RTE WILDLIFE AND COVER-TYPE MAPPING

First-Draft

ROCKY REACH HYDROELECTRIC PROJECT FERC Project No. 2145

November 9, 2000

Prepared by: Duke Engineering & Services Bothell, Washington

Prepared for: Public Utility District No. 1 of Chelan County Wenatchee, Washington

RTE Wildlife & Cover-type Mapping

TABLE OF CONTENTS

SECTION 1: INTRODUCTION ...... 1-1 1.1 Background ...... 1-1 1.2 Study Goals and Objectives...... 1-4

SECTION 2: STUDY AREA...... 2-1

SECTION 3: METHODOLOGY ...... 3-1 3.1 General Study Design...... 3-1 3.2 Cover-Type Mapping ...... 3-1 3.3 Vertebrate Species Surveys ...... 3-2

SECTION 4: RESULTS AND DISCUSSION...... 4-1 4.1 Cover-Type Mapping ...... 4-1 4.2 Vertebrate Species Surveys ...... 4-19

SECTION 5: CONCLUSIONS ...... 5-1 5.1 Wildlife Habitat...... 5-1 5.2 Wildlife Communities...... 5-3

SECTION 6: REFERENCES ...... 6-1

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LIST OF TABLES

Table 4-1: Comparison of Cover-Type Summary Data from Ebasco Environmental (1991) and Rocky Reach RTE Wildlife and Cover-Type Mapping Study (2000)...... 4-57 Table 4-2: Mean values of habitat data collected within cover-types during the Rocky Reach RTE Wildlife Study...... 4-59 Table 4-3: Environmental setting and general conditions at the Seven Intensive Study Sites...... 4-60 Table 4-4: Environmental setting and general conditions at the 11 Roving Study Sites...... 4-61 Table 4-5: Relative abundance1 of bird species documented by point count surveys at the Intensive Study Sites during the Rocky Reach RTE Wildlife Study...... 4-63 Table 4-6: Relative abundance1 of bird species documented by point count surveys at the Roving Study Sites during the Rocky Reach RTE Wildlife Study...... 4-65 Table 4-7: Relative abundance1 of bird species documented by point count surveys within cover-types during the Rocky Reach RTE Wildlife Study...... 4-68 Table 4-8: Habitat descriptions and locations of waterfowl survey points for the Rocky Reach RTE Wildlife Study...... 4-71 Table 4-9: Small mammal capture rates (captures per 100 trap nights) documented during the Rocky Reach RTE Wildlife Study...... 4-73 Table 4-10: Small mammal capture rates (captures per 100 trap nights) by trap type documented during the Rocky Reach RTE Wildlife Study...... 4-74 Table 4-11: Small mammal captures by feeding group documented during the Rocky Reach RTE Wildlife Study...... 4-74 Table 4-12: Mean values of habitat data collected at each small mammal trapping station during the Rocky Reach RTE Wildlife Study...... 4-75 Table 4-13: Bat species captured during the Rocky Reach RTE Wildlife Study...... 4-76 Table 4-14: Possible bat species detected by ultrasonic detection equipment during the Rocky Reach RTE Wildlife Study...... 4-77 Table 4-15: Amphibians and reptiles found by all methods at Intensive Study Sites during the Rocky Reach RTE Wildlife Study...... 4-78 Table 4-16: Results of area-constrained searches for amphibians and reptiles at Intensive Study Sites during the Rocky Reach RTE Wildlife Study...... 4-78 Table 4-17: Pitfall trapping results for amphibians and reptiles at Intensive Study Sites during the Rocky Reach RTE Wildlife Study...... 4-78 Table 4-18: Amphibians and reptiles found by all methods at Roving Study Sites during the Rocky Reach RTE Wildlife Study...... 4-79 Table 4-19: Summary of dedicated amphibian surveys at Amphibian Sites (AS) for the Rocky Reach RTE Wildlife Study...... 4-80 Table 4-20: Results of dedicated amphibian surveys at Amphibian Sites (AS) for the Rocky Reach RTE Wildlife Study...... 4-82 Table 4-21: State and Federally listed and monitored wildlife species known or possible from the vicinity of the Rocky Reach Project...... 4-86

LIST OF FIGURES

Figure 2-1: Rocky Reach Project Boundary and Location Map...... 2-2

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APPENDICES

APPENDIX A: COVER-TYPE MAPS FOR THE ROCKY REACH PROJECT AREA

APPENDIX B: COVER-TYPE MAPS FOR THE SEVEN INTENSIVE STUDY SITES

APPENDIX C: WILDLIFE SPECIES THAT POTENTIALLY OCCUR IN THE ROCKY REACH STUDY AREA AND THOSE DOCUMENTED DURING THE RTE WILDLIFE STUDY

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RTE Wildlife & Cover-type Mapping

SECTION 1: INTRODUCTION

1.1 Background

1.1.1 General Description of the Relicensing Process Public Utility District No. 1 of Chelan County (hereinafter called Chelan PUD) owns and operates the Rocky Reach Hydroelectric Project (FERC No. 2145) located on the Columbia River in Chelan County, Washington, approximately seven miles upstream of the City of Wenatchee. The original license was granted for the Rocky Reach Project on July 11, 1957 by the Federal Power Commission, now the Federal Energy Regulatory Commission (FERC). This license expires on June 30, 2006.

Chelan PUD intends to seek a new federal license to operate the Rocky Reach Project and has begun preparation for the process referred to as “relicensing”. The FERC relicensing process is based on laws and regulations that require years of extensive planning, including environmental studies, agency consultation, and public involvement. Chelan PUD has requested and received approval from FERC to employ an Alternative Relicensing Process for the Rocky Reach Project, as allowed under FERC’s Final Rule issued on October 29, 1997 (Docket No. RM95-16-000; Order No. 596). The Alternative Relicensing Process (ARP) proposed by Chelan PUD is intended to expedite the licensing process by combining the pre-filing consultation and environmental review processes into a single process, and by improving and facilitating communications among the participants in the licensing process.

One of the first steps taken by Chelan PUD in the Rocky Reach Project ARP was to solicit identification of issues from the participating stakeholders regarding aspects of the Project that would need to be addressed during the relicensing process. Issues identified were then grouped by similar topics. From the sub-groups of topics, study plan outlines were developed to address the pertinent issues. Detailed study plans were then developed from these outlines.

The effect of the Rocky Reach Project operation on rare, threatened, and endangered (RTE) wildlife species and their associated habitats is an issue that has been identified in the relicensing process. To assess the Rocky Reach Project’s effects on RTE wildlife and their habitats, an RTE Wildlife Survey and Cover-type Mapping Study was conducted in the Project area during the fall and winter of 1999 and the spring and summer of 2000. This RTE Wildlife Survey Study Report provides the results of that study.

1.1.2 General Description of the Region The Rocky Reach Hydroelectric project is located within the mid-Columbia River reach approximately 215 river miles below the Canadian border and 474 river miles above the mouth of the Columbia River at Astoria, Oregon.

The Columbia River and its tributaries drain an area of 219,000 square miles in seven western states and 39,500 square miles in British Columbia. In the United States, most of the basin is located in Washington, Oregon, Idaho and Montana. The Columbia River originates at Columbia Lake on the west slope of Rocky Mountain Range in British Columbia and flows west and south, eventually

Draft Study Report Rocky Reach Project No. 2145 November 9, 2000 Page 1-1 SS/2493 RTE Wildlife & Cover-type Mapping draining into the Pacific Ocean between Washington and Oregon. Total river length is 1,214 miles (Chelan PUD 1999).

The mid-Columbia River reach forms the boundary between the Entiat Mountains to the west and the Columbia Plateau to the east. The Entiat Mountains consist of gneisses and granodiorites and reach elevations of approximately 7,000 feet above sea level. In the vicinity of the Rocky Reach project, the river flows over mainly Paleozoic metamorphic and intrusive rocks. Further south, toward Rock Island dam, the river passes into the Columbia basalt group (Chelan PUD 1999). In and around Rocky Reach, the Columbia River flows through a gorge interrupted by confluences with several tributary valleys. The Entiat River and a number of intermittent streams with deep "V" shaped valleys flow into the Columbia River from the west (Chelan PUD 1999).

Located in the rain shadow of the Cascade Range, the mid-Columbia region is classified as arid to semi-arid and experiences low precipitation, dry summers with warm to hot temperatures, and relatively cold winters. Some marine influences are still felt, but continental-type climate conditions prevail. Most of the Columbia basin receives less than 20 inches of precipitation annually, with much of this precipitation occurring in winter. Deep snow may accumulate over the mountainous areas, where water is held as natural storage until spring runoff.

Vegetation in the mid-Columbia region consists mainly of shrub-steppe communities dominated by big sagebrush (Artemisia tridentata), bitterbrush (Purshia tridentata), and rabbitbrush (Chrysothamnus spp.), with some areas of ponderosa pine (Pinus ponderosa) and Douglas-fir (Pseudotsuga menziesii) on north-facing slopes with sufficient precipitation (Franklin and Dyrness 1973). Plant species that may be found in riparian areas along streams or rivers include black cottonwood (Populus balsamifera spp. trichocarpa), white alder (Alnus rhombifolia), willows (Salix spp.), red-osier dogwood (Cornus stolonifera), Douglas hawthorn (Crataegus douglasii), and snowberry (Symphoricarpos albus). Other habitats with distinct vegetation communities include those with gravelly or sandy soils, shallow, stony sites; and sand dunes near the Columbia River (Franklin and Dyrness 1973). Much of the area has been cultivated with a variety of crops or is grazed by livestock.

