysis Package FORTRAN 77 Version of 15 Nov., 1984 Page 2
* * * * * a n a l y s i s o f n e g a t i v e b i n o m i a l p o p u l a t i o n s * * * * *
- - - separate estimates for each population - - -
population mean var(mean) lower ci upper ci k-hat var(k-hat) gof prob log-likelihood ------
1 .0903 .0004 .0500 .1306 .2267 .18302825E-01 .4811 -91.26182 2 .1401 .0006 .0922 .1880 .1824 .39289649E-02 .6613 -168.3209 total -259.5827
- - - summary for populations assuming constant k - - -
population mean var(mean) lower ci upper ci k-hat var(k-hat) gof prob log-likelihood ------
1 .0903 .0004 .0490 .1316 .1933 .32861918E-02 .9020 -259.6342 2 .1401 .0006 .0927 .1875 .1933 .32861918E-02 .9020 -259.6342
- - - summary for combined populations - - -
population mean var(mean) lower ci upper ci k-hat var(k-hat) gof prob log-likelihood ------
combined populations .1192 .0003 .0868 .1517 .1860 .29927170E-02 .2221 -260.7920
- - - summary of populations assuming constant mean - - -
population mean var(mean) lower ci upper ci k-hat var(k-hat) gof prob log-likelihood ------
1 .1185 .0003 .0858 .1512 .2084 .15133134E-01 .4904 -260.7661 2 .1185 .0003 .0858 .1512 .1785 .37640662E-02 .4904 -260.7661
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Pellet Group Data Analysis Package FORTRAN 77 Version of 15 Nov., 1984 Page 3
* * * * * * * * * * * * * s u m m a r y o f t e s t r e s u l t s * * * * * * * * * * * * *
+------+ i i i m o d e l i s i i i I all populations different i i i i log likelihood is -259.583 i i i +------+ x x x x x x x x x x x x likelihood ratio test of x likelihood ratio test of all populations different x all populations different vs. x vs. separate m values, common k x separate k values, common m chi-square = .103 x chi-square = 2.367 degrees of freedom = 1 x degrees of freedom = 1 pr(larger chi-square) = .7484 x pr(larger chi-square) = .1240 x x x x x x x x x x x x +------+ x +------+ i i likelihood ratio test of i i i m o d e l i s i all populations different i m o d e l i s i i i vs. i i i separate m values, common k i all populations the same i separate k values, common m i i i chi-square = 2.418 i i i log likelihood is -259.634 i degrees of freedom = 2 i log likelihood is -260.766 i i i pr(larger chi-square) =.2984 i i +------+ x +------+ x x x x x x x x x x x x likelihood ratio test of x likelihood ratio test of separate m values, common k x separate k values, common m vs. x vs. all populations the same x all populations the same chi-square = 2.316 x chi-square = .052 degrees of freedom = 1 x degrees of freedom = 1 pr(larger chi-square) = .1281 x pr(larger chi-square) = .8200 x x x x x x x x x x x x +------+ i i i m o d e l i s i i i i all populations the same i i i i log likelihood is -260.792 i i i +------+ models are represented by boxes, with tests between models along the 'x' paths.
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PEACE RIVER SITE C HYDRO PROJECT
BASELINE VEGETATION AND WILDLIFE REPORT
ADDENDUM #2
2009 PEACE RIVER BAT STUDIES
Prepared for BC Hydro Site C Project by
Keystone Wildlife Research Ltd.
PEACE RIVER SITE C HYDRO PROJECT
BASELINE VEGETATION AND WILDLIFE REPORT
ADDENDUM #2
2009 PEACE RIVER BAT STUDIES
Prepared for BC Hydro Site C Project by Keystone Wildlife Research Ltd.
October 2009
Lead Author: Lorraine Andrusiak
Contributors: Lauren Simpson Chris Albrecht
Accepted by: Anré McIntosh (BC Hydro)
Site C Hydro Project 2009 Peace River Bat Studies
TABLE OF CONTENTS
1.0 INTRODUCTION ...... 11
2.0 STUDY AREA ...... 11
3.0 BACKGROUND ...... 12
4.0 METHODS...... 15
4.1 BAT CAPTURE...... 16 4.1.1 DNA Sampling ...... 18
4.2 RADIO TELEMETRY...... 19
4.3 BAT HABITAT ABUNDANCE AND DISTRIBUTION ...... 22
4.4 DATA ANALYSIS ...... 23 4.4.1 Capture Data Analysis...... 23 4.4.2 Roost Site Data Analysis...... 24
5.0 RESULTS...... 24
5.1 CAPTURE RESULTS...... 24
5.1.1 Sampling Effort ...... 25 5.1.2 Sampling Conditions...... 27 5.1.3 Habitats Sampled ...... 27 5.1.4 Species Captured ...... 29 5.1.5 Condition of Captured Bats ...... 32
5.2 RADIOTELEMETRY...... 32 5.2.1 Roost Descriptions ...... 34 5.2.2 Random Roost Tree Description ...... 38 5.2.3 Characteristics of Roost Stands ...... 43 5.2.4 VRI Characteristics of Roost Stands ...... 43
5.3 BAT HABITAT ABUNDANCE AND DISTRIBUTION ...... 47 5.3.1 Habitat Distribution ...... 51
6.0 DISCUSSION ...... 53
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6.1 BAT SPECIES INVENTORY ...... 53
6.2 BAT HABITAT ASSESSMENT ...... 54 6.2.1 Day and Maternity Roosts ...... 54 6.2.2 Night Roosts ...... 62
6.3 REVIEW OF KNOWN HABITAT USE BY NORTHERN MYOTIS ...... 63
6.4 TECHNICAL AND DATA LIMITATIONS...... 65
6.5 RECOMMENDATIONS FOR FUTURE WORK...... 66 6.5.1 Bat Survey of the Regional Study Area...... 66 6.5.2 Assessment of Bridge Night Roosts – Current Use and Success of Future Mitigation...... 67
7.0 LITERATURE CITED ...... 69
8.0 PERSONAL COMMUNICATIONS...... 80
LIST OF TABLES
Table 3.0. Bat species known present or potentially present in the Peace River area...... 14 Table 4.2. Scheme used to record the amount of clutter in front of the roost...... 21 Table 4.3. Habitat capability and suitability rating scheme (from RIC 1999)...... 22 Table 5.1.1. Mist-netting effort (m2-hr) completed in July 2009, by study area...... 25 Table 5.1.3a. Habitat types sampled during netting sessions...... 27 Table 5.1.3b. Bat captures by study area...... 28 Table 5.1.4a. Bats captured in 2009 mist-netting surveys, by study area...... 29 Table 5.1.4b. Net microsites where possible northern myotis were captured in 2009...... 31 Table 5.2a. Bats to which transmitters were attached...... 33 Table 5.2b. Summary of relocated bats...... 34 Table 5.2.1a. Characteristics of cutbank roosts located in 2009...... 35 Table 5.2.1b. Characteristics of roost trees used by three male bats (two little brown myotis, one little brown myotis/northern myotis)...... 36 Table 5.2.1c. Distance between capture site and roosts (including triangulated roosts) for little brown myotis and long-eared myotis complex captured in 2009...... 37 Table 5.2.1d. Maximum commuting distance between capture site and roosts (including triangulated roosts) for reproductively-active female little brown myotis and little brown myotis/northern myotis captured between 2006 and 2009...... 38
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Table 5.2.2a. Characteristics of roost trees used by one big brown bat, one little brown myotis/northern myotis, and one silver-haired bat. Numbers in brackets are averages...... 40 Table 5.2.2b. Characteristics of roost trees used by little brown myotis. Numbers in brackets are averages. 41 Table 5.2.4a. VRI polygons of Myotis roost trees located in 2006, 2008 and 2009...... 43 Table 5.2.4b. Little brown myotis roosts by VRI polygon tree species...... 45 Table 5.2.4c. Little brown myotis roosts by VRI vegetation type and cover type...... 45 Table 5.2.4d. Projected age of VRI polygons of little brown myotis roost trees located in 2006, 2008 and 2009. 47 Table 5.2.4e. VRI crown closure for little brown myotis roosts...... 47 Table 5.3a. Area of bat habitat (ha) by suitability and capability class within the Regional and Peace River Corridor study areas as mapped by the 1:50,000 biophysical mapping...... 48 Table 5.3b. Area of bat habitat (ha) by suitability and capability class in the Peace River Corridor as mapped by the 1:20,000 Terrestrial Ecosystem Mapping...... 50
List of Figures
Figure 1. Available mapping within the regional study area...... 13 Figure 5.1.1. Locations of 2009 netting sites...... 26 Figure 5.1.3. Bat capture success in 2009 in relation to habitat and netting effort...... 29 Figure 5.2.2. Habitats around roost trees of little brown myotis radiotracked in 2006 to 2009 by site series. 39 Figure 5.2.4. Roost sites of little brown myotis radiotracked in 2005, 2006 and 2008 by VRI projected stand height...... 46 Figure 5.3a. Suitable and capable bat feeding and reproducing habitat as predicted by the draft ratings and the 1:50,000 biophysical mapping...... 49 Figure 5.3b. Suitable and capable bat feeding and reproducing habitat in the PRC as predicted by the draft ratings and the 1:20,000 TEM...... 50
List of Maps
Map 1. Biophysical- Feeding Habitat Suitability
Map 2. Biophysical - Feeding Habitat Capability
Map 3. Biophysical - Reproducing Habitat Suitability
Map 4. Biophysical - Reproducing Habitat Capability
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Map 5. PRC - Feeding Habitat Suitability
Map 6. PRC - Feeding Habitat Capability
Map 7. PRC - Reproducing Habitat Suitability
Map 8. PRC - Reproducing Habitat Capability
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List of Acronyms
AB – Alberta
Ac – Balsam poplar (Populus balsamifera)
At- Trembling aspen (Populus tremuloides)
BC CDC – British Columbia Conservation Data Centre
BWBSmw1 – Boreal White and Black Spruce moist, warm Peace variant dbh – diameter at breast height
FD-G – Feeding during the Growing Season
GIF – Ground Inspection Form
HAP – Halfway Plateau
MoE – BC Ministry of Environment
MoF – BC Ministry of Forests
MYEV – Myotis evotis, long-eared myotis
MYLU – Myotis lucifugus, little brown myotis
MYSE – Myotis septentrionalis, northern myotis
PEL – Peace Lowland
PIT – Passive integrated transponder
Pl – Lodgepole pine (Pinus contorta)
PRC – Peace River Corridor
RB- Reproducing (birthing)
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RIC – Resources Inventory Committee (now renamed Resources Inventory Standards Committee)
RSA- Regional Study Area
Sw – White spruce (Picea glauca)
TEM – Terrestrial Ecosystem Mapping
USFWS- United States Fish and Wildlife Service
UTM – Universal Transverse Mercator
VRI – Vegetation Resources Inventory
WBWG – Western Bat Working Group
WNS – White-nose Syndrome
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Glossary
Anthropogenic – caused by activities of people
Blue List - species and subspecies of special concern (formerly vulnerable) in British Columbia
Cohort – a group of individuals as defined for data analysis purposes
Commuting – travelling between habitats
Coniferous – needle-leaved trees (e.g. white spruce)
Deciduous – broad-leaved trees (e.g. aspen, balsam poplar)
Guano – bat droppings
Hibernacula – plural of hibernaculum
Hibernaculum – a site where bats hibernate through the winter
Indigenous species – species native to BC that have not been introduced from other areas of the world
Mesic – having a well-balanced or moderate moisture supply, well-drained but usually moist throughout the growing season
Morphometric – measurements of body size
Myotis - any of the ‘mouse-eared’ bat species
Protected Area – federal and provincial parks, and ecological reserves
Riparian – used to describe habitat that is influenced by the presence of a waterbody
Seral – describes an intermediate stage found in ecological succession. In the Peace River Valley, it often indicates a deciduous-dominated forest
Snag – a standing dead tree
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Structural stage – numerical scale used in Terrestrial Ecosystem Mapping describing forest structure and how it changes with age. Structural stages include 1 (non- vegetated/sparse), 2 (herb), 3 (shrub), 4 (pole-sapling), 5 (young forest), 6 (mature forest) and 7 (old forest).
Taxa - Plural of ‘taxon’
Taxon – refers to either a species or subspecies unit
Taxonomy – the system of classification and naming of organisms
Tragus – a fleshy prominence at the base of the external ear
Volant – able to fly
Acknowledgements
Thanks to our field crew: Chris Albrecht, Melissa Flint, Mandy Kellner, Todd Kohler, Anré McIntosh, Lisa Rockwell, Mike Sarell, and Lauren Simpson. David Nagorsen provided helpful input into project planning. Purnima Govindarajulu (BC Ministry of Environment) and Laura Friis (BC Ministry of Environment -retired) facilitated DNA sampling. Bat capture was carried out under Wildlife Act Permit # FJ09-54479 and Park Use Permits #103838 and #103839. Anré McIntosh of BC Hydro provided project co-ordination. We greatly appreciate the private landowners who graciously allowed us to access their land. We thank BC Hydro and Power Authority for funding this project.
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EXECUTIVE SUMMARY
BC Hydro and Power Authority requested that Keystone Wildlife Research Ltd. continue bat sampling within the Peace River valley and surrounding regional study area. Previous bat sampling had been completed by Keystone in 2005, 2006 and 2008. Eight bat species, including the Blue-listed northern myotis (Myotis septentrionalis), are potentially present in the area, but DNA analysis is required to distinguish the northern myotis from the closely-related long-eared myotis (Myotis evotis). The objectives of the 2009 field program, as defined by BC Hydro, were to:
1. collect additional data on northern myotis occurrence and habitat use within the Project area; 2. begin to collect data on the northern myotis in the region; and, 3. assess bat habitat availability at a regional scale.
Bat capture was carried out at 15 different locations within a 60 km radius of Fort St. John between July 23 and 30, 2009. Two crews captured bats in mist-nets. Radiotransmitters were placed on northern myotis/long-eared myotis individuals and on little brown myotis in order to investigate roosting habitat use. DNA samples were taken from northern myotis/long-eared myotis to confirm species identification.