Land use in the mid-Columbia reach varies considerably from north to south. Rangeland predominates around Rufus Woods Lake, impounded by Chief Joseph Dam, while irrigated cropland and orchards predominate the river corridor around the Rocky Reach Project and reservoir. Below Rock Island Dam, land cover is mostly rangeland, with irrigated cropland on the east side of the river. Land throughout the project reach is predominantly in private ownership, although there are a number of public land units. Federal land in the mid-Columbia River includes the Colville Indian Reservation to the north, the Okanogan and Wenatchee National Forests in sections between Wells and Rocky Reach Dams, and scattered tracts of U.S. Bureau of Land Management (BLM) land. There are also 13 state wildlife refuges and seven state parks in the mid-Columbia region (Chelan PUD 1999).

1.1.3 General Description of the Rocky Reach Project The Rocky Reach Project is located at river mile (RM) 473.7. The reservoir formed by Rocky Reach Dam, also known as Lake Entiat, extends upstream 43 miles to Douglas County PUD’s Wells Dam

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(FERC No. 2149). Rocky Reach in one in a series of five hydroelectric projects built by Chelan, Douglas, and Grant County Public Utility Districts (PUD’s) between RM 397.1 and RM 515.1 on the mainstem Columbia River.

The Project consists of a dam, powerhouse, spillway, non-overflow structures, power transmission facilities, a fish passage system, and a visitors' center. The dam is a 130-foot-high concrete gravity dam. The powerhouse is 1,088 feet long, 210 feet wide, and 218 feet high. It contains 11 generating units, with a peak capability of 1,280 megawatts (MW). The hydraulic capacity of the Rocky Reach powerhouse is 217,000 cfs (Chelan PUD 1999). Power from the Project flows to a single distribution point, the Rocky Reach Switchyard, which is located on the east bank, opposite the powerhouse. The spillway includes 12 gates, each 50-feet wide, which regulate the surface elevation of the reservoir. The forebay wall overlooks the visitors’ grounds and ties the powerhouse to the west bank. The center dam connects the spillway and powerhouse. The visitor facilities are located on the west bank and include a historical museum, visitor center, and 30 acres of lawn and landscaped grounds. The Project also includes fish passage facilities, including a fish ladder adjacent to the west bank and a prototype surface collection system near the forebay wall.

Rocky Reach reservoir has a surface area of approximately 9,100 acres, a gross storage capacity of 382,000 acre-feet, a mean depth of 42 feet, and a shoreline length of approximately 93 miles. The Entiat River is the primary tributary flowing into the reservoir.

In accordance with the existing FERC license, the Rocky Reach reservoir (Lake Entiat) is operated with a normal maximum headwater elevation of 707 feet. The minimum headwater level is 703 feet and the maximum headwater level, used for passage of flood flows, is 710 feet. Although Rocky Reach has existing pondage capacity (useable storage of 36,400 acre-feet between headwater 707 feet and 703 feet), actual pondage drawdowns are avoided if possible because they lower operating head and reduce overall efficiency.

Due to the relatively small storage volume available, Rocky Reach is operated as a run-of-river Project. As a result, the water surface elevation is not constant throughout the reservoir, but increases measurably from Rocky Reach Dam to Wells Dam. As an example, with a headwater elevation at Rocky Reach of 707 feet and a flow of 100,000 cfs, the water surface elevation at Wells Dam is approximately four feet higher, or 711 feet.

Chelan PUD operates the Rocky Reach Project to optimize use of the water resources of the Columbia River to produce electric energy while meeting flood control, irrigation, recreation, municipal, environmental, and other needs. Chelan PUD is a signatory to the Mid-Columbia Hourly Coordination Agreement, along with Public Utility District No. 1 of Douglas County (Douglas PUD), Public Utility District No. 2 of Grant County (Grant) and the Bonneville Power Administration (BPA). Under the terms of this agreement, the five non-federal projects on the Columbia River (Priest Rapids, Wanapum, Rock Island, Rocky Reach, and Wells Dams), as well as the Grand Coulee and Chief Joseph federal projects, are operated in a coordinated manner to optimize water use through this stretch of the Columbia River. Chelan PUD proposes to continue its historical operating policy for the Project with any changes that result from consultation with interested parties during the relicensing process.

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1.2 Study Goals and Objectives The goals of the RTE Wildlife Survey are to evaluate the condition, distribution, and structure of the existing plant communities within the Project Study Area and to survey the wildlife species using these habitats including any rare, threatened, or endangered species (RTE). Specific objectives of the study include: 1. Update the cover-type map developed in 1991 (Ebasco Environmental 1991) to show the current distribution, abundance, and interspersion of wildlife habitats the study area. 2. Document wildlife species occurrence and relative abundance in habitats within the study area. 3. Determine species-habitat associations, which may be used to predict potential project effects on wildlife communities. Document important wildlife breeding or other life-requisite habitats. 4. Document species occurrence in habitats that may be susceptible to or negatively influenced by non-project impacts (e.g., human disturbance). 5. Document the occurrence of RTE species within the study area.

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SECTION 2: STUDY AREA

The study area for the RTE Wildlife Survey and Cover-Type Mapping Study consists of lands within the Project boundary and areas likely to be impacted by Project operations. The Project boundary extends from the tailrace of the Rocky Reach Dam (RM 473.5) upstream to the tailrace of the Wells Dam (RM 516.5) (Figure 2-1). The width of the study area varies by location but generally lies between the major roadways on either side of the Columbia River. The study area is the same as was used in the Rocky Reach Pool Raise Study (Ebasco Environmental 1991).

On the east bank the boundary is Route 2 from Rocky Reach Dam to Beebe Bridge (RM 504.1), except for a section (approximately 8 miles long) north of Daroga State Park where the highway diverges more than a half mile from the river; within the latter area the boundary is defined by elevation contours. North of RM 505 there are no roads along the shoreline; as such the boundary is defined by elevation contours.

On the west bank the study area boundary is the Burlington Northern railroad embankment, which is closely adjacent to Alternate Route 97 from Rocky Reach Dam to the point where the highway diverges toward Lake Chelan (at approximately RM 493.2), and adjacent to Route 97 from Beebe Bridge to Wells Dam. On the west bank the study area also extends approximately 1.3 miles up the Entiat River, a perennial tributary of the Columbia. In addition, on both sides of the river, the study area includes sub-impoundments and wetlands on low ground separated from the river by the highways but within the area potentially affected by the Project.

The use of these study boundaries is appropriate for the following reasons.

1. The area corresponds to the study area used for the proposed Rocky Reach pool raise, a study that had acceptance and prior involvement by the two principal agencies that deal with wildlife issues, WDFW and USFWS; the use of the same boundaries allows for direct comparisons of habitat changes since the previous study. 2. This area encompasses all of the riparian habitats and wetlands along the river in the reach and extends into adjacent non-riparian habitats; species moving between these areas are likely to be documented. 3. Any possible effects of the Project on small mammals, bats, birds, reptiles, and amphibians will be overwhelmingly concentrated in, if not restricted to, this area. 4. The adjacent highways likely form a partial barrier to movement for many species, particularly small mammals, reptiles, and amphibians.

Draft Study Report Rocky Reach Project No. 2145 November 9, 2000 Page 2-1 SS/2493 1720000 1740000 1760000 1780000 1800000 1820000 1840000 1860000 1880000 1900000 FIGURE 1-1

PROJECT LOCATION MAP W± ELLS DAM ROCKY REACH HYDROELECTRIC PROJECT A n on to /(97 Ske ny in let Ca e on C PUBLIC UTILITY DISTRICT NO. 1 re 340000 e 340000 k CHELAN COUNTY WENATCHEE, WASHINGTON

FERC PROJECT NO. 2145 JULY 07, 1999

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± PROJECT BOUNDARY STATE OF WASHINGTON 260000 $T Daroga State Park 260000 BUREAU OF LAND MANAGEMENT n o y n a US FOREST SERVICE C e in P ENTIAT CITY / TOWN # Entiat River # $TEntiat Park PARKS / RECREATION SITES T$ WATERVILLE 240000 $TOrondo Park # 240000 /(2

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$T ± Lincoln Rock State Park

ROCKY REACH DAM ± PROJECT BOUNDARY TO WENATCHEE ±

1720000 1740000 1760000 1780000 1800000 1820000 1840000 1860000 1880000 1900000 RTE Wildlife & Cover-type Mapping

SECTION 3: METHODOLOGY

3.1 General Study Design Data collection for the RTE Wildlife Study consisted of two primary tasks: 1) updating the existing cover-type mapping (Ebasco Environmental 1991) and 2) vertebrate species surveys. Cover-type mapping was updated within the entire study area. Vertebrate species surveys were conducted at seven Intensive Study Sites and 11 Roving Study Sites. The location and a general description of these sites are given in Section 4.1.3 (Table 4-1 and Table 4-2). In addition, sub-impoundments and ponds in the study area were the subject of surveys specifically designed to document amphibians. These Amphibian Survey (AS) sites are listed in Section 4.2.4 (Table 4-19). The Intensive Sites were judged to be representative of habitats within the study area and exhibited a range of habitat conditions and levels of past disturbance. At the Intensive Sites breeding bird, small mammal, bat, reptile, amphibian, and habitat surveys were conducted. The Roving Sites tended to be smaller habitat patches and are intended to show the range of conditions within the study area. Roving Sites received less intensive survey efforts. Breeding bird surveys were conducted at all the Roving Sites and limited bat, reptile, and amphibian surveys were conducted at several Roving Sites.