Sixteen crew-nights of netting were completed, 6 in the Peace River Corridor (PRC) and 10 in the Regional Study Area (RSA). In total, 85 captures of at least 5 species were recorded with 66 in the RSA and 19 in the PRC. Eight bats of the long-eared species complex (northern myotis/long-eared myotis) were captured, one in the PRC and the remainder in the RSA. Nine individuals were instrumented with transmitters in 2009, one within the PRC and the remaining eight in the RSA. Two were long-eared complex, three were little brown myotis/northern myotis, and four were little brown myotis. The bats that could be relocated (seven) were tracked from three to nine days. Twelve roosts were identified. Three roosts were in buildings (park outhouses), three were in cutbanks, two in trembling aspen snags, two in live aspens, and two in live balsam poplars.
Thirty-five tree roosts located for bats of all species instrumented in 2006, 2008 or 2009 were revisited in 2009. Twenty-five little brown myotis roost trees that were located
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Site C Hydro Project 2009 Peace River Bat Studies during the three years of telemetry in the Peace area, and for which random roost tree data were recorded, were analysed in detail. At the stand level, reproductively-active females showed selection for snags over live trees as roost trees and selected trees with more decay, fewer branches and foliage remaining and less bark remaining.
DNA analysis to confirm the species of captured bats must be completed in order to assess habitat use by northern myotis within the Peace area. DNA samples have been submitted to the provincial Ministry of Environment and the results are pending. A literature review of habitat use by northern myotis is presented.
Draft wildlife habitat ratings had been previously prepared for Reproducing-birthing and for Feeding during the Growing season for bats as a species group, using a six-class system. The draft bat habitat ratings were run on the 1:50,000 biophysical mapping (regional study area) and on the Terrestrial Ecosystem Mapping (Peace River Corridor) and the amounts of habitat in each capability and suitability class were summarized. Recommendations for future work are provided.
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1.0 INTRODUCTION
The Peace River valley is located in northeastern British Columbia. The river system has two existing hydroelectric developments, the W.A.C. Bennett Dam and the Peace Canyon Dam. Information on the bat species present and their habitat associations within the river corridor is required to assess the potential effects of the Site C dam, a third dam proposed on the Peace River, should that project proceed to Stage 3. Data on the bat species present and the suitability of habitat outside of the river corridor are needed in order to evaluate the availability of alternative habitat for the bat species known to use the river corridor.
BC Hydro and Power Authority (BC Hydro) requested bat survey work as part of baseline studies in the Peace River valley area. Three years of inventory work in the river valley has documented six bat species, as well as the possible identification of the Blue-listed northern myotis (Myotis septentrionalis) (Keystone Wildlife Research Ltd. 2009; Kellner and Simpson 2005; 2006). The scale of bat survey work was expanded in 2009 in order to investigate bat species presence and habitat use within the region, outside of the Peace River valley, as well as the continuation of inventory effort within the valley.
The objectives of the 2009 field program, as defined by BC Hydro, were to:
1. collect additional data on the Blue-listed northern myotis occurrence and habitat use within the Project area; 2. begin to collect data on the Blue-listed northern myotis in the region; and, 3. assess bat habitat availability at a regional scale.
2.0 STUDY AREA
Terrestrial Ecosystem Mapping (TEM) at 1:20,000 has been completed for the Peace River Corridor and related Transmission Line (Keystone Wildlife Research Ltd. 2008a). The extent of the TEM mapping for the Peace River valley will be referred to as the ‘Peace River Corridor’ (PRC) study area, and covers a 4-km wide strip centred along the Peace River (Figure 1). The regional study area (RSA) was defined as the extent of the
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existing 1:50,000 scale biophysical mapping (Lower Halfway, Fort St. John East, and Pine-Moberly projects) that was converted to TEM units (Figure 1). The RSA lies within the Peace Forest District in the Northern Interior Forest Region. The PRC is contained within the RSA.
Both the PRC and RSA fall within the Peace River Basin ecoregion. The Peace River Basin is a wide plain that lies between rolling uplands to the north and south, and is dissected by the Peace River and its tributaries (Demarchi 1996). The PRC study area lies within the Peace Lowlands (PEL) ecosection. The Peace Lowlands Ecosection is a blocky mountain area on the east side of the Rocky Mountains, with strong rainshadows (Demarchi 1996). A portion of the RSA lies within the Halfway Plateau (HAP) ecosection. A single biogeoclimatic subzone variant is present, the BWBSmw1 – Peace moist, warm Boreal White and Black Spruce (Delong 1990). Additional detail on the biophysical characteristics of the study area has been provided in Keystone Wildlife Research Ltd. (2008a).
3.0 BACKGROUND
Eight bat species are potentially present in the Peace region (Table 3.0). The northern myotis is Blue-listed (Special Concern) provincially; all the others are Yellow-listed (Not At Risk). Northern myotis cannot be reliably distinguished from long-eared myotis based on physical characteristics. DNA analysis is required to separate those two species. DNA work did not previously form a component of bat sampling in the Peace River area, so the field identifications of northern myotis in previous surveys are unconfirmed. Individuals whose species has not been confirmed via DNA typing are referred to as belonging to the ‘long-eared myotis complex’ of species.
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Figure 1. Available mapping within the regional study area. TEM is available for the Peace River Corridor and Transmission Line study areas.
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Table 3.0. Bat species known to be present or potentially present in the Peace River area.
Maximum BC Provincial Common Name Species Conservation Status Framework Priority Long-Eared Myotis Myotis evotis* Yellow 2 Little Brown Myotis Myotis lucifugus* Yellow 5 Northern Myotis Myotis septentrionalis* Blue 2 Long-legged Myotis Myotis volans* Yellow 2 Silver-haired bat Lasionycteris noctivagans* Yellow 2 Eastern Red Bat Lasiurus borealis No status n/a Big Brown Bat Eptesicus fuscus* Yellow 6 Hoary Bat Lasiurus cinereus* Yellow 2
*Captured in the area during previous surveys.
Five of the bat species known/potentially present are listed as Priority 2 (on a 6-class scale) by the BC Conservation Framework (Table 3.0). The framework ranks native species and ecosystems in terms of conservation priority and management action, thereby identifying appropriate conservation actions. Native species and ecosystems are ranked in terms of conservation priority on a scale of one to six, with one being the highest priority and six being the lowest.
All 8 bat species known/potentially present are insectivores and forage where insect densities are high, including open forests, over slow-moving water or ponds, and along cliffs. Many bats forage along edges and linear features such as lines of trees, cutblock edges or riparian forest (Holroyd 2005). Some of the species present in the Peace River area are strong, fast fliers that generally forage in open habitats (hoary bat and big brown bat). Others, such as the northern myotis, are slow, manoeuvrable fliers adapted to capture insects in spatially complex habitats such as within the forest canopy
(Patriquin and Barclay 2003; Norberg 1994).
All 8 species are known to roost in trees, with some also known to use buildings, rock crevices or cliffs. The limited research done to date in boreal forests on little brown myotis (M. lucifugus), northern myotis (M. septentrionalis), and silver-haired bats (L. noctivagans) suggests that these species roost mainly in dying or dead balsam poplar
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(Populus balsamifera) and trembling aspen (P. tremuloides) trees (Vonhof et al. 1997; Crampton and Barclay 1998). Roost microsites may include cracks, cavities, foliage clusters (for 2 species), and under loose bark, on trees or snags that are larger in height and diameter than other available wildlife trees, and are in older, more open forest stands (Barclay and Brigham 1996). Investigations of roost use in the Peace in 2006 and 2008 found that balsam poplars are important habitat features and are heavily used by roosting bats in this area (Kellner and Simpson 2006; Keystone Wildlife Research Ltd. 2009). That conclusion was supported by data from bat detectors showing high levels of bat activity at dusk in balsam poplar stands, indicating emergence of roosting bats. Cutbanks along the Peace River also provide important roosting habitat. Additional details on the taxonomy and biology of the bat species present or potentially present in the region have been provided in Keystone Wildlife Research Ltd. (2009).
4.0 METHODS
Due to the size of the study areas and the logistical difficulties of access, sampling was restricted to the north side of the Peace River near Fort St. John (within a 60 km radius). Mist-net surveys targeted potential bat habitat in each of the study areas. Potential netting sites were chosen through analysis of digital map data and digitized onto field maps. Map features that were considered included ecosystem map unit (TEM and biophysical), proximity of roads, and land ownership. Sites that appeared to have old roads and trails through dense shrub or tree vegetation were targeted, as northern myotis have often been captured at sites with these characteristics in other areas of their range. There is evidence that northern myotis may be captured more readily at interior forest sites compared to water sites and edges (Carroll et al. 2002). Nagorsen (pers. comm. 2008) reports M. septentrionalis were most frequently captured in the Hazelton area on trails or old roads with extensive canopy overhang and dense shrub understorey (cluttered sites), with nets < 1 m from the ground.
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4.1 BAT CAPTURE
Mist-netting was scheduled for late July to sample during the period when females were reproducing, in order to document maternity roost locations, if possible. Two capture crews were used for mist-netting, both based from Fort St. John for optimum coverage of the two study areas. All crew members handling bats had completed the rabies pre- exposure immunization series. Each netting location was normally sampled for one night, but netting locations with good capture success may have been sampled again (see Weller and Lee 2007). Field crews searched for netting sites in the afternoon to confirm their suitability and obtain permission from private property owners, if required, and returned in the early evening to set up nets.
Three to seven mist nets measuring 2.6 m high by 6, 9, or 18 m wide were set up across forest gaps and overgrown roads, under and over bridges and across trails at each sample site. Nets were set up during the daylight and were opened approximately ½ hour before sunset (2100 – 2230). A Ground Inspection Form (GIF) was filled out at each netting site to document the habitat, structural stage, and Universal Transverse Mercator (UTM) location. Weather conditions (temperature, wind, cloud cover, precipitation) were recorded at the beginning and end of each session (RIC 1998). The net configuration (number, sizes, locations) was recorded. Nets were opened shortly before dusk. Once opened, nets were checked at least every 5 minutes and closed when bats were no longer detected on handheld bat detectors (approximately 0200). Nets were also closed early if there were multiple captures and the time required to process animals made it difficult to check nets frequently. Bats that remain in mist nets for longer than a few minutes often chew their way out and escape, resulting in damage to the nets.
Bats were captured in mist nets, generally following procedures outlined by BC’s Resource Inventory Committee standards (RIC 1998). Some departures from RIC standards were made in accordance with the recently-released protocols for preventing the spread of white-nose syndrome (WNS). WNS is an emerging fungal pathogen that is lethal to bats. It was first documented in 2005 in the northeastern US, and has been
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spreading westward since (Blehert et al. 2009). The syndrome affects bats at hibernacula, primarily caves. Affected bats awaken from hibernation prematurely and appear to exhaust their fat reserves, become emaciated and exhibit abnormal behaviours such as flying outside in low temperatures during the winter. A white fungus, not previously known to science and now named Geomyces destructans, may be present on the faces and flight membranes of infected bats. The fungus damages the bats’ flight membranes, eventually making flight impossible. Most of the affected bats (80 to 95%) starve to death when they exhaust their fat reserves. Research is currently ongoing regarding the causes of WNS, but it is believed to threaten all North American bat populations.
WNS has not yet been documented in Canada, but the Western Bat Working Group (WBWG) has issued guidelines for bat researchers to minimize the potential spread of the fungus (WBWG 2009). Accordingly, all nets in which bats were captured, and all bat holding bags, were disinfected the following morning in a 10% bleach solution and allowed to air-dry in sunlight. All field gear that contacted bats (cutting boards, callipers et cetera) was disinfected with an alcohol wipe between bats, and the field crew used alcohol-based hand sanitizer between processing of individual bats.
The field protocol included examination of captured bats for signs of WNS (flaking/discoloured skin, loss of flight membranes, irregular tears and holes in flight membranes and other signs of fungal damage to skin). The flight membranes of captured bats were examined and their condition scored using the US Fish and Wildlife Service (USFWS) guide to bat wing damage (Reichard 2009; http://www.fws.gov/northeast/PDF/Reichard_Scarring%20index%20bat%20wings.pdf).
Captured bats were removed promptly from the nets and transferred to individual cloth bags until they could be processed. Data were recorded on RIC-standard data sheets customized for the project (RIC 1998). The following attributes of each captured bat were recorded:
• weight (g)
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• species • time of capture • capture mechanism (net length and position) • gender • age (adult/juvenile) • reproductive condition (nonbreeding, pregnant, lactating, post-lactating for females; non-reproductive, reproductive for males) • forearm length (mm) • ear length (mm) • wing damage index (Reichard 2009).
Bats of non-target species (i.e. those not considered for transmitter attachment) may not have been held for the full hour recommended in RIC (1998) before weighing, to minimize stress as per WBWG recommendations (WBWG 2009). Bats considered for transmitter attachment were held for at least 1 hour (to allow food to clear the digestive tract) before weighing to ensure that they met minimum weight criteria.
Each animal was identified to species (where possible) using published keys (Nagorsen 2002; Nagorsen and Brigham 1993) and instrumented bats were photographed. Age was determined based on the degree of ossification of the finger joints (RIC 1998). Reproductive condition was determined for males by the presence of enlarged testes, and for females, by visual examination and gentle palpation of the abdomen and nipples (Racey 1988). Bats were released on-site by allowing them to fly off the hand.
4.1.1 DNA Sampling
An ongoing project sponsored by the BC Ministry of Environment involved the collection of tissue samples, morphometric data and recordings of vocalizations of long-eared species complex bats for the purpose of developing field methods for distinguishing the species. Data were collected during fieldwork in the Peace River area and contributed to the Ministry’s project. DNA samples were collected from long-eared species complex bats, and from other individuals for whom field identification was difficult, following the
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procedure described in Lausen (2005). Samples were taken using sterile 2 mm biopsy punches. Both sides of the bat’s tail membrane were cleaned with alcohol. The bat was held gently against a cutting board while the punch was pressed firmly down onto the tail membrane, then lifted. The disk of tissue that resulted was removed from the cutting board with sterilized forceps and placed into a labelled vial of 95% ethanol. Additional data were recorded from individuals from which samples were taken:
• fur colour • ear colour • tragus length • tragus shape • jaw colour • thumb length • length of third and fifth metacarpals • width and length of unfurred patch on nose • slope of forehead • presence of facial mask • presence of long hair on the toes.
4.2 RADIO TELEMETRY
In order to locate day-roosts used by bats in the study areas, radio-tags (Holohil Systems Ltd.) were attached to suitable individuals. Northern myotis were prioritized for instrumentation as per the study objectives; but transmitters were also attached to little brown myotis, since few captures of the rare northern myotis were expected. Since it is difficult to distinguish between long-eared species (northern myotis and long-eared myotis) based on physical characteristics, DNA samples were collected from all probable long-eared species.
The suitability of adult bats for radio-tagging was assessed based on the following criteria (RIC 1998): species, gender, current reproductive condition, and the 5% rule, which suggests that transmitters should not exceed 5% of the animal’s body mass
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(Nagorsen and Brigham 1993). Holohil Systems BD-2N transmitters were used, which weigh 0.39 g; therefore, the minimum weight of a bat suitable for tagging was 7.8 grams. Juveniles, females in late stages of pregnancy, and any bats that appeared unusually stressed by capture were not tagged. The bat’s fur was clipped (if required) in the area below the shoulder blades where the transmitter was to be attached. A small amount of Skin Bond® or Torbot® cement was applied to the clipped area and to the transmitter, and allowed to stand for three minutes. The transmitter was then placed on the bat and held in place for 3 to 5 minutes. The transmitter was tugged gently to ensure it was firmly attached. Bats were released on-site once the glue had set.
Radio-tagged bats were tracked for as long as possible after capture, and were located daily whenever possible. Vehicle and foot access was used for most relocations. Road access is limited in some portions of the study areas, so a helicopter was used if radio- tagged bats could not be relocated from the ground. The bat’s general location was determined during the flight and if possible, the bat was relocated from the ground on the same day.
Roost sites were located by walking up to the site, or if access was unfeasible (e.g., across the Peace River or on private land), by triangulation from bearings taken at multiple locations where a strong signal was received. No private property was accessed without verbal permission from the land owner. Habitat characteristics (site series and structural stage) for each accessible roost were described by completion of a RIC-standard GIF form. The habitat type of inaccessible roosts was determined by plotting the bearings on the TEM map and identifying the habitat polygon or polygons where the bearings intersected. For inaccessible roosts, a UTM location was assigned based on triangulation data. Coordinates were placed in the approximate centre of the polygon drawn from bearings.
Roost trees were photographed and described using the methodology for describing wildlife trees in Field Manual for Describing Terrestrial Ecosystems (BC MELP and BC MoF 1998). The tree species, diameter at breast height, estimated height, percentage bark remaining, crown class (canopy position), appearance class, crown condition class,
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bark retention class and wood condition class was recorded for each roost tree. Orientation of the roost entrance was determined (when possible) with a compass. The amount of clutter in front of the roost entrance (when possible) was determined subjectively by assessment of the level of structural complexity within 1 m2 directly in front of the portion of the tree considered the roost-area entrance (Owen et al. 2002; Table 4.2).
Table 4.2. Scheme used to record the amount of clutter in front of the roost.
Complexity Value Definition
1 No vegetation in front of roost
2 Up to 25% of roost area obscured by vegetation
3 Up to 50% of roost area obscured by vegetation
4 Up to 75% of roost area obscured by vegetation
5 Roost area totally obscured by dense vegetation
Wildlife tree attributes were also measured at two randomly selected trees/snags at each positively identified roost tree site in order to assess roost tree preferences. A random bearing was chosen from the roost tree and the first live or dead tree encountered (within 2.5 m of the bearing line) at that bearing that was >20 cm dbh and >5 m tall (i.e. potentially large enough to be used as a roost; Jung et al. 2004) was recorded. A new random bearing was selected if no suitable tree was encountered along the original bearing within 200 m from the roost tree, or if the surveyor encountered a barrier (road, stream) or entered a different habitat type. This method implicitly assumes that the random trees are not used by bats as roosts, and that all roost trees are equally valuable (Willis et al. 2006). Random roost tree measurements were completed at all individual roost trees located from bats tracked in 2009 as well as roost trees from previous inventories (Keystone Wildlife Research Ltd. 2009; Kellner and Simpson 2006).
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Data recorded for non-tree roosts included UTM location, type of structure (cutbank, building, bridge etc.), and any evidence of use (guano, staining). Other data recorded for cutbank roosts included aspect, height of bank, and height of roost entrance (if known). All roosts were photographed, if possible.
4.3 BAT HABITAT ABUNDANCE AND DISTRIBUTION
Draft wildlife habitat suitability ratings (RIC 1999) have been prepared for bats in the Peace River Corridor (Keystone Wildlife Research Ltd. 2008b). Wildlife ratings can be used to summarize both habitat suitability and habitat capability. Habitat suitability is the ability of the habitat, in its current state (structural stage) to meet the needs of the species being rated. Capability is the maximum suitability possible for the habitat.
Draft ratings were prepared for Reproducing-birthing (RB) and for Feeding during the Growing season (FD-G) for bats as a species group, using a six-class system (Table 4.3). The ratings were based on the general habitat preferences of bats as a species group, due to lack of data on habitat use for each individual species at the scale of the mapping (see Craig and Wilson 2005). The highest ratings for RB were assigned to cutbanks and to mature and old (structural stages 6-7), moist to wet forests. The highest ratings for FD-G were applied to waterbodies and wetlands.
Table 4.3. Habitat capability and suitability rating scheme (from RIC 1999).
% of Provincial Best Rating Class 100% - 76% High 1 51% - 75% Moderately High 2 50% - 26% Moderate 3 25% - 6% Low 4 5% - 1% Very Low 5 0% Nil 6
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For comparative purposes, the draft ratings were run on both the 1:50,000 biophysical mapping and the 1:20,000 TEM. The biophysical mapping was originally completed over 30 years ago, and does not include more recent disturbances. Some updates were done to the biophysical mapping before the ratings were run. These include:
• Addition of structural stages to the non-forested units that had no age code. Cultivated Field (CF) and Sedge wetland (SE) were assigned structural stage 2 (herb), Gravel Bar (GB) and Cutbank (CB) were assigned structural stage 1 (nonvegetated), and Willow-Horsetail (WS) and Black Spruce-Tamarack (TS) were assigned to structural stage 3 (shrub)
• Floodplain polygons with no age code were updated to Gravel Bar (GB)
• large (>2 ha) Open Water (OW) polygons were updated to Lake (LA).
The ratings were run on the updated biophysical (includes both the RSA and the PRC) and on the TEM map (PRC). Ratings for complex polygons (those identified as containing two or three different ecosystems) were assigned using a weighted average of the ratings for the ecosystem components. Area summaries and habitat maps of both capability and suitability were prepared for each map base.
4.4 DATA ANALYSIS
Where applicable, data from previous inventories (Keystone Wildlife Research Ltd. 2009; Kellner and Simpson 2005, 2006) were pooled with the data collected in 2009 to increase the sample size and to provide context.
4.4.1 Capture Data Analysis
Bat captures were summarized by species, age, sex and reproductive condition. Netting effort was defined as a function of both area (m2) of net used and of the total time the nets were open (hours). The area of each net was calculated from its dimensions, then multiplied by the time the net was open. Netting effort per sampling site was the sum of
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all m2-hr of netting. Captures per unit effort (captures per net m2-hour) were calculated for each species, site, study area and overall.
4.4.2 Roost Site Data Analysis
Statistical analyses of continuous (i.e., measured) and ordinal (i.e., ranked) data were conducted using Kruskall-Wallis H-tests and Mann-Whitney U-tests. Nominal data (i.e., categorical, with no ranking) were analyzed using Fisher’s Exact Probability test due to low sample sizes.
Roost site locations were overlain onto the available Vegetation Resources Inventory (VRI) mapping for the study area. VRI mapping includes stand-level attributes that are not available in the TEM mapping and can be used to further characterize roosts.
5.0 RESULTS
5.1 CAPTURE RESULTS
Bat mist-netting took place from July 23 to 30, 2009. Two two-person crews, each at a different location, set up three to seven nets each night. Habitat types considered for netting sites included bridges, creeks, rivers, floodplain forests, roads and trails through mesic forest, forest edges and cutbanks. Initial site selection concentrated on old roads and trails through forest because these sites had increased capture success for long- eared species complex on the south coast of BC (D. Nagorsen, pers. comm.). However, low capture success in those habitats resulted in a shift of effort to forest gaps close to suitable roosting trees (old balsam poplar or aspen) or bridges used as night roosts. Nets were generally opened shortly before 2200 and were closed at approximately 0200, depending on the amount of bat activity at the site. Nets were closed early on three nights due to high numbers of captures, when crews could not continue to check nets while processing captured bats.
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5.1.1 Sampling Effort
Sixteen crew-nights of netting were completed, six in the PRC and ten in the RSA (Table 5.1.1; Figure 5.1.1). In total, 8068.6 m2-hr of netting effort was completed, 2312.9 in the PRC and the remainder in the RSA.
Table 5.1.1. Mist-netting effort (m2-hr) completed in July 2009, by study area.
PRC RSA Sample Sample Grand Total Date Netting Effort Stations Netting Effort Stations Netting Effort 09_LA_01 23-Jul-09 386.5 09_MK_01 386.5 09_LA_02 24-Jul-09 1260.2 09_MK_02 1260.2 09_LA_03 09_MK_03 25-Jul-09 760.2 760.2 26-Jul-09 526.5 09_LA_04 538.2 09_MK_04 1064.7 09_LA_05 27-Jul-09 1440.0 09_MK_05 1440.0 28-Jul-09 639.6 09_LA_06 464.1 09_MK_07 1103.7 09_LA_07 29-Jul-09 1027.7 09_MK_07 1027.7 09_LA_09 30-Jul-09 1025.7 09_MK_08 1025.7 Grand Total 2312.9 5755.8 8068.6
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Figure 5.1.1. Locations of 2009 netting sites.
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5.1.2 Sampling Conditions
Weather conditions during sampling were generally favourable, with light, intermittent rain showers recorded on only two survey nights. The rain showers did not affect sampling. Moon phases during sampling ranged from new moon through second quarter. Temperatures during netting sessions ranged from a high of 23oC to a low of 11oC.
5.1.3 Habitats Sampled
A variety of habitat types was sampled (Table 5.1.3a). Sampled habitats included upland seral aspen forest ($01 AM:ap), dry aspen shrub (00 AS), moist coniferous forest (07 SH), poplar floodplain (Fm02), cultivated field edge (CF), and bridges (river/road habitat – RI/RZ).
Table 5.1.3a. Habitat types sampled during netting sessions.
Sample Study Site Series Structural Description Station Site Series Name Area Symbol stage Label Bear Flats 09_MK_01 AS SwAt – Soopolallie 4 ActSw - Red-osier Fm02 Cache Creek 09_LA_04 dogwood 4 Cache Creek bridge 09_MK_03 RI/RZ River/road N/a Sw - Currant – PRC 07 SH Halfway R 09_LA_01 Horsetail 3 Halfway River bridge 09_LA_03 RI/RZ River/road N/a $At - Creamy peavine $01 AM:ap Site C north bank 09_LA_06 (seral association) 4 Site C north bank cutbank 09_LA_06b CB Cutbank 1 $At - Creamy peavine RSA $01 AM:ap Beatton Park 09_LA_02 (seral association) 4 CF Cultivated field 2 09_MK_06 bridge night roost* RI/RZ River/road N/a 09_MK_08 Cache Road bridge 09_MK_07 RI/RZ River/road N/a Charlie Lake campground* 09_MK_04 $At - Creamy peavine $01 AMy:ap (seral association) 09_MK_05 5
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Sample Study Site Series Structural Description Station Site Series Name Area Symbol stage Label ActSw - Red-osier Fm02 Halfway River Floodplain 09_LA_09 dogwood 4 Northern Lights College 09_LA_05 07 SH Spruce-horsetail 5 Robinson Road bridge 09_LA_07 RI/RZ River/road N/a $At - Creamy $01 AM:ap peavine (seral Red Creek 09_MK_02 association) 5 *repeat sample site
The greatest numbers of bats were captured at bridge night roosts (RI/RZ, Figure 5.1.3.). Capture success increased with increased netting effort (Figure 5.1.3b; moon phase and weather conditions are assumed to be similar for all sample nights and not to have affected capture success). Catch per unit effort was very similar between the two study areas; 0.0082 bats/m2-hr for the PRC and 0.0088 bats/m2-hr for the RSA (Table 5.1.3b; not including the second night of sampling at the two repeated sites).
Table 5.1.3b. Bat captures by study area.
Total Bats Netting Effort Catch Per Unit Effort (bats/m2-hr Study Area Captured* (m2-hr)* of net) PRC 19 2312.9 0.008215 RSA 39 4421.3 0.008821 *only the first night’s sampling results included for sites sampled >once, as capture results on the second night may have been affected by bats becoming familiar with the locations of the nets.
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0.016 2500.0
0.014 catch per unit effort sum of netting effort 2000.0 0.012
0.01 1500.0
0.008
1000.0 0.006 netting effort m2-hr #bats captured/m2-hr
0.004 500.0
0.002
0 0.0 $01 07 SH AS CB CF Fm02 RI/RZ AM:ap habitat
Only the first night’s results are included for sites that were sampled >once. See Table 5.1.3a for habitat definitions.
Figure 5.1.3. Bat capture success in 2009 in relation to habitat and netting effort.
5.1.4 Species Captured
In total, 85 captures of at least five species were recorded, 66 in the RSA and 19 in the PRC (Table 5.1.4a).
Table 5.1.4a. Bats captured in 2009 mist-netting surveys, by study area.