3.2 Cover-Type Mapping The primary goal of the cover-type mapping was to develop a vegetation cover-type map describing the distribution, abundance, and interspersion of vegetation communities and other cover-types within the study area. Specific objectives were to:

1. Update the cover-type map developed in 1991 for the proposed Rocky Reach pool raise; 2. Collect information on the structure and composition of vegetation cover-types to evaluate their suitability for wildlife including RTE species; and 3. Compare current conditions to the conditions documented in 1991 and identify areas affected by changes in land-use.

The cover-type mapping used the existing, digitized cover-type map created as part of a wildlife habitat evaluation for the Rocky Reach Pool Raise Study (Ebasco Environmental 1991). The existing cover-type data was overlain on digital color ortho-photograph data of the study area. Hardcopy maps were then generated to serve as base maps for revising the cover-type delineations.

Revising the existing cover-type mapping consisted of the following tasks:

1. Reviewing recent (October 1998) color aerial stereo photographs and the existing cover-type data overlain on ortho-photographs to make initial cover-type revisions. The same cover-type classification system used by Ebasco Environmental was used in the current study. 2. Surveying the entire shoreline of Lake Entiat by boat, and making revisions to the base cover- type map. A two-stage mapping process combining aerial photographic interpretation with shoreline mapping in the field was consistent with that used in the Ebasco Environmental study. 3. Digitizing the cover-type revisions and incorporate into the existing GIS database. 4. Calculating the revised acreages of the cover-types and comparing them to those documented in 1991 (Ebasco Environmental 1991).

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Structural habitat data were collected in conjunction with the breeding bird surveys. The vegetation at each bird survey sample point (N=86) was characterized using a modification of the Relevé method (Mueller-Dombois and Ellenberg 1974). At each sample point a 25-m radius plot was established. Within each plot the approximate height and depth of the canopy (if present) was estimated and recorded. In addition, the percent of vegetative cover (projected onto the ground) was estimated in four strata:

1. Tree layer (plants taller than 5 m); 2. Tall shrub layer (plants 2 to 5 m tall); 3. Low shrub layer (plants between 50 cm and 2 m); and 4. Herbaceous layer (plants less than 50 cm tall).

Within the tree and shrub layers, percent coverage was also estimated individually for coniferous and hardwood plant groups and for species. The diameter at breast height (DBH) of trees in the plot was measured, as well as the number and DBH of snags. Slope and aspect of the terrain at each point was also recorded.

3.3 Vertebrate Species Surveys The primary goals of the vertebrate species surveys were to characterize the communities of birds, small mammals, reptiles, and amphibians within the study area with an emphasis on areas that are potentially influenced by Project operation. Inclusion of adjacent non-riparian areas is equally important to understanding wildlife distribution because many species are likely to move between the two areas. These surveys supplement existing databases and are linked to cover-type habitat information. Specific objectives for these studies were to:

1. Document species occurrence of RTE species and other vertebrate taxa; 2. Create and maintain a database on the distribution of small mammals, bats, birds, reptiles, and amphibians; Determine species-habitat associations which may be used to predict potential Project influences on vertebrate communities; 3. Document species occurrence in habitats that may be negatively influenced by land-use practices and activities unrelated to the Project; 4. Identify important breeding habitats and document the use of those habitats;

3.3.1 Bird Surveys Bird communities can be greatly influenced by the habitat characteristics of a site (Rice et al. 1984). For example, previous studies have found that habitat variables such as percent vegetative cover (Willson 1974), percent canopy cover (Crawford et al. 1981, Wiens and Rotenberry 1981), tree species diversity (Winternitz 1976), and presence of snags (Verner and Larson 1989) are associated with various bird community measures. Similarly, the bird communities within the Rocky Reach study area may be influenced by land-uses and other factors such as recreation activities, agricultural practices, and water regime. Therefore, avian studies were designed to relate bird community structure to specific habitats and habitat features, as well as adjacent land use patterns.

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Survey Methodologies Point counts (Reynolds et al. 1980, Bibby et al. 1993) were used to survey breeding birds using habitats within the study area. Fifty bird survey points were established in the Intensive Study Sites and 36 points were established in the Roving Study Sites. Sample points were established along transects with a spacing of at least 200 meters between adjacent points.

Each sample point was visited three times between late April and late June 2000. Surveys began at dawn (approximately 0500 hours) to coincide with peak songbird activity (Robbins 1981a), and continued until approximately 1000 hours. The order in which the points were surveyed was changed from survey to survey to reduce temporal bias. Surveys were not conducted during heavy rains or periods of high wind (Robbins 1981b). At each survey station, all birds heard or seen during a 10-minute period were recorded. The approximate location of each bird detected was recorded on a field map along with notes on behavior and activity. This reduced the probability of registering the same individual more than once and was used to estimate the number of birds of each species present at each point (i.e., relative abundance).

Migratory and wintering bird species were also surveyed using point counts. Twenty survey points were established along Lake Entiat at known or expected areas of waterfowl concentrations. These sites were surveyed in fall 1999, winter 2000, and spring 2000. During each survey birds seen or heard were recorded and counted.

In addition to the standardized survey methods described above, a species checklist was maintained during field visits to supplement the information derived from the point count surveys and provide a more complete description of the avian fauna within the study area.

Habitat Assessment The vegetation at each sample point was characterized using a modification of the Relevé method (Mueller-Dombois and Ellenberg 1974). At each sample point a 25-m radius plot was established. Within each plot the approximate height and depth of the canopy (if present) was estimated and recorded. In addition, the percent of vegetative cover (projected onto the ground) was estimated in four strata:

1. Tree layer (plants taller than 5 m); 2. Tall shrub layer (plants 2 to 5 m tall); 3. Low shrub layer (plants between 50 cm and 2 m); and 4. Herbaceous layer (plants less than 50 cm tall).

These strata emphasize vegetative structure and habitat configuration. For example, tree saplings will be included in the shrub layer estimates even though they are not shrubs. Habitat structure is generally considered more important in the distribution and abundance of birds than plant species composition (Ryder 1986), and foliage estimation within height strata are commonly used in breeding bird habitat assessments (Bibby et al. 1993).

Within the tree and shrub layers, percent coverage was also estimated individually for coniferous and hardwood plant groups and for species. The diameter at breast height (DBH) of trees in the plot was

Draft Study Report Rocky Reach Project No. 2145 November 9, 2000 Page 3-3 SS/2493 RTE Wildlife & Cover-type Mapping measured, as well as the number and DBH of snags. In addition, each snag within the plot that was 9 cm DBH or larger was inspected for evidence of woodpecker use and for the presence of potential nest cavities (Mannan et al. 1980). Slope and aspect of the terrain at each point was also recorded. The site characteristics recorded within each sample plot can be used to classify plots by vegetative characteristics if necessary (Eagles 1981).

Data Analysis Bird species richness (total number of species) was determined for each study site by pooling data from the three survey visits. However, because species richness may be related to sampling effort, the mean number of species detected per visit per sample point for each study site was also calculated. The relative abundance (number of individual birds detected per visit per point) of each bird species was calculated for all sample points and then averaged. Only detections within 50 m of the sample point were included to facilitate comparisons between study sites and account for differences in species detectability among habitats (Petit et al. 1995). Although these measures provide an index to bird species abundance, they are not absolute values. For example, the relative abundance of conspicuous species is often overestimated by standard bird survey methods (Bibby et al. 1993). However, the mean bird species richness is often highly correlated with the total density of birds (Blondel et al. 1981).

3.3.2 Small Mammal Surveys Small mammal communities (i.e., small rodents and insectivores) tend to be substantially influenced by small-scale habitat features, such as the presence of certain forage and cover plant species, stem densities, foliage cover and volume, and woody debris characteristics. These taxa occupy relatively small home ranges and have limited mobility compared to other mammalian groups. For these reasons, studies of small mammals may be very informative in evaluating habitat suitability of cover-types or examining the effects of land-use practices, such as hydroelectric projects, grazing, agriculture, and recreation.

Survey Methodologies Most studies of small mammals designed to document presence and relative abundance require the use of traps operated for several days. Cooperrider et al. (1986) suggests 270 trap nights per site (90 traps operated for three consecutive nights) for a study designed to document species occurrence and estimate relative abundance with the most accuracy. However, because “small mammals” encompass a wide variety of taxa of different sizes and life history, no single trapping methodology is equally effective for capturing all species. Thus, the most successful study designs are those based on the combined use of live traps, snap traps, and pitfalls to increase the likelihood of sampling the majority of species within a given area.

Small mammal populations were surveyed by removal trapping. A combination of Museum Special snap traps, Sherman live traps, pitfall traps, and several sizes of Havahart live traps were used in the small mammal surveys. At each of the seven Intensive Study Sites 60-to-80 trapping stations were established. Trapping stations were established either in a grid or along transects, dependent upon the configuration of the habitat being sampled, at approximately 15-meter intervals (Cooperrider et al. 1986). Two traps, a combination of Museum Specials and Sherman live traps, were placed at each station. The exact location of traps at each station was dictated by micro-habitat features to

Rocky Reach Project No. 2145 Draft Study Report SS/2493 Page 3-4 November 9, 2000 RTE Wildlife & Cover-type Mapping maximize opportunities for captures. Snap and live traps were baited with a mixture of peanut butter and rolled oats. Six Havahart live traps (two small, two medium, and two large) were also placed along the trapping transects. These traps were located in areas with habitat features that were likely to attract larger mammal species. Small Havahart traps were baited with peanut butter and rolled oats, while the larger traps were baited with canned meat.