Study Area
Species Gender Reproductive Condition RSA PRC Total Big brown bat M Partially descended testes 1 1 Hoary bat M Abdominal testes 1 1
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Study Area
Species Gender Reproductive Condition RSA PRC Total Lactating 5 1 6 Non-reproductive (juvenile) 4 1 5 F Pregnant 10 10 Post-lactating 2 1 3 Nonbreeding 5 5 Little brown myotis Abdominal testes 11 1 12 Non-reproductive (juvenile) 3 1 4 M Partially descended testes 3 3 Scrotal testes 1 1 Unrecorded** 1 1 Unknown Myotis * F Unrecorded* 1 1 Non-reproductive (juvenile) 1 1 Pregnant 1 1 Northern myotis/ F long-eared Post-lactating 1 1 2 myotis*** Nonbreeding 1 1 Abdominal testes 1 1 M Non-reproductive (juvenile) 2 2 Northern F Lactating 3 3 myotis/little brown M Abdominal testes 3 3 myotis*** Lactating 7 7 Non-reproductive (juvenile) 1 1 Pregnant 1 1 F Long-legged Post-lactating 2 2 myotis Nonbreeding 5 5 Unrecorded 1 1 M Non-reproductive (juvenile) 1 1 Total 66 19 85 *escaped before processing; **found in closed net at end of session; ***species confirmation pending (DNA analysis)
Little brown myotis were the most commonly captured (50 captures; Table 5.1.4a). Eighteen long-legged myotis were captured, as well as one big brown bat and one hoary bat. Eight bats of the long-eared species complex (northern myotis/long-eared myotis – MYSE/MYEV) were captured, one in the PRC and the remainder in the RSA. An additional six bats were captured in the RSA that were difficult to identify in the field. They resembled little brown bats but had long and pointed ears typical of long-eared species (MYSE/MYLU). DNA samples were taken from those individuals as well as from
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the long-eared complex bats. DNA analysis will be used to confirm species (Zinck et al. 2004), and samples have been submitted to BC Ministry of Environment for analysis.
All of the bat species captured in 2009 had been captured in previous surveys in the PRC (Keystone Wildlife Research Ltd. 2009). One Myotis individual escaped before it could be identified to species. The silver-haired bat was the only species (to date; before DNA confirmation) known to be present in the study area that was not captured in 2009. The big brown bat was the only species captured in the PRC in 2009 that was not also captured in the RSA.
Of the 14 individuals identified as belonging to the long-eared species complex, 6 were captured in nets across road gaps in forested habitat, 5 at night roosts (2 picnic shelters and 1 bridge), 1 in a net across a meadow, and 1 in a shrubby Fm02 backchannel (Table 5.1.4b).
Table 5.1.4b. Net microsites where possible northern myotis were captured in 2009.
Sample Study Area Station Name Label Species (Field ID) Total Bats Net Microsite MYSE/MYEV 1 picnic shelter 2 across road gap, mesic forest 09_LA_02 MYSE/MYLU 1 picnic shelter 1 across road gap in Fm02 1 across road gap in Fm02 MYSE/MYEV RSA 09_LA_09 1 across road gap in Fm02 1 across road gap in Fm02 09_MK_04 MYSE/MYLU 1 picnic shelter 09_MK_05 MYSE/MYLU 1 across meadow 09_MK_06 MYSE/MYLU 1 below bridge 09_MK_08 MYSE/MYEV 2 bridge PRC 09_LA_04 MYSE/MYEV 1 Fm02
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5.1.5 Condition of Captured Bats
Most (69/84) of the bats processed were adults, although three juvenile long-legged myotis, three juvenile long-eared complex and nine juvenile little brown myotis were captured. No captured bats went into torpor during sampling. No bats were injured during capture or processing, although three were released before all measurements were completed, as they appeared unduly stressed during handling (e.g. rapid respiration, extreme struggling and vocalizing).
Testes of adult male vespertilionid bats descend from the abdomen to the scrotum only during the breeding season (fall). Most (17/22) of the adult male bats captured had abdominal testes, 1 little brown myotis had scrotal testes, and 3 little brown myotis and 1 big brown bat had partially-descended testes. Adult female little brown myotis were mostly pregnant (10) or lactating (6), with the remainder post-lactating (3) or nonbreeding (not pregnant, lactating or post-lactating; 5). In contrast, only 1 adult long- legged myotis was pregnant, while 7 were lactating and 2 post-lactating. An additional five female long-legged myotis were non-breeding. Adult long-eared complex females were pregnant (1), post-lactating (2), lactating (3) or nonbreeding (1).
No wing damage consistent with WNS (according to photos in Reichard 2009) was noted on any captured bats. Only minor injuries, such as slight wing tears, small punctures and faint, pale scar patches were observed on flight membranes. That damage is consistent with normal minor injuries common on flight membranes (Reichard 2009).
One or two DNA samples were taken from fourteen bats. Those samples were submitted to the Ministry of Environment for DNA analysis.
5.2 RADIOTELEMETRY
Nine individuals were instrumented with transmitters in 2009, one within the PRC and the remaining eight in the RSA. Two were long-eared complex (MYSE/MYEV), three
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were little brown myotis/northern myotis (MYSE/MYLU), and four were little brown myotis (MYLU; Table 5.2a).
Table 5.2a. Bats to which transmitters were attached.
Study Capture Reproductive Transmitter Netting Site Species Gender ID Area Date Condition Frequency RSA 09_LA_02 2009-07-24 MYSE/MYLU F Lactating NEL 150.317 RSA 09_LA_02 2009-07-24 MYSE/MYLU F Lactating SYS 150.538 PRC 09_LA_04 2009-07-26 MYSE/MYEV F Post-lactating MYR 150.438 RSA 09_LA_09 2009-07-31 MYSE/MYEV F Post-lactating XEN 150.338 Abdominal RSA 09_MK_05 2009-07-28 MYSE/MYLU M CEN 150.418 testicles Partially- RSA 09_MK_08 2009-07-30 MYLU M descended BIO 150.097 testicles RSA 09_MK_08 2009-07-30 MYLU F Nonbreeding BEA 150.038 Partially- RSA 09_MK-07 2009-07-29 MYLU M descended THE 150.077 testicles Partially- RSA 09_MK-07 2009-07-29 MYLU M descended DOB 150.117 testicles
The transmitter placed on one bat (XEN) was retrieved from the ground near the bat’s capture site the morning following its capture. One other bat (BEA) could not be relocated. The bats that could be relocated (7) were tracked from 3 to 9 days (Table 5.2b). Twelve roosts were identified. Three roosts were in buildings (park outhouses), three were in cutbanks, two in trembling aspen snags, two in live aspens, and two in live balsam poplars.
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Table 5.2b. Summary of relocated bats.
Days Tracked Number Bat Capture Number (first Roost Species Sex Different ID Date Relocations relocation Comments Roosts to last relocation) Northern Beatton Park NEL myotis / little F 2009-07-24 6 1 6* outhouse brown myotis Northern Beatton Park SYS myotis / little F 2009-07-24 6 2 6* outhouses brown myotis Long-eared MYR myotis F 2009-07-26 4 2* 6* Cutbanks complex Long-eared Dropped XEN myotis F 2009-07-31 0 0 0 transmitter; no complex relocations Northern CEN myotis / little M 2009-07-28 2 1 3** Aspen snag brown myotis 1Cutbank; Little brown BIO M 2009-07-30 5 2 5** 1 unknown myotis (triangulated) Little brown Could not be BEA F 2009-07-30 0 0 0 myotis relocated Live balsam Little brown THE M 2009-07-29 9 2 9 poplar myotis Live aspen Aspen snag Little brown Live aspen DOB M 2009-07-29 9 3 9 myotis Live balsam poplar *transmitter likely dropped; **signal lost after indicated number of days tracked.
5.2.1 Roost Descriptions
Anthropogenic Roosts
The two outhouses used as roosts by two lactating female little brown/northern myotis in Beatton Provincial Park were wooden structures located a few metres apart. Multiple bats could be heard vocalizing beneath the wooden siding forming the walls. One bat
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(SYS) moved from one outhouse to the other (first relocation to second relocation), after which her transmitter remained at the same location for the remaining four days for which it was monitored. A second bat (NEL) captured the same night as SYS was relocated in one of the outhouses the day after her capture; this transmitter never moved after that date. Both transmitters were detected in the outhouses between 2145 and 2315 on July 31, 2009, indicating that they had likely been detached from the bats because the transmitters did not leave the outhouses during normal bat foraging time, when NEL and SYS were expected to be away from their roost. The outhouses were the only roosts recorded for NEL and SYS.
Cutbank Roosts
One male little brown myotis and one female northern myotis/long-eared myotis roosted in two cutbank sites. The female roosted in a warm-aspect cutbank, approximately 100 m high, on the west bank of Cache Creek just north of the Peace River (Table 4.2.1a). The male roosted in a cutbank approximately 100 m in height, off St. John Creek (Beatton River). Both cutbanks had sparse shrub cover. Due to the inaccessibility of the roost sites, the microsite characteristics could not be measured, although crevices and holes were observed in the cutbanks.
Table 5.2.1a. Characteristics of cutbank roosts located in 2009.
Roost ID Species Gender Cutbank Cutbank Surrounding height (m) aspect Habitat (degrees) (ecosystem unit) MYR-2 Northern F 100 87 Fm02 myotis/little brown myotis BIO-2 Little brown myotis M 100 288 WW/AS
Tree Roosts
Three male bats in the RSA (two little brown myotis, one little brown myotis/northern myotis) used six tree roosts; two in trembling aspen snags, two in live aspen, and two in
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live balsam poplar (Table 5.2.1b). The largest aspen snag was a veteran, but the remaining roost trees were not.
Table 5.2.1b. Characteristics of roost trees used by three male bats (two little brown myotis, one little brown myotis/northern myotis).
Roost ID CEN-1 DOB-1 DOB-2 DOB-3 THE-1 THE-2 Habitat AMy:ap AM:ap SO SO AM:ap AM:ap Structural Stage 5 5 5 5 5 5 Stand height m 30 25 25 30 30 Roost type snag snag live tree live tree live tree live tree Balsam Tree species Aspen Aspen Aspen Balsam poplar poplar Aspen dbh cm 17 44.6 29.2 22.9 20.7 25.7 Crown Class Codominant Codominant Codominant Intermediate Codominant Codominant Vet Y or N N Y N N N N Tree height (m) 14 24 30 26 16 22 Height to live crown (m) n/a n/a 30 26 8 Appearance Class* 6 4 1 1 3 1 Crown Condition* 5 3 1 1 1 1 Bark Retention* 3 3 4 3 2 2 Wood Condition* 3 2 2 3 2 1 crack bark crack crack bark bark Potential Roost Microsites snag leaning Visible cavity against tree Clutter 0 2 2 4 3 2 *see Appendix 1 for definitions.
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Commuting Distances
The average distance between capture site and roost site for bats instrumented in 2009 ranged from 25 m for a lactating little brown myotis to 2.5 km for a male little brown myotis (Table 5.2.1c).
Table 5.2.1c. Distance between capture site and roosts (including triangulated roosts) for little brown myotis and long-eared myotis complex captured in 2009.
Distance from capture site (m) Average Reprod. Distance Bat ID Species Stage Gender Roost 1 Roost 2 Roost 3 (m) Little brown BIO M 797 361 579 myotis Northern CEN myotis / Little M 188 188 brown myotis Little brown DOB M 1816 1887 1887 1863 myotis Little brown THE M 2501 2501 2501 myotis Northern Post- MYR myotis /long- F 548 1969 1259 lactating eared myotis Northern NEL myotis/ Little Lactating F 254 254 brown myotis Northern SYS myotis / Little Lactating F 30 20 25 brown myotis
The largest sample sizes available for analysis of commuting distances are for female little brown myotis and little brown myotis/northern myotis complex. When maximum roost-to-capture-site distances from individuals captured in 2006, 2008 and 2009 are averaged, commuting distances for lactating females are the smallest (Table 5.2.1d; note that sample sizes are small).
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Table 5.2.1d. Maximum commuting distance between capture site and roosts (including triangulated roosts) for reproductively-active female little brown myotis and little brown myotis/northern myotis captured between 2006 and 2009.
Averaged maximum Reproductive Condition commuting distance (m) N (individuals) Lactating 385.9 6 Post-lactating 600.1 2 Pregnant 2083.4 1 Grand Total 622.2 9
5.2.2 Random Roost Tree Description
Thirty-five tree roosts located for bats of all species instrumented in 2006, 2008 or 2009 were revisited in 2009. For each individual roost, data was recorded on the roost trees as well as two random trees/snags in the same stand (see Methods section for more details), resulting in data from 70 random roost trees. Twenty-nine roost trees were located in the PRC study area and six in the RSA; these areas were not compared due to insufficient sample size.
Pooling of multiple species, genders and reproductive conditions to conduct detailed statistical analysis is not recommended for bats, as it can result in erroneous conclusions due to the inherent differences that may exist between these groups (Miller et al. 2003). For example, little brown myotis exhibited noticeable differences in habitat selection for roosting depending on their gender and reproductive condition (Figure 5.2.2).
To avoid bias from inappropriate pooling of data, all bat and tree roost data were divided into separate species, gender and reproductive condition groups. Upon division into these groups, all species groups with the exception of little brown myotis (all genders and reproductive conditions) had five or fewer roost sites and were deemed of
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insufficient sample size. Therefore, only little brown myotis roosts were used for detailed statistical analysis (N= 25). Data recorded for the 10 roost trees associated with the other species groups (one big brown bat, one little brown myotis/northern myotis, and one silver-haired bat) relocated over the three years of data collection are summarized in Table 5.2.2a.
9
Males 8 Female - Active Reprod. Cond.
Female - Inactive Reprod. Cond. 7
6
5
4 number roosts of 3
2
1
0 AM SO Fm02 $AM:ap $SH:ac site series
Figure 5.2.2. Habitats around roost trees of little brown myotis radiotracked in 2006 to 2009 by site series.
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Table 5.2.2a. Characteristics of roost trees used by one big brown bat, one little brown myotis/northern myotis, and one silver-haired bat. Numbers in brackets are averages.
Little brown myotis/ Species Big brown bat Silver-haired bat northern myotis Gender** Female Male Female Reproductive Active N/A Active Condition** No. of Roosts 5 1 4 Habitat AM:ap/Fm02 AM:ap Fm02 Structural Stage 5-6 (5.6) 5 3 Tree species Ac/At At Ac Dbh (cm) 27.4-39.9 (33.5) 17 43.5-85.0 (69.8) Tree height (m) 8.5-35.0 (17.3) 14 7.0-12.0 (10.5) Appearance Class* 2-6 (5) 6 6-7 (6.75) Crown Condition* 1-6 (4.25) 5 6 Bark Retention* 2-5 (3.25) 3 5-7 (6.5) Wood Condition* 1-5 (3.25) 3 8 *see Appendix 1 for definitions; **no other genders or reproductive conditions used tree roosts.
Twenty-five little brown myotis roost trees that were located during the three years of telemetry in the Peace area, and for which random roost tree data were recorded (50 random trees), formed the analysis data set. Eight of the roosts belonged to females classified as pregnant or lactating (female reproductively-active; FRA), nine roosts were of females classified as nonbreeding or post-lactating (female reproductively-inactive; FRI), and eight roosts were of males (male; M). Of the 25 roosts, 2 were in trembling aspen snags, 4 were in live trembling aspen, 10 were in balsam poplar snags and 9 were in live balsam poplar (Table 5.2.2b).
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Table 5.2.2b. Characteristics of roost trees used by little brown myotis. Numbers in brackets are averages.
Gender Female Female Male Reproductive Active (FRA) Inactive (FRI) N/A (M) Condition No. of Individuals 3 3 3 tracked No. of Roosts 8 9 8 Habitat Fm02 AM:ap/Fm02/SH:ac AM/Fm02/SO Structural Stage 4-6 (5.1) 3-6 (5.0) 5-6 (5.4) Tree species Ac Ac/At Ac/At DBH cm 45.9-81.2 (69.1) 23.1-82.0 (43.6) 20.7-133.0 (57.9) Tree height (m) 4.0-40.0 (22.5) 3.5-25.0 (14.3) 16.0-30.0 (22.3) Appearance Class* 2-7 (4.5) 2-7 (3.9) 1-4 (2.0) Crown Condition* 1-6 (4.3) 1-6 (3.2) 1-3 (1.5) Bark Retention* 2-6 (3.9) 2-5 (3.0) 2-4 (2.7) Wood Condition* 1-8 (4.1) 1-8 (3.6) 1-3 (2.0) *see Appendix 1 for definitions.
Little brown myotis were observed to roost in trees with different characteristics depending upon their cohort (i.e., defined for the purposes of this analysis by gender and reproductive condition). Reproductively active females (FRA) were only found roosting within balsam poplar trees, while reproductively inactive females (FRI) and males (M) were found roosting in trembling aspen as well as balsam poplar. This may be due to the habitats in which the bats were located, as FRA roosts were only located within Fm02 habitats where balsam poplar is very common (Figure 6.1.7.1), while many of the habitats in which FRI and M roosts were located have a much higher proportion of trembling aspen and fewer or no balsam poplar. Spatial autocorrelation (lack of independence between observations) is also present as individuals generally roost within a defined roosting area (often within the same stand), where trees are expected to have similar characteristics.
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FRA selected snags over live trees for roosting more often than M (p=0.020). FRA selected trees for roosting with more decay (U=55.0, n1=n2=8, p=0.007) and fewer branches/foliage (U=52.5, n1=n2=8, p=0.014) than those selected by M. FRI roosts were also found in trees with fewer branches/foliage than M (U=56.0, n1=9, n2=8, p=0.030).
Bark condition and wood condition didn’t differ between the cohort roosts (p>0.05). This is not unexpected since some form of bark loss or wood decay is generally required to provide the microhabitat features that provide roosting structures (loose bark and cavities). Roost tree dbh also did not significantly differ between cohorts (p>0.05), although the minimum dbh of trees used by FRI and M was much smaller than the minimum dbh of trees used by FRA (Table 6.1.7.2).
At the stand level, FRA showed selection for snags over live trees as roost trees (p=0.028). As a corollary, this cohort also selected trees with more decay (U=107.0, n1=8, n2=16, p=0.004), fewer branches and foliage remaining (U=96.5, n1=8, n2=16, p=0.022), and less bark remaining (U=105.5, n1=8, n2=16, p=0.005) than others available within the stand, indicating a preference for trees with more advanced decay. FRI also exhibited selection for trees within the stand that had more decay, and M selected for trees with less remaining bark, but those two cohorts did not show selection for any other attributes.
FRA did not select trees within the roost stand that were larger (height or dbh) than other trees within the stand (p>0.05). The lack of selection for larger trees may be explained by the selection of snags over live trees, since decaying snags may lose height (broken top) or diameter (lost bark) over time. FRA may also select roost stands with an abundance of large trees, so that the roost trees selected are not necessarily larger than their neighbours. FRI and M were found to roost in trees that were smaller (shorter height) than others available within roost stands (FRI: U=128.0, n1=9, n2=18, p=0.015;
M: U=93.5, n1=7, n2=16, p=0.012).
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5.2.3 Characteristics of Roost Stands
The six tree roosts of male little brown myotis discovered in 2009 were all in upland forest types (Trembling aspen-Creamy peavine - AM:ap, White spruce-Currant- Oak fern -SO; Table 5.2.4b). One roost site of a lactating female northern myotis/little brown myotis (MYR) was triangulated across the Peace River to a polygon of dry seral deciduous forest (Trembling aspen – Soopolallie- SW:as).
5.2.4 VRI Characteristics of Roost Stands
In order to evaluate the potential utility of the forest stand data provided by the VRI mapping, all roost locations documented in 2006, 2008 and 2009 were overlain on the VRI map. Sample sizes were very low for bats other than Myotis species so they were not considered, and all but one of the roosts of Myotis for whom species identification is unconfirmed were not in trees (either anthropogenic or cutbanks). Myotis roost site data included two triangulation locations and 30 located to individual trees. Not all fields within the VRI data were populated for each roost polygon.
A roost was defined as a spatial location used during the day by an individual bat for one or more days, so the single tree used by two radiotagged individuals was counted as two roosts. It is important to note that that the roosts are not independent and are not true replicates. Some degree of spatial autocorrelation exists between roost locations of an individual bat, which were often within the same VRI polygon (Table 5.2.4a). Therefore, results are presented as descriptive parameters only.
Table 5.2.4a. VRI polygons of Myotis roost trees located in 2006, 2008 and 2009.
VRI polygon number Bat Identifier Gender Number roost trees 104* BIO M 1 342 WIL M 3 402* BET F 1 405 BET F 1 406 NOR F 2
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VRI polygon number Bat Identifier Gender Number roost trees BET F 3 441 NOR F 2 BET F 1 442 FAW F 2 513 DOB M 3 516 THE M 2 LUC F 1 OPA F 1 523 RUB F 2 FAR F 1 524 LUC F 1 525 FAR F 1 579 FAR F 1 647 CEN M 1 678 LIZ F 1 9999 ALN M 1 Grand Total 32
*triangulated
The VRI analysis was conducted on a final dataset that included 21 roosts from 8 female little brown myotis (10 VRI polygons) and 11 roosts for 5 male little brown myotis and one male little brown/northern myotis (6 VRI polygons). Characteristics of VRI polygons overlapping with roost sites are summarized below. Samples are not independent and sample sizes were not sufficient to demonstrate statistical significance.
Both females and males used both deciduous and mixed forest polygons (Table 5.2.4b). Most roosts (14/33) were in open-canopy deciduous polygons (Table 5.2.4c).
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Table 5.2.4b. Little brown myotis roosts by VRI polygon tree species.
VRI Polygon Tree Species Females Males Total No data 10 4 14 Ac (Balsam poplar) 5 5 At (Trembling aspen) 1 4 5 AcAt (Balsam poplar/Trembling aspen) 2 2 Total roosts in deciduous polygons 8 4 12 Ac(Sw) (Balsam poplar/White spruce) 2 2 AcAt(Sw) (Balsam poplar-Trembling aspen/White spruce) 3 3 At(Pl) (Trembling aspen/lodgepole pine) 1 1 Total roosts in mixed forest polygons 3 3 6 Total 21 11 32
Table 5.2.4c. Little brown myotis roosts by VRI vegetation type and cover type.
VRI Level 4 VRI Females (number Males (number vegetation Vegetation Grand Total roosts) roosts) type cover type* No data 1 1 shrub low open 2 2 shrub low sparse 6 6 shrub tall dense 2 3 5 treed broadleaf dense 1 2 3 treed broadleaf open 9 5 14 treed broadleaf sparse 1 1 Grand Total 21 11 32 * Sparse -Tree cover is between 10% and 25% for Treed polygons, or between 20% and 25% for Shrub or Herb polygons. Open - Tree, shrub, or herb cover is between 26% and 60% crown closure for the polygon. Dense - Tree, shrub, or herb cover is between 61% and 100% crown closure for the polygon.
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Female little brown myotis of all reproductive classes tended to roost in stands that were taller than stands used by males (Figure 5.2.4). Roost stands used by females also tended to be older (Table 5.2.4d), as is expected as stand age and tree size are typically correlated. VRI crown closure (where available) tended to be high for roosts used by all bats (Table 5.2.4e).
6 Males
Lactating females
5 Post-lactating females
Nonreproductive females
4
3 number of roosts number
2
1
0 10-14.9 15-19.9 20-24.9 25-29.9 30+ projected height (m)
Figure 5.2.4. Roost sites of little brown myotis radiotracked in 2005, 2006 and 2008 by VRI projected stand height.
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Table 5.2.4d. Projected age of VRI polygons of little brown myotis roost trees located in 2006, 2008 and 2009.
Females Non- Projected age (yrs) Lactating reproductive Postlactating Males Total females females females No data 5 0 5 4 14 47 0 0 0 1 1 60 0 0 0 3 3 66 0 0 0 1 1 70 0 0 0 2 2 73 0 0 1 0 1 79 0 0 1 0 1 119 4 2 0 0 6 130 2 0 0 0 2 147 0 0 1 0 1 Total 11 2 8 11 32
Table 5.2.4e. VRI crown closure for little brown myotis roosts.
Females Crown Closure Post- Males Total Lactating Non-reproductive lactating No data 5 0 3 1 9 20 0 0 1 0 1 30 0 0 0 3 3 46 0 0 0 1 1 50 1 0 0 1 2 60 5 2 3 3 13 70 0 0 1 2 3 Total 11 2 8 11 32
5.3 BAT HABITAT ABUNDANCE AND DISTRIBUTION
Habitat suitability is the ability of the habitat, in its current state (structural stage) to meet the needs of the species being rated. Capability is the maximum suitability possible for the habitat. Both capability and suitability of habitats were assessed.
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The draft habitat ratings were run on the 1:50,000 biophysical mapping. This process identified over 13,000 ha of High (Class 1) suitability feeding habitat, but no High suitability reproducing habitat (Table 5.3a and Figure 5.3a). There are moderate amounts of Moderately High (Class 2) suitability feeding and reproducing habitat, and Moderate (Class 3) and Low (Class 4) form the majority of the remaining area for feeding suitability. Over 284,000 ha are Class 6 (Nil) suitability for reproducing, reflecting extensive areas of non-forested habitats such as cultivated fields and lakes.
Over 17,000 ha of High (Class 1) capability feeding habitat is present, as well as over 9,000 ha of High capability reproducing habitat. The average capability is higher than the average suitability within the study area, which is expected given that capability is the best possible habitat (ignoring forest succession due to disturbance, such as logging or fire) while suitability is the habitat currently present on the landscape; thus, suitability can never be higher than capability. The difference between average capable and suitable ratings reflects the disturbance history within the area. It is important to note that while some updates have been done to the biophysical mapping, additional updates are planned as future work, so these results should be considered preliminary.
Table 5.3a. Area of bat habitat (ha) by suitability and capability class within the Regional study areas as mapped by the 1:50,000 biophysical mapping.
Suitability Capability Description Class Reproducing- Reproducing- Feeding Feeding Birthing Birthing High Class 1 13506.0 0 17143.8 9274.1 Moderately Class 2 37527.5 58335.4 85839.5 195669.2 High Moderate Class 3 147089.6 101995.1 242227.9 92468.5 Low Class 4 198990.7 99750.7 196874.4 73258.9 Very Low Class 5 63636.7 3191.7 4689.0 9365.1 Nil Class 6 87236.1 284713.5 1211.9 167950.5 Total 547986.4 547986.4 547986.4 547986.4 Average 3.96 4.65 3.16 3.70 Class* * Weighted average of habitat classes based on polygon area.
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100%
Nil 80% Very Low
Low
60% Moderate
Moderately High High 40% % of total mapped area
20%
0% Suitability-Feeding Suitability - Reproducing Capability - Feeding Capability-Reproducing life requisite
Figure 5.3a. Suitable and capable bat feeding and reproducing habitat as predicted by the draft ratings and the 1:50,000 biophysical mapping.
The ratings run on the 1:20,000 TEM resulted in High (Class 1) feeding and reproducing habitat mapped within the Peace River Corridor (Table 5.3b; Figure 5.3b). Approximately half of the High and Moderately High (Class 1 and 2) capability reproducing habitat is currently mapped as High and Moderately High (Class 1 and 2) suitability reproducing habitat. Very little feeding habitat (682 ha) is rated as Nil (Class 6) capability, although considerably more (>21, 000 ha) is Nil (Class 6) suitability.
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Table 5.3b. Area of bat habitat (ha) by suitability and capability class in the Peace River Corridor as mapped by the 1:20,000 Terrestrial Ecosystem Mapping.