Four pitfall arrays were installed at each study site. Each pitfall arrays consisted of 10 #10 metal cans buried flush with the ground. Pitfalls were connected with drift fences, made of silt fence, in arrays with four arms. Pitfall arrays were installed at each site the week prior to trapping to allow for acclimation of the resident small mammals (Cooperrider et al. 1986). The cans were covered during this acclimation period.

To the extent practical, pitfall arrays were placed in the vicinity of the other traps. However, the practicality of installing these arrays was contingent on site characteristics. For example, rocky or boulder strewn sites made drift fences ineffective or entirely precluded their use. A small amount of water (approximately 5 cm) was placed in each pitfall trap to drown small mammals (American Society of Mammalogists 1987); this procedure is particularly necessary for shrews, which will otherwise eat other captured animals, thus biasing the data collected. Funnels made of flexible plastic were also attached to the top of pitfalls to reduce the potential for escapes.

Trapping was conducted for four consecutive nights. Traps were checked daily (early morning) and re-baited if necessary. The date, location within the trapping array, and trap type were recorded for each small mammal captured. Missing, broken, or otherwise disabled traps were replaced. Snap or live traps that were tripped but did not result in a capture were also recorded. Species captured were identified by pelage, skull, and dental characteristics using standard small mammal keys. Small mammals caught in live traps were released away from the trapping arrays to prevent recapture.

Habitat Assessment The vegetation at each trapping station was characterized using methods adapted from Morrison and Anthony (1989) and McCracken (1990). A 3-m radius circular plot was centered at each trapping station. Within this plot, the percent cover (projected onto the ground) of 11 vegetative and structural variables was visually estimated. Habitat variables assessed at each trapping station are listed below.

1. Percent forb cover. 2. Percent grass cover. 3. Percent conifer shrub cover. 4. Percent deciduous shrub cover. 5. Percent deciduous tree cover (> 2 m in height). 6. Percent conifer tree cover (> 2 m in height). 7. Percent downed woody debris cover. 8. Percent fallen log cover (> 7.5 cm). 9. Percent litter cover. 10. Percent bare ground. 11. Percent boulder/rock cover.

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Data Analysis Species richness was determined for each site, and small mammal relative abundance was expressed as the number of captures per 100 trap nights for all individuals and each species by site. Capture rates for each trap type were calculated for each site. Captures were also summarized by the following feeding groups: omnivores (seeds, fruits, and insects), herbivores (primarily green vegetation), and insectivores (insects). Summary statistics for habitat variables were calculated for each site.

3.3.3 Bat Surveys The goal of the bat study was to compile a species list and document areas of concentrated bat activity in the study area. The distribution and abundance of bats is often directly related to the availability of certain prominent physical features, including both natural and man-made structures (Cooperrider et al. 1986). These physical features, described as ‘unique habitats’ by Maser et al. (1979), typically comprise only a small percentage of the total land base but are often disproportionately important as habitat for roosting and foraging, and as a source of drinking water.

Roosting habitat can often be a limiting factor for bats. Roosts provide shelter from predators and inclement weather, and some provide the appropriate conditions for raising young (Nagorsen and Brigham 1993). In the Pacific Northwest, all bat species are insectivorous and may be grouped into two general types: cavity-roosting colonial species and foliage-roosting solitary species (Thomas and West 1989). Although vespertilionid (plain-nose) bats are best known for their use of caves, they have been found roosting in a wide variety of structures: trees (hollows, under and within bark, and in foliage), rock crevices, animal burrows, storm sewers, abandoned mines, tunnels, buildings, and cave-like cavities in talus slopes (Nagorsen and Brigham 1993).

Certain bat species are known to use different habitat types while foraging. The Yuma myotis (Myotis yumanensis) in British Columbia is very closely associated with water (Nagorsen and Brigham 1993). Myotis species have been found to be 10 to 75 times more active over water than in a forested interior (Thomas and West 1989, Lunde and Harestad 1986). The fringed myotis (M. thysanodes), western small-footed myotis (M. ciliolabrum), hoary bat (Lasiurus cinereus), and Townsend’s big-eared bats (Corynorhinus townsendii) are more often observed foraging over land than water (Christy and West 1993).

Insectivorous bats emit echolocation calls aiding them in navigation, prey location, and prey capture. Ultrasonic detection equipment allows biologists to detect echo-locating bats without interfering with bat activities (Thomas and West 1989). Echo-locating bats emit signals that may be dominated by constant-frequency components or may sweep through a narrow or wide range of frequencies (Simmons et. al. 1979). Because there are species differences in echolocation calls, some species can be identified with ultrasonic detection equipment. Three types of information are thus potentially available using ultrasonic detection equipment: 1) the distribution of echo-locating bats; 2) a species list of bats in an area; and 3) the identification of important habitat areas used by bats for feeding activity, navigation corridors, and roosting access. Ultrasonic bat detectors are increasingly being used in bat research (Lance et. al. 1995).

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Survey Methodologies Bat surveys were conducted on one or two nights at each Intensive Study Site and several Roving Study Sites. Visual surveys and audio surveys using the Anabat II bat detector were conducted by two to three individuals on each survey night. Surveys began prior to dusk and continued until approximately 2300 hours. Surveys were conducted in areas of suitable habitat for bats, and used both point and transect observations. During these surveys, areas of high use or traffic were noted, and echolocation calls were recorded with the Anabat II bat detector.

Bat trapping was conducted at six sites, in part to assist in species identification. Areas of relatively high use were observed at these sites during the visual and audio surveys; thus, trapping was attempted. Nylon mist nets (6 to 18 m long) with 38-mm mesh were used for bat trapping. Bats captured were identified by external morphological characteristics and then released. Anabat recordings were also conducted during the mist-netting period.

Data Analysis Bat captures were expressed as the number of captures per net hour for each site. Anabat recordings were analyzed using Analyze software (Jolly 1998). Recordings were evaluated aurally, and figures depicting bat call duration and frequency were visually inspected to determine whether each call was complete and whether more than one bat was recorded. Incomplete calls or recordings with more than one bat were not included in the analysis. For each bat call recording analyzed, the following attributes were calculated: maximum frequency, average frequency, minimum frequency, end frequency, duration, curvature, start slope, and end slope. For each unknown recording, these attributes were entered into a spreadsheet along with the attributes of known species from the regional bat call libraries. Most species that potentially occur near the study area were included (13 total). The calls of a few species are not available at this time. Cluster analysis was then used to determine which known bat calls most closely resembled the unknown bat calls based on the attributes used in the analysis (Jolly 1998). A joining (tree clustering) classification system was used for this analysis. This analysis combines objects (bat calls) into successively larger clusters based on some measure of similarity or distance (call attributes).

3.3.4 Amphibian and Reptile Surveys Amphibians as a group are well suited for descriptive community studies because suitable micro- habitats are often easily defined and recognizable. Amphibians are also far less mobile than other species groups, which increases the likelihood of detection. Most species can be documented by more than one life stage (adult, larva, or egg). Salamanders and frogs are among the most vulnerable vertebrate taxa to habitat changes and are often used to investigate the effects of land-use practices, particularly those affecting aquatic habitats and wetlands. Reptile community investigations are sometimes problematic because these taxa tend to be more mobile and less strongly associated with a narrow range of micro-habitats than amphibians. Observations of snakes and lizards are often opportunistic in nature, and rarely provide much information on relative abundance.

Survey Methodologies Amphibians were surveyed using the following methods: 1) systematic searches for amphibian larvae at suitable sites using a dip-net and aquatic funnel traps (“minnow traps”); 2) surveys at night to listen for calling frogs and search for frogs by reflected eye-shine; 3) systematic, area-constrained

Draft Study Report Rocky Reach Project No. 2145 November 9, 2000 Page 3-7 SS/2493 RTE Wildlife & Cover-type Mapping search on the surface and under cover objects in suitable habitats within the riparian zones, in around ponds, and in other likely areas; and 4) pitfall trapping conducted for the small mammal surveys.

Surveys for larvae provide a convenient approach to document species that may otherwise escape detection and a basis for comparing populations at different sites. We sampled using a heavy duty, fine mesh, D-shaped dipnet (net dimensions about 31cm x 16.5 cm x 25 cm deep; mesh size about 1 mm2 ). A standard for measuring sampling effort at each site was the total number of net “sweeps” (Kiviat et al. 1994). With the net held at an angle about 30o from vertical, each sweep follows a continuous figure-8 pattern covering a distance of about 1.2 m and is repeated three times in place, a motion designed to create eddies to lift larvae off the substrate. Dense vegetation, shallow water, fine silt, or organic debris sometimes necessitates modifications to net position. Water deeper than about 1.3 m cannot be sampled effectively by dipnet. Sampling is “blind”; that is, sweeps are distributed throughout a site in different depths and microhabitats without deliberately pursuing larvae.

Previous studies suggest that areas as large as 5 ha may be adequately sampled (i.e., accurately portray species composition and relative abundance of each species) with 50 sweeps (Kiviat et al. 1994, Nyman 1999). At some small sites sampling was discontinued after fewer than 50 sweeps as soon as the entire area had been thoroughly searched.