Suitability Capability Description Class Reproducing- Reproducing- Feeding Feeding Birthing Birthing High Class 1 1342.7 1298.7 1550.3 3500.6 Moderately Class 2 3124.0 14556.2 6286.9 31425.7 High Moderate Class 3 13640.3 6318.7 33881.6 5538.5 Low Class 4 12847.1 7714.7 16918.5 4613.0 Very Low Class 5 11697.7 381.2 4644.9 512.7 Nil Class 6 21313.3 33695.6 682.9 18374.5 Total 63965.1 63965.1 63965.1 63965.1 Average 4.48 4.44 3.29 3.35 Class* * Weighted average of habitat classes based on polygon area.
100%
90%
80%
70% Nil
60% Very Low Low 50% Moderate
40% Moderately High
percent of mapped area 30% High
20%
10%
0% Suitability-Feeding Suitability - Reproducing Capability - Feeding Capability-Reproducing life requisite
Figure 5.3b. Suitable and capable bat feeding and reproducing habitat in the PRC as predicted by the draft ratings and the 1:20,000 TEM.
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The current average suitabilities of both feeding and reproducing habitats in the PRC are much lower than the average capability. Considerably more Moderately High (Class 2) habitat is capable than is suitable.
5.3.1 Habitat Distribution
The distribution and spatial location of capable and suitable bat habitat are summarized below, and are presented on Maps 1-8.
Biophysical – Feeding Habitat Suitability
High suitability (Class 1 and 2) feeding habitat is concentrated in the western half of the regional study area, on the uplands between the Peace River and Moberly River, and between Halfway River and the Peace River (Map 1). Most of the moderate suitability (Class 3) feeding habitat east of Fort St. John is located on the uplands south of the Peace River.
Biophysical- Feeding Habitat Capability
Most of the highly (Class 1 and 2) capable feeding habitat is located on the western half of the regional study area, on the uplands between the Peace River and Moberly River, south of the Halfway River, and between the Pine and Moberly Rivers (Map 2). Little high capability habitat was mapped east of Fort St. John, except for small amounts along the Peace River. Moderate capability (Class 3) feeding habitat is also concentrated west of Fort St. John.
Biophysical – Reproducing Habitat Suitability
Moderately high and moderate (Class 2 and 3) suitability reproducing habitat is well distributed across the Regional study area (Map 3). No highly (Class 1) suitable habitat was mapped. There are extensive areas of Nil (Class 6) suitability, which are likely non- forested habitats (cultivated fields, wetlands, and shrub communities).
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Biophysical – Reproducing Habitat Capability
Highly (Class 1) capable reproducing habitat is located along major rivers (Peace, Halfway, Moberly; Map 4) and extensive contiguous areas of moderately high (Class 2) capability habitat are present west of Fort St. John. Smaller polygons of Class 2 habitat are distributed east of Fort St. John, interspersed with large areas of Nil (Class 6) capability reproducing habitat.
TEM - Feeding Habitat Suitability
Most of the highly (Class 1 or 2) suitable feeding habitat is currently located within the Peace River floodplain, with little present on the valley slopes (Map 5). High (Class 1) suitability habitat was also mapped along the eastern half of the transmission line route.
TEM - Feeding Habitat Capability
Most of the highest (Class 1 and 2) capability feeding habitat is located on the Peace River floodplain and in the wetlands on the transmission line (Map 6). Moderate capability (Class 3) feeding habitat was mapped throughout the length of the transmission line route and on the slopes of the Peace River valley.
TEM - Reproducing Habitat Suitability
Highly (Class 1 and 2) suitable reproducing habitat is well distributed along the PRC, in the river floodplain and along the valley slopes as well as along the powerline route (Map 7). Extensive areas of Nil (Class 6) suitability were mapped, mostly north of the Peace River where human activities such as agriculture are most intensive.
TEM - Reproducing Habitat Capability
Much of the TEM-mapped area is highly capable as bat reproducing habitat (Map 8). Only permanently non-forested areas (water bodies, cultivated fields, cutbanks, permanent shrub communities) are incapable of providing roosting habitat under optimum conditions.
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6.0 DISCUSSION
6.1 BAT SPECIES INVENTORY
All of the species detected are those expected to be present in the region based upon their ranges within the province and previous capture data (Keystone Wildlife Research 2009; BC Ministry of Environment 2008), although the status of two myotis species (long-e ared and northern myotis) is still to be confirmed. Physical characteristics of northern myotis, long-eared myotis and little brown myotis may overlap and field identifications may require revision based on DNA results (Haney et al. 2002). DNA samples from individuals of unconfirmed species have been submitted to BC MoE and results of those analyses are pending. Two big bat species (big brown bat and silver- haired bat) have not been captured in the RSA, though they are expected to be present based upon range and habitat. Both of those species have been reported from Bear Mountain, 14.5 km south of Dawson Creek (Hemmera 2006). Big brown bats are habitat generalists and have not been strongly associated with particular habitat types (Agosta 2002). Only seven silver-haired bats have been captured in 4 years of mist-net surveys in the PRC (2005, 2006, 2008 and 2009).
Weller and Lee (2007) suggested that at least 26 nights of mist-net surveys (a night is defined by them as any number of nets at a site for a night) were required to capture 8 out of 9 bat species in northwestern California, but that survey efficiency could be improved by focusing on productive (focal) sites. Some Peace River sites that were found to be particularly productive were sampled twice in 2009. Some other sites known to be productive from earlier surveys in the PRC in 2005, 2006 and 2008 (such as bridge night roosts), were also re-sampled in 2009 to maximize bat captures.
The bat species present in the study area are all termed ‘overdispersed’ species that roost at low densities in foliage, tree cavities and crevices (O’Shea et al. 2003). Standard inventory methods (bat capture) do not provide demographic information, since to monitor population numbers, capture data must be accompanied by the probability of
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capture of an individual. Capture probabilities within a single site are expected to vary with species, sex, reproductive class and age and as such, those data are rarely obtainable (Weller 2007; O’Shea et al. 2003).
6.2 BAT HABITAT ASSESSMENT
The major components of bat habitat include:
• maternity roosts where females give birth and/or care for dependent pups
• summer day roosts used by non-breeding individuals
• night roosts used between foraging bouts
• foraging habitat
• commuting habitat used for travelling between roosting and foraging areas
• winter hibernacula.
Draft maps of suitability and capability for foraging and reproducing habitat have been produ c ed. In general, suitability is considerably lower than capability within both the region and the Peace River corridor. Fire history and ongoing clearing for agriculture and oil and gas exploration have affected the availability of older forests that are most suitable for roosting. Management of habitat for bats must ensure that well distributed suitable habitat is available in the present, as well as plan for recruitment of suitable bat habitat in the future. Additional discussion of some specific bat habitats is presented below.
6.2.1 Day and Maternity Roosts
The availability of suitable roost trees is thought to be limiting to bat populations in some areas (Kunz and Lumsden 2003; Willis et al. 2003; Humphrey 1975). Although specific data on the effects of roost quality on individual bat fitness are scarce (Barclay and Kurta 2007), roosting habitat remains a critical resource (Kalcounis-Ruppell et al. 2005),
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regardless of whether roost availability is the primary limiting factor for bat populations in a given area.
Bats are believed to select roost sites primarily on the basis of microclimate, although there is little hard data to support this (Barclay and Kurta 2007). Tree roost microclimates are typically more stable than ambient temperature, and warm roosts may be particularly important to pregnant and lactating females (ibid.)
Bat tree-roosting habitat may be examined at a variety of scales. Fine-scale characteristics include those affecting the microclimate of the roost, such as cavity size, opening size and shape, number of openings, wall thickness, bark thickness, and roost aspect (Parsons et al. 2002). Characteristics at the tree level include tree species, tree condition (live/dead), amount of bark remaining, canopy class, tree dbh and tree height. Habitat type, stand age, amount of clutter, canopy closure and distance from suitable foraging habitat have been used to characterize roosting habitat at the stand level (Waldien et al. 2000; Campbell et al. 1996; Kunz 1982 cited in Agosta 2002). The characteristics of bat day-roosting habitat at all scales may vary by species (Lacki et al. 2007), sex (Perry and Thill 2007; Broders and Forbes 2004; Bogan et al. 2003), reproductive condition (Garroway and Broders 2008; Willis et al. 2006; Bogan et al. 2003), weather conditions (Willis and Brigham 2005) and season (O’Shea et al. 2003). It should be noted that the characteristics of cavity roost trees may also reflect the preferences of the primary cavity excavator (i.e. woodpeckers) rather than the bats that subsequently use them.
Roost Microsites
Roost microsites in trees include cavities, cracks, under bark or within deep bark fissures (Barclay and Kurta 2007). All of these microsites are potentially available on both living and dead trees.
Willis et al. (2006) reported that female big brown bats in the Cypress Hills of Alberta roosted in aspens with crevices and multiple holes more often than expected, and more than in aspens with single holes. Crevice trees were the most preferred roosts. In
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general, bat roost trees are large (greater dbh and height than surrounding trees), and project above the main canopy (Barclay and Kurta 2007). Roost trees in open areas with reduced amounts of clutter provide clear flight paths, which may be particularly important for newly volant pups (Garroway and Broders 2008; Campbell et al. 1996).
The densities of roost microsites within the Peace River study area are unknown, but will vary with stand age and history. Potential roost site density is generally thought to be greatest in mature and old forests (Crampton and Barclay 2008). Cavities created by fungi such as Phellinus spp. or Armillaria spp. require time to develop, and are thus more common in mature and older forests (Parsons et al. 2003). Swystun et al. (2007) investigated the availability of potential roost trees in riparian cottonwood (Populus deltoides) stands along the Missouri River. They reported that the densities of potential roost cavities did not differ between mature and old forests, and that bat activity (as measured by acoustic detection) was higher in mature forests than in either old or young forests. Suitable roost sites may also occur in younger stands. Fire history in the Peace region has resulted in shrubby, non-forested areas with multiple remnant snags, which were documented to provide suitable roosting microsites (Keystone Wildlife Research Ltd. 2009).
Older forests generally have larger trees, and larger snags are expected to offer proportionately more roost microsites and to remain standing longer than smaller- diameter snags. Snags in early to mid stages of decay generally provide the most roost microsites (Barclay and Kurta 2007). As many of the smaller bat species roost under exfoliating bark, ongoing bark loss may result in snags becoming less suitable for use as roosts over time (Barclay and Brigham 2001). Forestry techniques such as thinning may potentially enhance the production of large-diameter trees and snags across a landscape (Baker and Lacki 2006).
Cutbanks along rivers and creeks also provide roost sites, and were used by bats in 2006, 2008 and 2009 (Keystone Wildlife Research Ltd. 2009). Although cutbanks are also created from road cuts, to date, no bats have been documented roosting in road cutbanks in the Peace area. There are multiple roosting opportunities in the cutbanks
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present along the river, and these cutbanks are also used by Bank Swallows, which create additional microhabitat features with their nest burrows. Radiotransmitters on bats roosting in crevices within cutbanks along narrow gullies are difficult to locate from the ground or air due to the confined signal beam and rapid attenuation of the transmitter signal. It is possible that some of the bats that could not be relocated from 2006 to 2009 were roosting in deep cutbank crevices. Relocation success in 2008 was low for bats radiotagged around steep-sided, sparsely forested gullies such as Farrell Creek.
No data are available on the relative value of cutbank roosts versus tree roosts. Vertical cutbanks might provide greater protection from terrestrial predators than do tree roosts due to the difficulty in access, and the deeper crevices available. Cutbanks may also offer more stable temperatures and space for more individuals to aggregate. Conversely, cutbank crevices probably do not warm in the sun to the same degree as shallower tree cavity or under-bark roosts. Areas of obvious instability are present along the steep banks of the Peace River, but most cutbank crevices located above the high- water mark are likely relatively stable and have greater longevity as suitable roost sites than most tree cavities.
Slough (2009) observed reproductive female little brown myotis in the Yukon basking in the sun outside rock crevice day roosts, the first report of basking in any North American bat species. Basking could potentially be a thermoregulation strategy employed by bats in other northern areas, such as the Peace River, though to date it has not been reported outside of the Yukon.
Coloniality
Multiple bats were detected roosting behind the siding of the outhouses in Beatton Park that were used by two radio-tagged little brown myotis/northern myotis lactating females. Four additional communal little brown myotis day-roosts in anthropogenic structures were located in 2005 and 2008, under siding and roofs of buildings. Communal roosting was not confirmed for tree roosts in 2009, but was documented for three tree roosts in August 2006 (one roost) and 2008 (two roosts). Two of the three roosts were located by
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radiotracking a post-lactating female little brown myotis. Multiple bats (at least two) were observed and/or heard at those roosts. One roost site was under loose bark on a balsam poplar snag, and the other was in a crack in a live aspen. Trees with vertical cracks may be particularly valuable as communal roosts (Willis et al. 2006). Psyllakis and Brigham (2006) located 11 communal tree roosts of Myotis spp. in sub-boreal forests, all in vertical cracks. Crevices/cracks may provide a larger ratio of roost substrate (wood surface) to air volume than other types of tree roost, resulting in greater thermal advantages for colonially roosting bats. The remaining known communal roost from 2008, also in a balsam poplar snag, was used simultaneously for at least one night by two radiotagged lactating little brown myotis. The same tree had been used on the previous night by a third radiotagged lactating little brown myotis.
Occupancy of a single roost by multiple bats (colonial roosting) is thought to offer thermoregulatory advantages (Willis and Brigham 2007). Garroway and Broders (2007) investigated colonial roosting by lactating female northern myotis in Nova Scotia. They counted 1 to 67 individuals emerging from individual roost sites. Bats at colony roosts actively associated with each other, although the composition of roosting groups as a whole was ‘largely ephemeral’. Subgroups of two to nine individuals were more stable and remained associated at roosts throughout the season. Associations were strongest during lactation, and the authors suggested that the benefits of subgroup cohesion might extend beyond thermoregulatory advantages, although they were not able to document any instances of mutualistic or co-operative behaviours. Passive aggregation (a number of bats choosing a particular roost for its favourable characteristics) could also explain some communal roosting (Willis et al. 2006). Willis et al. (2006) reported that female big brown bats in the Cypress Hills of Alberta roosted in larger cavities more than expected, possibly because more bats could occupy them compared to smaller cavities.