All quantitative sampling was conducted within the period May 16 to June 9, 2000 and was completed during daylight hours. This sampling period is appropriate for larvae of all of the species that potentially occur. In most instances, larvae were identified in the field and released alive. When necessary a small number of larvae were preserved. Reptiles were surveyed using two methods: 1) systematic area-constrained search on the surface and under cover objects (rocks, logs, boards, etc.) and 2) pitfall trapping conducted for the small mammal surveys. Reptiles observed opportunistically were also recorded.

Data Analysis The number of amphibian and reptile observations during the time-constrained surveys was expressed as the number of observations per search-hour to facilitate comparisons among study sites. Pitfall captures were expressed as the number of captures per 100 trap nights. Species lists were developed for each site.

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SECTION 4: RESULTS AND DISCUSSION

4.1 Cover-Type Mapping

4.1.1 General Discussion of Region and Habitats The Columbia River Basin within the study area lies between two significantly different physiographic areas. The Project is located in a valley that is north-south trending, with the North Cascades Mountains to the west and the Columbia Plateau to the east. The rugged peaks in the Cascades average around 5,000 feet and reach elevations of over 10,000 feet. The Columbia River Plateau ranges from 750 feet to 2,500 feet in elevation and was created by repeated, extensive lava flows during the Miocene period resulting in numerous vast layers of basalt covering the existing bedrock of the region.

The Columbia River Basin within the study area is essentially a gorge interrupted by the confluences of a number of tributary valleys. Two major drainages, the Chelan and Entiat Rivers, and a number of intermittent streams with deep "V" shaped valleys flow into the Columbia River from the west. There are no perennial streams entering the Columbia River from the east. One major intermittent drainage, Corbally Canyon, does join the Columbia from the east. Exposed rock of both fluvial and glacial origin is often mixed into the landscape.

The study area is in the big sagebrush/bluebunch wheatgrass (Artemisia tridentata/ Pseudoroegneria [Agropyron] spicata), or “shrub-steppe” ecological zone, which is characteristic of the drier portions of the Columbia basin (Franklin and Dyrness 1973). This ecological zone is also described as the Central Arid Steppe (Cassidy 1997). Small, scattered stands of ponderosa pine and Rocky Mountain juniper (Juniperus scopulorum) can also be found in the study area, particularly at higher elevations. Due primarily to a history of grazing, undisturbed shrub-steppe is uncommon in the study area (Chelan PUD 1999).

Riparian vegetation occurs intermittently along the shoreline of Lake Entiat. While not uncommon in the study area, riparian vegetation is restricted to a narrow band along the shoreline. The development of riparian vegetation in the study area is limited by arid conditions, steep banks that are often stabilized by rip-rap, and residential and agricultural development along the shoreline (Chelan PUD 1999). Conversely, irrigation has promoted the development of woody riparian vegetation adjacent to some orchards and residential developments.

Narrow wetlands are scattered along the shoreline of Lake Entiat and are typically part of larger riparian habitats. There are also wetlands in small depressions that are impounded by the highways that parallel much of Lake Entiat. Although much of the hydrology for these wetlands is from upland runoff that is temporarily impounded by the highway, some of these small wetland areas are supported by water that is directly related to the water surface elevation of Lake Entiat.

Much of the developed upland area adjacent to Lake Entiat supports fruit orchards, which have been critical to the economy of the Wenatchee area since the early 1900’s. Several large fruit packing

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There is considerable human development within the study area. The larger developments include the Project facilities, Orondo, Entiat, Chelan Falls, and the Wells Dam. Entiat, with a 1998 population of 865 people, is the only incorporated town on Lake Entiat. The only other population centers are the unincorporated communities of Orondo and Chelan Falls, with populations of approximately 75 and 100 respectively. There are also more diffuse developments, particularly residential dwellings and orchard facilities, throughout much of the study area. Approximately 100 parcels of land out of the nearly 400 with frontage on the reservoir have residences on them (Chelan PUD 1999).

Development along the shore of Lake Entiat has resulted in a highly fragmented landscape with many small habitat patches. There are relatively few large tracts of native vegetative communities within the study area and many of these have been disturbed by activities such as grazing and fire.

4.1.2 Cover-Type Analysis Ebasco Environmental (1991) produced a cover-type map of the study area to assist in determining the effects of a proposed 3-foot pool raise on wildlife habitats and species. During that study, cover- type boundaries were delineated on maps in June 1990 in the field as viewed from a boat traveling along the entire shoreline of the reservoir, and using existing black-and-white aerial photographs (dated 1980) and color aerial photographs for the Gallagher Flats and Beebe Bridge areas (date not reported). The 1991 cover-type map was used as the base map for the cover-type mapping conducted for this study.

A cover-type summary is presented in Table 4-1, comparing total areas for each cover-type reported in 1991 with current values. Totals for the major categories (i.e., upland cover-types; riparian and wetland cover-types; disturbed, developed, or modified cover-types; and water cover-types) are also compared. A total of 35 different cover-types under current conditions are mapped in Figure A-1 (Appendix A). Many of the mapped cover-types are very minor components of the available habitats in the study area and are of limited value to wildlife. Furthermore, some of the cover-types overlap in functional attributes as wildlife habitat. Therefore, for the purposes of this discussion several of the pool raise study cover-types will be discussed together as functionally similar groups.

Recreational (RE) The Recreational cover-type includes all designated recreational facilities within the study area including campgrounds, picnic areas, boat launches, and day use areas. Not included in this cover- type are informal gathering or camping areas. There are seven recreational facilities within the study area: 1) Rocky Reach Dam Recreation Facility and Visitor center, 2) Lincoln Rock State Park, 3) Orondo Park, 4) Entiat Park, 5) Daroga Park, 6) Beebe Bridge Park, and 7) Chelan Falls Park.

This cover type currently occupies 212.5 acres in the study area, an increase of 59.2 acres since the Ebasco Environmental pool raise study. Most of this change occurred with the development of Beebe Bridge Park, and the expansion of facilities at Chelan Falls Park and Daroga Park.

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Breeding bird and habitat surveys were conducted at Entiat Park, Daroga Park, and Chelan Falls Park during this study. Nine vegetation sampling plots were located in these recreational facilities.

Recreational facilities often have habitat components that are valuable to certain wildlife species groups. For example, parks typically include groves of shade trees; where these trees are large they may provide suitable nesting habitat for tree and cavity nesting birds. Of the cover-types sampled, Recreational had the second highest mean percent canopy closure (48.0 percent) and the highest mean percent conifer tree cover (8.3 percent) (Table 4-2). In terms of tree structure characteristics, recreational facilities were similar to the Riparian Deciduous cover-type. The mean tree DBH in the recreational cover-type was 12.7 inches and the Riparian Deciduous had a mean tree DBH of 13.1 inches. The mean number of snags per plot (0.4 and 0.5, respectively) and the mean DBH of snags (10.8 and 12.2 inches, respectively) were also similar between Recreational and Riparian Deciduous cover-types. Common tree species in recreational facilities include ponderosa pine, Douglas-fir, Lombardy poplar (Populus nigra var. italica), black cottonwood, black locust (Robinia pseudo- acacia), and Siberian elm (Ulmus pumila).

The Recreational cover-type typically did not exhibit well-developed shrub layers or diverse herbaceous vegetation. Percent shrub cover was relatively low for both the high (11.3 percent) and low shrub (8.6 percent) layers at recreational sites (Table 4-2). The most abundant shrubs in this cover-type were seedlings and saplings of the dominant tree species, although willows and other hydrophytic shrubs can be found directly along the shorelines. Recreational sites had the highest mean percent herbaceous ground cover (78.3 percent); however, this consisted almost entirely of maintained lawns which have limited wildlife value.

Residential/Industrial (RI) The Residential/Industrial cover-type includes all human developments within the study area. Areas of concentrated developments include the Project facilities, Orondo, Entiat, Sun Cove, Chelan Falls, and the Wells Dam. There are also more diffuse developments, particularly residential dwellings and orchard facilities, throughout much of the study area. The area upstream of Beebe Bridge, particularly on the east side of Lake Entiat is the least developed part of the study area. No vegetation sampling plots were established in the Residential/Industrial cover-type.

Residential/Industrial has increased in total area by 230.8 acres, more than any other cover type in the study area, and by a greater percentage than any other major cover-type (65.9 percent). As before, this cover-type occupies the third largest area of any cover-type, exceeded only by Shrub- steppe and Orchard. The increase in developed areas is largely reflected in a decrease in Shrub- steppe, although there has also been conversion from Orchard and Conifer Shrub.

Concentrated human developments generally have very limited wildlife habitat value; however, more diffuse developments can provide some wildlife habitat. For example, widely scattered residential dwellings with landscaped yards often have similar vegetative structural characteristics to recreational facilities. Tree species composition is also similar to recreational facilities in the study area. As with recreational facilities, however, residential areas tend to have poorly developed shrub layers and ground cover that consists primarily of maintained lawns. Some residential developments include remnants of Riparian Shrub or Riparian Deciduous habitats, but most do not.