Roost Fidelity and Roost Switching
Tree-roosting bats typically switch roosts (on average every 2.5 days), so each individual bat requires multiple roost sites within its home range (Barclay and Kurta 2007). The value (suitability) of particular trees can be inferred from repeated use, specifically,
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individual bats returning to specific roost trees after roosting elsewhere. Return to previously used roost trees was observed for six radiotagged bats in the Peace River Corridor in 2006 (one male big brown bat, one male little brown myotis (2 roost trees), one lactating silver-haired bat, and three female little brown myotis, two post-lactating and one nonbreeding), and one bat radio-tagged in 2008 (a lactating little brown myotis). Return to familiar roosts enables an individual to avoid the energetic costs of searching for new, suitable roosts (Veilleux and Veilleux 2004 cited in Arnold 2007).
Although there are benefits from returning to suitable, previously used roosts, there are also potential benefits from using alternate roosts. Roost switching may allow bats to (Lacki et al. 2007; Bogan et al. 2003; Kurta et al. 2002; Lewis 1995):
• gain and maintain knowledge about locations of alternate roosts,
• choose the optimum roost site in response to ambient weather conditions,
• take advantage of spatially separated, sporadically productive foraging sites,
• develop and maintain social relationships,
• prevent parasite build-up, and
• avoid predators.
Relatively little evidence has been published in support of any of these theories (Barclay and Kurta 2007).
Although most species of cavity-roosting bats frequently switch roost sites, they usually remain within a particular, relatively small roosting area (review in Barclay and Kurta 2007; B aker and Lacki 2006; Willis et al. 2006; Willis and Brigham 2004; Vonhof and Barclay 1996) and will often re-use trees within that area (Willis et al. 2003). Most of the publish e d data suggests that roost site choice occurs at the stand level (Brigham 2007). Trees within the same stand and with the same stand history are more likely to share
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species, size and structure characteristics that result in suitable roosting habitat (Barclay and Kurta 2007).
Alternate roost sites of instrumented bats in the Peace River area were only an average of 347 m apart (Keystone Wildlife Research Ltd. 2009), so it is not likely that roost switching occurred in response to spatio-temporal changes in food resources. Roost- switching as an anti-predator and/or anti-parasite strategy also seems improbable, as some roost trees were re-used within one or two days. Roost area (a polygon created by joining all known roost sites) of individual reproductively active female little brown myotis in the PRC ranged from 0.5 ha (4 roosts) to 29.4 ha (6 roosts; Keystone Wildlife Research Ltd. 2009). The size of an individual’s roosting area likely depends on the availability of quality roost sites (Barclay and Kurta 2007).
Bats may return to the same roosting area year after year, although multi-year data on roost site use by individuals are rare (Barclay and Kurta 2007). Foster and Kurta (1999) documented between-year re-use of particular roost trees by northern myotis. Given the long life spans of many bat species (over 31 years for little brown myotis (Fenton and Barclay 1980), 18.5 years for northern myotis (Caceres and Barclay 2000)) and their documented fidelity to hibernacula, inter-annual return to a distinct roosting area does not seem implausible. Some authors (Garroway and Broders 2008; Barclay and Kurta 2007; Willis et al. 2006) suggest that forest roosting areas be defined as ‘habitat areas’ for bat colonies and that management activities be applied at the scale of the roosting area (landscape scale) rather than at the level of the individual tree. That approach is consistent with the use of habitat mapping to monitor the supply and distribution of suitable roosting habitat in the Peace River area.
Roost Stands
Within the Peace River study area, roost trees of female little brown myotis were mainly located in VRI polygons classified as shrubs with sparse coverage (remnant snags in stands with fire history), or open (26% - 60% crown closure) deciduous forest. Females tended to use deciduous forest more than mixed forest, while males used deciduous and
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mixed forest approximately equally. Small sample sizes prevent assessment of statistical significance. Other possible confounding factors include the relatively low abundance of coniferous trees in the study area, and spatial autocorrelation of roost sites of individuals. Broders and Forbes (2004) found that male little brown myotis roosted more often in mixed and coniferous stands than in deciduous stands in New Brunswick. Jung et al. (2004) reported that male little brown myotis and northern myotis roosted in upland habitats away from water in Ontario.
In the Peace area, there also appeared to be a trend for male little brown myotis to roost within polygons with smaller, younger trees than did females; though sample sizes were too small to test for significance. Studies of roosting habitat generally emphasize roosts used by reproductively active females, as breeding females are thought to be the most constrained to particular roost characteristics. Nevertheless, habitat suitable for roosting by all genders and life stages must be available in an area for complete bat populations to be maintained (Barclay and Kurta 2007).
Almost half of the female little brown myotis roosts (10/21) were in polygons typed as ‘shrub’ rather than ‘treed’. Of the five of those ten roosts for which the individual tree was confirmed, four were snags that had persisted in the shrub polygon after burning. Young age class polygons can provide roosts suitable for bats if remnant snags are present, but the data field for snag density (DEAD_STEMS) is not populated in the VRI mapping of the study area. The data for the shrub height and shrub canopy closure fields were also missing in the VRI mapping. Examination of shrub polygons with a stand history of burning may identify young stands with snag features that are suitable for bat roosting.
Craig and Wilson (2005) identified characteristics of stands with high suitability for bat day roosting in British Columbia as:
• Coniferous forest stands >120 years old (or stands 81-120 years old where veteran trees were present), or deciduous/mixed stands >80 years old;
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• Stands >19.4 m in height;
• Presence of tree species known to be used for roosting by bats; and,
• Crown closure 16-65%.
That model was based upon forest inventory mapping, and the authors noted that the model could be used for assessment of forested stands where stand height was known. Assessment of the suitability of younger stands was dependent on knowledge of veteran tree p re sence.
Kalcounis-Ruppell et al. (2005) conducted a meta-analysis of multiple studies comparing characteristics of cavity roost trees to random trees for North American bat species. The scale of the roost/random tree selection varied between studies (landscape level vs. plot or stand level). They concluded that, in comparison with random trees, roost trees in general were taller, had larger dbh, were in more open canopy, and were in stands with more snags per hectare that were closer to water. Although the roosting habitat analysis of the Peace River data is hampered by small sample size, the general patterns observed appear to be consistent with that reported in the literature.
6.2.2 Night Roosts
Night roosting habitat was not specifically targeted as a subject of the 2009 work. Night roosts provide secure sites where bats can rest and digest their prey between feeding bouts, and may provide thermal advantages, especially on cooler nights (Adam and Hayes 2000; Barclay 1982; Kunz 1982 cited in Agosta 2002). Anthropogenic night roosts discovered during previous years’ inventory work were included in sites mist- netted in 2009. The bridges in the Peace River area (Highway 97 over Farrell Creek and Cache Creek) are valuable night roosts for a variety of bat species, including northern myotis (pending DNA confirmation), little brown myotis, and long-legged myotis. Big brown bats may also use bridges (Keely and Tuttle 1999) although none have been captured under bridges during mist-netting in the Peace River Corridor. Concrete and metal bridges absorb heat during the day and remain warm well into the night.
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Other night roosts located in 2009 include picnic shelters in Beatton Provincial Park and Charlie Lake campground. Multiple bats were captured in mist-nets deployed at those structures. Bats that use anthropogenic structures as night roosts often show higher fidelity to them than to other types of night roost (Lewis 1995), possibly due to their size, thermal characteristics and/or permanence on the landscape. Trees and warm-aspect rock crevices are also likely to be used as night roosts by small groups of bats in the PRC and RSA study areas, but anthropogenic structure roosts were the most accessible and easily detectible by surveyors.
6.3 REVIEW OF KNOWN HABITAT USE BY NORTHERN MYOTIS
One of the objectives of the 2009 bat survey was to investigate habitat use by the Blue- listed northern myotis in the PRC and in the RSA. This section will be revised once DNA test results are known and the species identification of radiotagged individuals is confirmed. Habitat associations of this species as reported in the literature must be interpreted with caution as few studies have included DNA testing to confirm identification of northern myotis where it occurs with other species that it closely resembles.
The northern myotis is distributed across North America from as far north as the Yukon (Slough and Jung 2008) east to Newfoundland and south to Florida (Caceres and Barclay 2000). The northern myotis has been defined as a forest-dependent species that forages and travels preferentially in forested habitats (Henderson and Broders 2008; Jung et al. 1999). The species’ presence has been correlated with the area of deciduous stands in maritime Canada (Henderson et al. 2008). Henderson and Broders (2008) reported that northern myotis on Prince Edward Island were detected a maximum of 78 m away from forested habitat. Foraging areas were concentrated along forested creeks, and females preferred deciduous roost trees in the interior of deciduous- dominated stands, but also used an anthropogenic (barn) roost. In the United States,
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northern myotis foraged in both upland forest and riparian forest, primarily on moths and beetles (reviewed in Schmidt 2003).
Northern myotis roost in a variety of tree species and types across their range, likely responding to the availability of suitable roost microsites rather than to particular tree species (Henderson et al. 2008). Although most bat species are reported to roost in larger-than-average trees, Owen et al. (2002) found that reproductively active female northern myotis in West Virginia roosted in trees that were smaller in diameter than random trees.
Roost microsites used by northern myotis vary according to sex and reproductive status (Caceres and Pybus 1997). Perry and Thill (2007) found that male northern myotis roosted in smaller-diameter trees than did females. As such, males may have a wider range of usable roost trees available to them than do females (Henderson et al. 2008) and loss of roosting habitat may have a correspondingly larger effect on females than on males. In the eastern US, colonial maternity roosts containing 5 to 88 northern myotis have been reported in cavities in snags or live trees, under bark and in buildings (review in Schmidt 2003; Owen et al. 2002).
Vonhof and Wilkinson (2000) used radiotelemetry to investigate roosting habitat of northern myotis near Fort Nelson, BC. Females roosted colonially, mostly in cracks, in balsam poplar or trembling aspen. Males roosted singly under loose bark. Bats in that study usually switched roosts daily, although they moved an average of only 200 m to a new roost. Male northern myotis in Ontario (Jung et al. 2004) roosted primarily under exfoliating bark of snags, in upland sites away from water bodies, and appeared to select roost snags based on their thermal characteristics. It is thought that female bats in general select warm roosts to speed development of young, but males choose cooler roosts that facilitate the use of torpor as an energy-saving mechanism (Bogan et al. 2003). Jung et al. (2004) suggested that warm roost sites might be preferred by male northern myotis in more northerly portions of their range where average growing season temperatures are lower.
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Northern myotis have been particularly affected by white-nose syndrome in the northeastern portions of their range (Cryan 2009). At this time, white-nose syndrome is not believed to be present in BC. If, when or how white-nose syndrome will affect this species (and other species of hibernating bats) in the Peace River area is not known.
6.4 TECHNICAL AND DATA LIMITATIONS
Investigation of bat habitat use is generally done using either radiotelemetry to relocate individuals or acoustic detection techniques (usually used to indicate ‘activity’ at foraging, commuting or swarming sites). Both of these methods have been used to study bats in the Peace River Corridor (Keystone Wildlife Research Ltd. 2009), but there are constraints involved with each method.
Radio-t elemetry studies of bats in general are prone to the effects of small sample sizes due to the logistical difficulties of work with this species group (Kunz 2003; Miller et al. 2003). The size constraints of bat radio transmitters mean that both signal range and battery life are short, making it impossible to track a single individual through multiple reproductive states (i.e. pregnancy, lactation, post-lactating). The relatively small body size of most northern myotis, in particular, makes them challenging subjects for radiotelemetry. One two-year BC study targeting northern myotis for telemetry did not succeed in the capture of any individuals of sufficient size to carry the transmitters (Haney et al. 2002).
The radiotelemetry program in 2009 was limited by the short times the transmitters remained on the bats. Retention times of glued-on transmitters are highly variable and are affected by a number of factors, including the brand of adhesive used (Albus and Carter 2008; J. O’Keefe pers. comm.). Many previous bat research projects used Skin- Bond brand adhesive, but this is no longer available. Although Torbot is suggested by RIC (1998) as a suitable replacement, the transmitters attached in 2009 using this glue were believed to detach prematurely (<6 days), and at least one was detached the same night it was applied. Others researchers have also reported that Torbot may not be the best choice for long-term transmitter attachment to bats (Albus and Carter 2008).
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6.5 RECOMMENDATIONS FOR FUTURE WORK
Bats are often overlooked during assessments of impacts of development projects, most often due to the lack of existing data on BC bats, uncertainties pertaining to the degree to which bat species are threatened, and the inherent technical difficulties involved with inventory and monitoring for this species group. The following suggestions for additional work are provided in context with the limitations and assumptions discussed in section 6.4 above.
6.5.1 Bat Survey of the Regional Study Area
Sampling within the RSA was an objective of the 2009 work, but the 2009 inventory/telemetry fieldwork only sampled in the vicinity of Fort St. John. Additional sampling within the RSA would provide more data on bat species presence outside the area potentially affected by the Site C dam, which could be used to assess the relative contribution of the Peace River valley to the area’s bat diversity.
• Mist-net surveys would be completed at a variety of habitats outside of the valley, distributed relatively regularly on both sides of the river, with survey sites chosen to maximize coverage of the study area.
• Sampling sites would be selected throughout the area covered by the biophysical mapping, from the AB border to Hudson’s Hope. Radiotelemetry would not form a component of this survey, so survey sites would not be constrained to well- roaded sites. Sampling south of the river, especially, would require the field crew to use ATVs and/or helicopters for access, and to camp at some locations. DNA testing would be used to distinguish between northern and long-eared myotis.
Const ra ints and Limitations
• Mist-net surveys may not detect the presence of high-flying species that are difficult to capture in nets.
• Surveys will only sample habitats in which mist-nets can be used effectively.
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• Sampling will require significant financial resources due to the large size and access constraints of the study area.