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Orchard (OR) Orchards occupy the largest portion of the human-modified terrestrial cover-types, and currently a larger proportion of the study area than any other single terrestrial cover-type (25.2 percent of total area). The habitat value of this cover-type to wildlife is relatively limited, although some passerine songbirds may nest in fruit trees, and forage in orchards for insects and fruit. Windbreaks comprised of Lombardy poplars are often associated with orchards in the study area and provide nesting and roosting habitat. Perhaps more importantly, in some areas riparian vegetation has clearly benefited from indirect irrigation (i.e., from run-off and percolation of irrigation water into riparian areas). No vegetation sampling points were established within the Orchard cover-type. Orchards were also not directly sampled for vertebrate species. However, some study sites (e.g., Sun Cove Riparian) were immediately adjacent to orchards.

Although some existing orchards have expanded in area, this cover type has decreased by 14.6 acres (1.5 percent). More than half of this change is associated with new residential development. The rest of the change is reflected in areas now mapped as Grassland/Forbland or Disturbed; the latter are areas with either temporary removal of fruit trees or impending conversion to Residential/Industrial.

Other Human Disturbed or Modified Cover-Types Human disturbed or modified cover-types also include the following: Disturbed (D), Pasture (P), Road, Railroad (RR), Rip-Rap (RP), and Grassland/Forbland (G/F). Grassland/Forbland, not used in the 1991 report, was an appropriate classification for weedy, grassy fields where fruit trees had been removed. None of these cover-types represent important habitats for wildlife. Some areas classified as Rip-Rap are similar to rock talus and may afford suitable hiding areas for lizards, snakes, and small mammals, such as bushy-tailed woodrat (Neotoma cinerea) and yellow-bellied marmot (Marmota flaviventris). No vegetation sampling plots were established in any of these cover-types.

Shrub-steppe (SS) The Shrub-steppe cover-type includes all upland habitats with microphyllous shrub and tree cover greater than 10 percent, but with tree cover alone less than 10 percent (Ebasco Environmental 1991). This cover-type encompasses a wide range of shrub densities, varied plant species composition (sometimes including macrophyllous shrubs), different dominant substrates, and diverse topographic features.

Shrub-steppe is by far the predominant upland native habitat, currently 828.7 acres, or 66.9 percent of all upland native cover-types. Nonetheless, much of the area is fragmented by orchards, residential developments, recreational parks, and roads. Only north of Beebe Bridge is there a large unbroken expanse of Shrub-steppe.

The total area of Shrub-steppe has decreased by 204.3 acres since the Ebasco Environmental pool raise study (a decrease of 19.8 percent). Most of the change is associated with new residential developments and the expansion of existing orchards. The loss of Shrub-steppe occurred almost entirely south of Beebe Bridge in landscapes already fragmented by orchards and residential developments.

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Twenty-five vegetation sampling plots were located in Shrub-steppe sites. Big sagebrush, bitterbrush, and rabbitbrush were the dominant shrub species in the Shrub-steppe cover-type. Western serviceberry (Amelanchier alnifolia), squaw currant (Ribes cereum) (both macrophyllous species), and northern buckwheat (Eriogonum compositum) were of secondary importance. Cover in the high shrub layer (2.0-5.0 m) ranged from 0 to 22 percent with a mean of 10.4 percent (Table 4-2). Big sagebrush and bitterbrush were the most abundant species in the high shrub layer. Cover in the low shrub layer (0.5-2.0 m) was more variable, ranging from 22 to 65 percent, with a mean of 40.3 percent. There were some small, scattered patches of ponderosa pine within shrub-steppe habitats, but otherwise trees were absent.

Ground cover in shrub-steppe habitats ranged from 42 to 90 percent with a mean of 67.3 percent (Table 4-2). Cheatgrass (Bromus tectorum) was the most abundant herbaceous species at 20 of the 25 vegetation sample plots in Shrub-steppe sites. Bunchgrasses (not classified to species) were most abundant in the herb layer within the other five sampling plots and four of these were located at the Uplake Shrub-steppe site. This was the largest and most remote shrub-steppe habitat sampled. Shrub-steppe sites had minimal downed woody debris cover (mean of 6.4 percent), consisting of shrub limbs only. Although there was minimal downed woody debris cover, many of the big sagebrush and bitterbrush plants had dense, low branches that may serve as cover for small vertebrates. Rock/boulder cover ranged from 0 to 35 percent with a mean of 13.5 percent. In some areas exposed rocks and boulders were a significant cover feature.

Shrub-steppe habitats are considered Priority Habitats by WDFW (WDFW 2000a), either as 1) large tracts (greater than 640 acres) of relatively intact and largely undisturbed shrub-steppe habitats with a variety of habitat features (e.g., variety of topography, riparian areas, canyons, habitat edges, and plant communities) or 2) small tracts (less than 640 acres) of relatively undisturbed shrub-steppe habitats, as indicated by the dominance of native plant species. The criteria for listing shrub-steppe habitats as Priority Habitats are the comparatively high wildlife density, high wildlife diversity, importance as wildlife breeding habitat, importance as wildlife seasonal range, limited availability, high vulnerability to habitat alteration, and presence of unique and dependent species (WDFW 2000a).

Exposed Rock (ER) and Exoposed Rock/Shrub-steppe (ERSS) The Exposed Rock cover-type is defined as nonvegetated lands (less than 10 percent vegetation cover) consisting of bedrock (Ebasco Environmental 1991). In practice, it includes some of the small islands of Lake Entiat that may be comprised of large boulders. Exposed Rock/Shrub-steppe consists of vegetated areas with very low-density shrub-steppe on bedrock, boulders, or cliffs. The current distribution and total area of these cover types (136.8 acres) has remained essentially unchanged since the Ebasco Environmental pool raise study (138.4 acres). The largest portion of the two cover-types is on Turtle Rock.

Eleven vegetation sampling plots were located in Exposed Rock/Shrub-steppe, which included portions of Turtle Rock and the Chelan Butte Wildlife Management Area. Vegetation was relatively sparse at these sites, and Rock/boulder cover was the most significant cover feature in this cover- type. Cover in the high shrub layer (2.0-5.0 m) ranged from 0 to 17 percent with a mean of 9.2

Draft Study Report Rocky Reach Project No. 2145 November 9, 2000 Page 4-5 SS/2493 RTE Wildlife & Cover-type Mapping percent (Table 4-2). Western serviceberry and bitterbrush were the most abundant species in the high shrub layer. Cover in the low shrub layer (0.5-2.0 m) was more variable ranging from 0 to 55 percent with a mean of 26.2 percent. Big sagebrush, bitterbrush and western serviceberry were the most abundant species in the low shrub layer.

Ground cover in Exposed Rock/Shrub-steppe habitats ranged from 25 to 85 percent with a mean of 51.0 percent (Table 4-2). Cheatgrass was the most abundant herbaceous species in this cover-type. Rock/boulder cover consisted of exposed bedrock, boulders, and cliffs and ranged from 35 to 75 percent with a mean of 59.2 percent.

Both cliff and talus habitats are considered Priority Habitats by WDFW (WDFW 2000a). To be considered as Priority Habitats, cliffs must be greater than 25 feet high and occur below elevations of 5,000 feet. The criteria for listing cliff habitats are their significance as wildlife breeding habitat, limited availability, and presence of dependent species (WDFW 2000a). To be considered as Priority Habitats, talus habitats must be homogenous areas of rock rubble ranging in average size from 0.5 to 6.5 feet, composed of basalt, andesite, and/or sedimentary rock, including rip-rap slides and mine tailings. These habitats may be associated with cliffs. The criteria for listing talus habitats are their limited availability, presence of unique and dependent species, and high vulnerability to habitat alteration (WDFW 2000a).

Upland Conifer/Shrub (CS) This cover-type includes upland habitats with tree cover greater than 10 percent, dominated by conifers, and not located in a riparian area (Ebasco Environmental 1991). Because these conifer patches are usually diffuse and tend to contain relatively few trees, they are not comparable to forest areas.

Conifer/Shrub occupied 49.4 acres in 1991, mostly concentrated in a few areas already fragmented by residential developments. In the interim period a large percentage (54.3 percent) of this cover- type has been converted to Residential/Industrial, and some to Orchard.

No vegetation sampling plots were established in this cover-type. A description of this cover-type was provided by Ebasco Environmental (1991) and is summarized below.

Ebasco Environmental (1991) found that tree cover in this cover-type ranged from 0 to 88 percent with a mean of 39.6 percent. Ponderosa pine was the dominant tree species with Rocky Mountain juniper, and Douglas-fir of secondary importance. Shrub cover was variable, ranging from 5 to 76 percent. Shrub species included small ponderosa pine, Rocky Mountain juniper, snowberry, western serviceberry, Himalayan blackberry (Rubus discolor), bitterbrush, and rabbitbrush. Herbaceous ground cover was generally sparse and consisted of grasses such as cheatgrass and bluebunch wheatgrass. This cover-type occurs primarily on dry sites in draws or at the base of slopes and often includes many large boulders and rocks.

Riparian Deciduous (RD) This cover-type includes vegetated habitats with tree cover greater than 10 percent, dominated by deciduous species, and in a riparian area (Ebasco Environmental 1991). Ebasco Environmental also

Rocky Reach Project No. 2145 Draft Study Report SS/2493 Page 4-6 November 9, 2000 RTE Wildlife & Cover-type Mapping mapped a related cover-type, Palustrine Forested (PF), based on the same criteria, as well as prior designation as wetlands on National Wetlands Inventory maps (NWI) of the area. Wetland criteria (hydrophytic vegetation, wetland hydrology, and hydric soils) were not verified in the field in 1990 or in the current study. Because both PF and RD habitats within the study area are limited to riparian areas and are similar in vegetation structure and composition (Ebasco Environmental 1991), these two cover-types were grouped for vegetation sampling and analysis by Ebasco Environmental and in the current study.