6.5.2 Assessment of Bridge Night Roosts – Current Use and Success of Future Mitigation
Bridges are known to be used by a variety of bat species, including northern myotis (Ennis 2006). Bridge night roosts are currently the only public sites within the PRC where relatively large numbers of bats can be captured in a night. The high degree of use of these sites reflects their importance to the local bat population. Some of the existing bridges are located within the potential Site C reservoir area and would be relocated upstream should the project proceed. Provisions for accommodating roosting bats could be incorporated into new bridge designs as part of the project’s mitigation plan, should the project proceed. Success of the bridge mitigation could be assessed by comparing use of the bridges, within and outside of the potential reservoir area, before the project, with use of rebuilt and unaffected bridges after the project was built.
• Mist-net sampling would take place at bridge night roosts (e.g. Farrell Creek, Halfway River, Cache Creek). Additional sampling could be done at bridges between Taylor and AB to provide control sites.
• All healthy adult captures would be marked using freeze-marking (Sherwin et al. 2002) and PIT (passive integrated transponder) tags (O’Shea et al. 2003). Freeze-marks result in a permanent spot of white hair where the mark was applied. PIT tags are tiny microchips that are injected under the skin of the bat’s back. The PIT tags provide individual identification for the life of the bat. Both methods require the bat to be recaptured for its tag/mark to be read/documented. Currently, PIT tag readers must be within 50 cm of the tag but this distance limitation may be improved in the future. The freeze-marks provide a means of permanently identifying a bat to which a PIT tag was applied, although distinguishing individuals cannot be done. The rate of recapture of freeze-
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marked individuals without PIT tags can be used to assess the rate of PIT tag loss. Both freeze-marking and PIT tags have been previously used on bats with few or no detrimental effects to the animals.
• Repeated netting of the bridges and scanning all captures for marks will enable assessment of the local population of bats using each bridge.
• Recapture of marked individuals over multiple years of sampling before and after the project will provide data on year-to-year return to bridges (and the surrounding geographical areas) by individuals, and the success of bridge enhancement, and may also provide some data on dispersal of young, timing of migration, and bat longevity.
• Monitoring bridge temperatures with data loggers may be incorporated to investigate the thermal properties of the existing bridges and compare them with the thermal regimes of the replacement bridges.
Constraints and Limitations
• Bat patterns of use at night roost will vary seasonally and with weather conditions. Sampling conditions should be standardized as much as possible with as many bridges as practical netted during the same night.
• Although bridges between Hudson’s Hope and Taylor have been assessed for bat use, it is not known how many bridges east of Taylor may be used as night roost sites.
• Permission to PIT-tag and freeze-mark bats must be obtained from the province’s Animal Care committee.
• Repeated netting at bridges may result in a temporary decline in bat use as a learned response to capture.
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• Results of bridge monitoring programs cannot be extrapolated to the bat populations at the landscape level.
7.0 LITERATURE CITED
Adam, M. D., and J. P. Hayes. 2000. Use of bridges as night roosts by bats in the Oregon Coast Range. Journal of Mammalogy 81(2):402-407.
Agosta, S. 2002. Habitat use, diet and roost selection by the big brown bat (Eptesicus fuscus) in North America: a case for conserving an abundant species. Mammalian Review 32(2): 179–198.
Albus, A. L., and T. C. Carter. 2008. Comparing Adhesive Types for Radiotransmitter Attachment on Eastern Bat Species. Poster presented at The 38th Annual North American Symposium on Bat Research, The University of Scranton and Hilton Hotel. Scranton, Pennsylvania, October 22 to 25, 2008.
Arnold, B. D. 2007. Population structure and sex-biased dispersal in the forest dwelling vespertilionid bat, Myotis septentrionalis. American Midland Naturalist 157:2, 374-384
Baker, M. D., and M. J. Lacki. 2006. Day-roosting habitat of female long-legged myotis in ponderosa pine forests. Journal of Wildlife Management 70:207-215.
Barclay, R. M. 1982. Night roosting behaviour of the little brown bat, Myotis lucifugus. Journal of Mammalogy 63(3): 464-474.
Barclay, R.M., and R.M. Brigham (eds.). 1996. Bats and Forests Symposium. B.C. Minist. For. Res. Program, Working Pap. No. 23. 292 pp.
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Barclay, R. M., and R. M. Brigham. 2001. Year-to-year reuse of tree-roosts by California bats (Myotis californicus) in southern British Columbia. American Midland Naturalist146: 80–85.
Barclay, R. M., and A. Kurta. 2007. Ecology and behaviour of bats roosting in tree cavities and under bark. Ch. 2 in M. J. Lacki, J. P. Hayes and A. Kurta (eds.). Bats in Forests: Conservation and management. Johns Hopkins University Press, Baltimore.
BC Ministry of Environment. 2008. Bat Distribution Mapping Project. Ministry of Environment, Victoria, BC.
BC Ministry of Environment, Lands, and Parks, (BC MELP) and BC Ministry of Forests (BC MoF). 1998. Field Manual for Describing Terrestrial Ecosystems. Land Management Handbook No. 25. http://www.for.gov.bc.ca/ric/Pubs/teEcolo/fmdte/deif.htm
Blehert, D. S., A. C. Hicks, M. Behr, C. U. Meteyer, B. M. Berlowski-Zier, E. L. Buckles et al. 2009. Bat white-nose syndrome: an emerging fungal pathogen? Science 323:227. Retrieved from: http://www.sciencemag.org/cgi/rapidpdf/323/5911/227.pdf?ijkey=cc/tHUAUCyxXc &keytype=ref&siteid=sci
Bogan, M. A., P. M. Cryan, E. W. Valdez, L. E. Ellison and T. J. O’Shea. 2003. Western crevice and cavity-roosting bats. Pp. 69-77 in T.J. O'Shea and M.A. Bogan (eds.). Monitoring Trends in Bat Populations of the United States and Territories: Problems and prospects: U.S. Geological Survey Information and Technology Report 2003-0003. 274 p.
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Brigham, R. M. 2007. Bats in forests: what we know and what we need to learn. Ch. 1 in M. J. Lacki, J. P. Hayes and A. Kurta (eds.). Bats in Forests: Conservation and management. Johns Hopkins University Press, Baltimore.
Broders, H. G., and G. J. Forbes. 2004. Interspecific and intersexual variation in roost- site selection of northern long-eared and little brown bats in the Greater Fundy National Park Ecosystem. Journal of Wildlife Management 68(3): 602-610.
Caceres, C. M., and R. M. Barclay. 2000. Myotis septentrionalis. Mammalian Species 634:1-4.
Caceres, M. C., and M. J. Pybus. 1997. Status of the Northern Long-eared Bat (Myotis septentrionalis) in Alberta. Alberta Environmental Protection, Wildlife Management Division, Wildlife Status Report No. 3, Edmonton, AB.
Campbell, L. A., J. G. Hallett, and M. O’Connell. 1996. Conservation of bats in managed forests: use of roosts by Lasionycteris noctivagans. In J. G. Hallett and M. O’Connell (eds.). Wildlife Use of Managed Forests: A landscape perspective. A Workshop. Vol. 3.
Carroll, S. K, T. C. Carter and G. A. Feldhamer. 2002. Placement of nets for bats: effects on perceived fauna. Southeastern Naturalist 1(2): 193-198.
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Cryan, P. 2009. White-Nose Syndrome Threatens the Survival of Hibernating Bats in North America. USGS Fort Collins Science Centre. Retrieved from: http://www.fort.usgs.gov/WNS/
Delong, C. 1990. A Field Guide for Identification and Interpretation of Ecosystems of the Northeast Portion of the Prince George Forest Region. Land Management Handbook #22. BC Ministry of Forests.
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Garroway, C. J., and H. Broders. 2008. Day roost characteristics of northern long-eared bats (Myotis septentrionalis) in relation to female reproductive status. Ecoscience 15(1): 89-93.
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Haney, A., M. J. Sarell and J. B. Runciman. 2002. Revelstoke Community Forest Corporation TFL 46 Northern Long-eared Bat Inventory. Final Report to Revelstoke Community Forest Corporation, Revelstoke.
Hemmera. 2009. Raptor and Migratory Bird and Bat Monitoring and Follow-Up Report 2008 and Recommendations for 2009. Report to Bear Mountain Wind Limited Partnership.
Hemmera. 2006. Application for an Environmental Assessment Certificate for Bear Mountain Wind Park. Report to Bear Mountain Wind Limited Partnership.
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Henderson, L. E., L. J. Farrow and H. Broders. 2008. Intra-specific effects of forest loss on the distribution of the forest-dependent northern long-eared bat (Myotis septentrionalis). Biological Conservation 141:1819-1828.
Holroyd, S. 2005. Impacts of Hydroelectric Activities on Bats and Their Habitats: Part of the British Columbia and Alberta Bat Conservation Strategy. Rept. to BC Ministry of Water, Land and Air Protection, Victoria, BC.
Humphrey, S. R. 1975. Nursery roosts and community diversity of Nearctic bats. Journal of Mammalogy 56(2): 321-346.
Jung, T. S., I. D. Thompson and R. D. Titman. 2004. Roost site selection by forest- dwelling male Myotis in central Ontario, Canada. Forest Ecology and Management 202:325-335.
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Kalcounis-Ruppell, M. C., J. M. Psyllakis and R. M. Brigham. 2005. Tree roost selection by bats: an empirical synthesis using meta-analysis. Wildlife Society Bulletin 33(3): 1123-1132.
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Kellner, M. and L. Simpson. 2006. Inventory and Habitat Use of Bat Species in the Peace River Corridor - 2005 - 2006. Report to BC Hydro and Power Authority.
Keystone Wildlife Research Ltd. 2009. Peace River Site C Hydro Project: Stage 2 Baseline Vegetation and Wildlife Report. Report to BC Hydro and Power Authority.
Keystone Wildlife Research Ltd. 2008a. Terrestrial Ecosystem Mapping of the Peace River Study Area. Revised. Prepared for BC Hydro and Power Authority, Burnaby, B.C.
Keystone Wildlife Research Ltd. 2008b. Peace River Wildlife Studies: Draft Wildlife Species Accounts. Revised March 2009. Report to BC Hydro and Power Authority.
Kunz, T.H. 1982. Roosting ecology. In: Ecology of Bats (Ed. by T. H. Kunz), pp. 1–55. Plenum Press, New York, NY.
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United States and Territories: Problems and Prospects. U.S. Geological Survey, Biological Sciences Division, Information and Technology Report, Washington, D.C.
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Miller, D. A., E. B. Arnett, and M. J. Lacki 2003. Habitat management for forest-roosting bats of North America: a critical review of habitat studies. Wildlife Society Bulletin 31 (1): 30-44.
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Perry, R. W., and R. E. Thill. 2007. Roost selection by male and female northern long- eared bats in a pine-dominated landscape. Forest Ecology and Management 247:220-226.
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Slough, B.G, and T. S. Jung. 2008. Observations on the natural history of bats in the Yukon. The Northern Review 29: 127–150.
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Swystun, M. B., J. E. Lane and R. M. Brigham. 2007. Cavity roost site availability and habitat use by bats in different aged riparian cottonwood stands. Acta Chiropterologica 9(1): 183-191.
Vonhof, M. J., and R. M. R. Barclay. 1996. Roost site selection and roosting ecology of forest-dwelling bats in southern British Columbia. Canadian Journal of Zoology 74: 1797–1805.
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Vonhof, M. J., and L. Wilkinson. 2000. A summary of roosting requirements of northern long-eared myotis in northeastern British Columbia. Pp. 459-460 in L. M. Darling, (ed.). Proceedings of a Conference on the Biology and Management of Species and Habitats at Risk, Kamloops, B.C., 15 - 19 Feb.,1999. Volume One. B.C. Ministry of Environment, Lands and Parks, Victoria, B.C. and University College of the Cariboo, Kamloops, B.C.
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Forests: Conservation and Management. Johns Hopkins University, Baltimore, MD.
Weller, T., and D. Lee. 2007. Mist-net effort needed to inventory a forest bat species assemblage. Journal of Wildlife Management 71(1): 251-257.
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Willis, C.K.R. and R. M. Brigham. 2005 Physiological and ecological aspects of roost selection by reproductive female hoary bats (Lasiurus cinereus). Journal of Mammalogy 86(1): 85-94
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Willis, C. K., C. M. Voss and R. M. Brigham. 2006. Roost selection by forest-living female big brown bats (Eptesicus fuscus). Journal of Mammalogy 87(2): 345- 350.
Zinck, J., D. A. Duffield and P. C. Ormsbee. 2004. Primers for identification and polymorphism assessment of Vespertilionid bats in the Pacific Northwest. Molecular Ecology Notes 4 (2): 239 – 242.
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8.0 PERSONAL COMMUNICATIONS
D. Nagorsen. Biologist, Mammalia Consulting Ltd., 2008, 2009.
J. O’Keefe. Department of Forestry and Natural Resources, Clemson University, Clemson, SC 29634, USA , 2009.
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Appendix 1. Wildlife Tree Descriptors
Visual appearance codes for wildlife trees.
Crown condition codes Code Description 1 All foliage, twigs, and branches present 2 Some or all foliage lost; possibly some twigs lost; all branches usually present; possible broken top 3 No foliage present; up to 50% of twigs lost; most branches present; possible broken top 4 No foliage or twigs present; up to 50% of branches lost; top usually broken 5 Most branches gone; some sound branch stubs remain; top broken 6 No branches present; some sound and rotting branch stubs, top broken
Bark retention codes Code Description 1 All bark present 2 Bark lost on damaged areas only (< 5% lost) 3 Most bark present; bare patches; some bark may be loose (5-25% lost) 4 Bare sections; firm and loose bark remains (26-50% lost) 5 Most bark gone; firm and loose bark remains (51-75% lost) 6 Trace of bark remains (76-99% lost) 7 No bark (100% lost)
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Wood condition codes Code Description 1 No decay 2 Probable limited internal decay and/or deformities 3 Wood essentially hard; limited decay 4 Wood mostly hard, but decay spreading; soft wood present 5 Balance of hard and soft wood; spongy sections 6 More soft and spongy wood than hard wood 7 No more hard wood; all soft or spongy; powdery sections 8 Hollow shell; outer wood mostly hard or firm
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