Riparian Deciduous currently occupies 113.4 acres in the study area; Palustrine Forested Wetland occupies just 2.0 acres. The total area of the two combined cover-types has decreased by 25.0 acres (17.8 percent) since the Ebasco Environmental pool raise study. It is unclear whether this reflects changes in vegetation or merely differences in the interpretation of field features. Possibly some areas previously classified as Riparian Deciduous were assigned to Riparian Shrub in the current study. It may be notable that the combined area of Riparian Deciduous and Riparian Shrub has remained almost unchanged.

Nineteen sample points were located in this cover-type. Riparian Deciduous occupies only a small portion of the study area (3.3 percent of terrestrial cover-types), but may contribute disproportionately to biodiversity of the region. Riparian habitats are considered Priority Habitats by WDFW (WDFW 2000a). Riparian habitat encompasses the area beginning at the ordinary high water mark and extends to that portion of the terrestrial landscape that is influenced by, or that directly influences, the aquatic ecosystem. Riparian habitat includes the entire extent of the floodplain and riparian areas of wetlands that are directly connected to stream courses. The criteria for listing riparian and wetland habitats as Priority Habitats are comparatively high wildlife and fish density, high wildlife and fish diversity, importance as wildlife and fish breeding habitat, importance as wildlife and fish seasonal range, limited availability, high vulnerability to habitat alteration, and presence of unique and dependent species (WDFW 2000a).

Riparian Deciduous habitats within the study area have very diverse vegetative structural characteristics and plant species compositions. This variability is due to many factors, including the topographical setting of each habitat, the level of historic and current disturbance, the presence of adjacent human developments, and the presence of invasive plant species. This discussion will only address general characteristics of the Riparian Deciduous cover-type. The unique vegetative structure and composition of riparian areas at each of the Intensive Study sites are discussed in Section 4.1.3.

Riparian Deciduous sites had the most tree cover of the habitats sampled. Canopy closure ranged from 45 to 87 percent with a mean of 66.4 percent (Table 4-2), compared to a range of 15 to 100 percent and a mean of 68 percent reported by Ebasco Environmental (1991). Dominant tree species varied by site, but black cottonwood was typically the most abundant species. Siberian elm, Lombardy poplar, black locust, weeping willow (Salix babylonica), water birch (Betula occidentalis), white alder, and Russian olive (Eleagnus angustifolia) were also locally abundant. This cover-type had the highest mean tree DBH (13.1 inches) and snag DBH (13.8 inches), as well as the highest mean number of snags per sample plot (0.5), although snags in general were not abundant in the study area.

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In addition to the high percent canopy cover, Riparian Deciduous sites exhibited well-developed shrub layers. Cover in the high shrub layer (2.0-5.0 m) was variable, ranging from 0 to 55 percent, with a mean of 18.7 percent (Table 4-2). Cover in the low shrub layer (0.5-2.0 m) was even more variable, ranging from 0 to 75 percent, with a mean of 21.9 percent. Species composition was variable, but white alder, willows, red-osier dogwood, Himalayan blackberry, and saplings of the dominant tree species were abundant.

Ground cover in Riparian Deciduous habitats was variable, ranging from 5 to 90 percent, with a mean of 47.9 percent (Table 4-2). Species composition was variable, but reed canarygrass (Phalaris arundinacea), horsetail (Equisetum spp.), and western poison ivy (Toxicodendron rydbergii [= Rhus radicans]) were generally abundant. Other herbaceous species include goldenrod (Solidago canadensis), mullein (Verbascum thapsus), cattail (Typha latifolia), knapweed (Centaurea spp.), and sedges (Carex spp.). The extent and the species composition of the herbaceous layer at a particular site was largely dependent upon the level of past or current disturbance and the presence of invasive species. For example, some sites had areas of fill that covered the native vegetation and allowed invasive species to colonize. Riparian Deciduous habitats had a moderate amount of downed woody debris (mean of 14.7 percent cover), which consisted of both small limbs and downed trees. In undisturbed Riparian Deciduous the combination of herbaceous ground cover and moderate amounts of downed woody debris provide suitable cover and foraging habitat for small mammal species.

Riparian Shrub (RS) The Riparian Shrub cover-type includes all habitats with macrophyllous shrub and tree cover greater than 10 percent, but with tree cover less than 10 percent (Ebasco Environmental 1991). By this definition, Riparian Shrub was not strictly limited to riparian settings; relatively mesic sites near irrigated land and disturbed sites with weedy macrophyllous shrubs are also classified as Riparian Shrub. Ebasco Environmental also mapped a related cover-type, Palustrine Scrub-shrub Wetland (PS), on the basis of prior designation on National Wetlands Inventory maps (NWI). Wetland criteria (hydrophytic vegetation, wetland hydrology, and hydric soils) were not field verified. Because the two cover-types overlap completely in distribution and are similar in vegetative structure and composition (Ebasco Environmental 1991) they were grouped for vegetation sampling and analysis in both studies. Riparian habitats may be considered Priority Habitats by WDFW (2000a) as discussed for the Riparian Deciduous cover-type.

Riparian Shrub currently occupies 134.4 acres in the study area, compared to 13.2 acres of Palustrine Shrub Wetland. The combined Riparian Shrub/Palustrine Shrub cover-types have increased in area by 31.4 acres (27.0 percent) since the Ebasco Environmental pool raise study. The increase largely represents incremental changes (i.e., enlargement of existing habitat areas); in addition, some areas previously classified as Riparian Deciduous were assigned to RS in this study.

Fourteen sample points were located in this cover-type. Riparian Shrub sites generally exhibited a sparse tree canopy (mean of 17.8 percent). Black cottonwood and Siberian elm were the tree species most often associated with Riparian Shrub. Because Riparian Deciduous and Riparian Shrub habitats were often contiguous, the species composition of these cover-types are very similar.

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Riparian Shrub sites within the study area have well-developed shrub layers and had the highest percent cover in the high shrub layer (2.0-5.0 m) and the second highest percent cover in the low shrub layer (2.0-5.0 m) of the habitats sampled. Cover in the high shrub layer (2.0-5.0 m) was variable, ranging from 12 to 75 percent, with a mean of 45.8 percent (Table 4-2). Cover in the low shrub layer (0.5-2.0 m) was also variable (10 to 67 percent), with a mean of 32.9 percent. Species composition was variable, but white alder, willows, red-osier dogwood, Himalayan blackberry, and saplings of the dominant tree species were abundant.

Ground cover in Riparian Shrub was variable (17 to 95 percent), with a mean of 57.4 percent (Table 4-2). Species composition was variable, but reed canarygrass, horsetail, and western poison ivy were generally abundant. Other herbaceous species include goldenrod, mullein, cattail, knapweed, and sedges. The extent and the species composition of the herbaceous layer at a particular site was largely dependent upon the level of past or current disturbance and the presence of invasive species. For example, some sites had areas of dense Himalayan blackberry which reduced or completely eliminated herbaceous vegetation. Riparian shrub habitats had a relatively small amount of downed woody debris (mean of 9.2 percent cover), which consisted mainly of small limbs.

Riparian Grassland Riparian Grassland is defined by Ebasco Environmental (1991) as a riparian area dominated by grasses (less than 10 percent woody vegetation cover). This cover-type occurs primarily as a narrow band along the shore, but was sometimes mapped by Ebasco Environmental upslope of Riparian Shrub or Riparian Deciduous. Apparent inconsistencies in prior application of this cover-type were noted, with the inclusion of areas on high banks or otherwise remote from the shoreline, including lawns of lake frontage residential developments, and the grassy edges of orchards. The latter are clearly areas affected by human activity and so should have been classified as Riparian Grassland.

The total area of Riparian Grassland has decreased by 32.8 acres (36.1 percent) since the Ebasco Environmental pool raise study. This is largely attributable to the reclassification of lawn areas as Residential/Industrial and non-riparian areas to other cover-types. No vegetation plots were established within this cover-type. Observation of areas previously mapped as Riparian Grassland areas suggest that a variety of forbs may occur in this cover-type, including western goldenrod, yellow flag (Iris pseudacorus), water horehound (Lycopus sp.), curly dock (Rumex crispus), spike- rush (Eleocharis sp.), Columbia coreopsis (Coreopsis atkinsoniana), western mountain aster (Aster occidentalis), and nodding beggar’s-tick (Bidens cernua). The wildlife habitat values of Riparian Grassland areas are limited.

Palustrine Emergent Wetland (PE, PEC, and PEB The Palustrine Emergent Wetland (PE) cover-type was defined by Ebasco Environmental (1991) on the basis of three criteria: 1) prior designation as a wetland by the National Wetland Inventory; 2) vegetation cover of at least 30 percent; and 3) vegetation consisting of herbaceous emergent species. In practice, it is likely that any observed patch of obligate hydrophytic emergents would have been mapped as this cover-type in the pool raise study. Palustrine Emergent is further classified where possible by the dominant emergent species, with stands of cattail designated as PEC, and stands of soft bulrush (Schoenoplectus [Scirpus] validus) designated PEB. Most examples of this cover-type

Draft Study Report Rocky Reach Project No. 2145 November 9, 2000 Page 4-9 SS/2493 RTE Wildlife & Cover-type Mapping are dominated by a single species, usually cattail, bulrush, or reed canarygrass, or occasionally two species (e.g., cattail and soft bulrush).

This cover type has increased in total area from 13.3 acres to 18.3 (38.1 percent increase). Nearly all of the emergent wetlands mapped in 1991 are extant and some have increased in size. The patches of this cover-type are, with few exceptions, small. Palustrine Emergent typically occurs in a narrow band scattered along the shore of Lake Entiat in shallow water, including protected, shallow bays and inlets; the largest shoreline Palustrine Emergent wetland is at Daroga State Park. In addition, this cover-type is a characteristic feature of sub-impoundments, ponds, and wetlands in the study area; all but three of these contained at least some areas of Palustrine Emergent. The largest single example (4.5 acres) of this kind of Palustrine Emergent wetland is at the Azwell Riparian Site.

Five habitat sample points were established within Palustrine Emergent habitats. By definition, this cover type does not contain trees or shrubs; however, shrub cover occurs sometimes at the margins from adjacent cover-types. Shrub species recorded at the margins of Palustrine Emergent habitat sample points included white alder, willows (including coyote willow (Salix exigua)), and Himalayan blackberry.

Ground cover in Palustrine Emergent habitats was high and ranged from 75 to 100 percent with a mean of 86.6 percent (Table 4-2). Species composition was variable, but reed canarygrass, cattail, softstem bulrush (Scirpus validus), and horsetail were common. Other herbaceous species include yellow flag, small-flowered bulrush (Scirpus microcarpus), common reed (Phragmites australis [P. communis]), common rush (Juncus effusus), spike-rush, smartweed (Polygonum spp.), nodding beggar’s-tick, and sedges.

Palustrine Aquatic Bed (PAB) This cover-type was defined by Ebasco Environmental (1991) on the basis of three criteria: 1) prior designation as a wetland by the National Wetland Inventory; 2) vegetation cover of at least 30 percent; and 3) vegetation consisting of macrophytic algae, mosses, or submerged, floating-leaved, or floating vascular plants. The occurrence of aquatic beds within Lake Entiat are discussed by Ebasco Environmental, and total areas are presented for this cover-type on the basis of other existing data (Keesee 1989); however, Palustrine Aquatic Bed was not mapped within Lake Entiat by Ebasco Environmental (1991) or in the current study (not within the scope of work). Areas of this cover- type in both studies are mapped only within sub-impoundments and ponds. Palustrine Aquatic Bed currently occupies approximately 2.1 acres within the latter areas, compared to 2.0 acres mapped by Ebasco Environmental. No habitat sample points were established within this cover-type. Amphibian surveys were conducted in sites mapped as Palustrine Aquatic Bed. These areas consisted of dense stands of Eurasia milfoil (Myriophyllum spicatum), pondweed (Potamogeton spp.), and other submerged aquatic vascular plants, along with duckweed (Lemna sp.) and algae at some sites.

Open Water Cover-Types (LOW, ROW and POW) Over water cover-types consist of Lacustrine Open Water (Lake Entiat, sub-impoundments, and some of the ponds), Palustrine Open Water (some of the ponds), and Riverine Open Water (Entiat River above the standard pool elevation of Lake Entiat). Lacustrine Open Water occupies by far the

Rocky Reach Project No. 2145 Draft Study Report SS/2493 Page 4-10 November 9, 2000 RTE Wildlife & Cover-type Mapping largest portion of the study area. The lacustrine and riverine habitats were not within the scope of the current study, except within sub-impoundments and ponds as possible habitat for terrestrial or amphibious vertebrates.

Description of Habitats within the Intensive Study Sites The location and general characteristics of each of the seven Intensive Study Sites are given in Table 4-3 and cover-type maps of the sites are in Appendix B.

Turtle Rock Turtle Rock is the largest island in Lake Entiat and lies approximately 1-mile upstream of the Rocky Reach Dam (RM 474.8 to 476.0). Turtle Rock is approximately 1.1 miles long and 0.4 miles wide at the widest point. Prior to construction of the Rocky Reach Project, Turtle Rock was connected to the east bank mainland, but is now separated by a 700 to 2100 foot wide channel.

Turtle Rock is comprised of two distinct areas characterized by differences in geology and vegetation. The downstream third of the island is flat to gently rolling, and areas of exposed bedrock and boulders are not extensive. The island is relatively narrow here, terminating in several small rocky islands. The Chelan PUD maintains a boat dock, fish rearing and holding facility, and maintenance buildings and roads in this section. Shrub-steppe is the dominant vegetation cover-type and there are narrow riparian habitats along much of the shoreline. Big sagebrush was the dominant species in both the high shrub (2.0-5.0 m) and low shrub (0.5-2.0 m) layers, with bitterbrush, rabbitbrush, and serviceberry of secondary importance. Percent cover was higher in the low shrub layer (33-37 percent) than the high shrub layer (12-17 percent). Ground cover was moderate (45-60 percent), with cheatgrass the dominant species. Riparian habitats in this section were generally narrow with the exception of an area of Riparian Shrubland and Palustrine Emergent Wetland associated with a cove on the south shore near the upstream end of this section. Russian olive was the dominant shrub in this area and formed nearly complete canopies in some instances. Cattail was the dominant species in the emergent wetland, with yellow-flag and reed canarygrass also abundant.

The upstream section of Turtle Rock consists mostly of steep slopes with abundant boulders, exposed bedrock, and cliffs. There is also a relatively flat open area between this section and the first. Much of this section of Turtle Rock was burned by an accidental fire in 1999. Due to the fire and the rocky substrates, this section of Turtle Rock has very sparse shrub-steppe vegetation. Percent cover was low in both the low shrub layer (5-15 percent) and the high shrub layer (0-17 percent). Big sagebrush and serviceberry were the most abundant shrub species. Ground cover was moderate (45-55 percent), with cheatgrass the dominant species. Exposed rock, boulders, and cliffs are the dominant cover feature in this section. Several species of birds that nest in exposed rock and cliff habitats were observed during the study, including cliff swallow (Hirundo pyrrhonota), rock wren (Salpinctes obsoletus), and canyon wren (Catherpes mexicanus).

Because Turtle Rock is an island with no public boat docks, there is relatively limited human disturbance. The Chelan PUD fish holding facility and maintenance buildings are visited regularly by Chelan PUD staff, but their activities are largely restricted to these facilities. The fire that occurred in 1999 burned a large portion of the island, but revegetation had already begun in 2000.

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The cliffs on Turtle Rock would probably be considered Priority Habitats as defined by WDFW (1996).

Entiat River The Entiat River is the major tributary entering Lake Entiat and is located on the west bank at RM 483.7. The Entiat River watershed consists of portions of the Entiat and Chelan Mountains to the west of the Project. In most of the watershed the river has a high gradient and lies in a relatively narrow, V-shaped valley. Near the confluence with Lake Entiat, the drainage widens somewhat forming the Entiat River Valley. The mouth of the river is bordered by the Swakane Wildlife Area to the south, and Entiat River Road and associated residential dwellings to the north. The adjacent Swakane Wildlife Area consists of very steep slopes with shrub-steppe vegetation, exposed rock and cliffs, and some ponderosa pine. The river gradient is lower in this reach, and, as a result, there are several islands and backwater areas near the confluence.

Riparian Deciduous and Riparian Shrub habitats comprise much of the area along the Entiat River, although orchards currently occupy a large part of the valley. These habitats are generally narrow and restricted to near-shore areas. There is a large emergent wetland/scrub-shrub wetland complex in a backwater area near the confluence with Lake Entiat. Smaller areas of emergent wetlands are interspersed with the riparian deciduous and shrub habitats along the shoreline in the upper reach.

Within Riparian Deciduous portions of this site, black cottonwood was the dominant tree species, with white alder and water birch of secondary importance. Canopy cover was moderate to dense (52-83 percent). Snags were not abundant, but nest cavities were observed in dead limbs of large black cottonwood trees. Riparian Deciduous areas also had a well-developed shrub layer, with high shrub cover (2.0-5.0 m) ranging from 27 to 33 percent, and low shrub cover (0.5-2.0 m) ranging from 17 to 25 percent. Common shrub species included white alder, red-osier dogwood, snowberry, willows, and black cottonwood saplings. Ground cover was moderate to dense (37-90 percent), with horsetail, reed canarygrass, and western poison ivy the most abundant herbaceous species. Downed woody debris cover ranged from 12 to 22 percent and consisted of large cottonwood limbs and downed trees.

Within Riparian Shrub areas there was little or no tree cover. These habitats had very dense shrub cover, with high shrub cover (2.0-5.0 m) ranging from 73 to 75 percent and low shrub cover (0.5-2.0 m) ranging from 22 to 37 percent. White alder and willows were the dominant shrub species. Ground cover was limited (25 to 35 percent) due to the dense shrub cover with horsetail, reed canarygrass, and western poison ivy the most abundant herbaceous species. Downed woody debris cover ranged from 12 to 22 percent and consisted of large cottonwood limbs and downed trees.

Palustrine Emergent areas of the Entiat River exhibited no tree cover and only sparse shrub cover (less than 10 percent), limited to white alder and willows along the margins. Ground cover was dense (75-80 percent), with cattail, softstem bulrush, and reed canarygrass the most abundant herbaceous species. Common rush, smartweed, goldenrod, and nodding beggar’s-tick were of secondary importance. There is a well-developed emergent wetland located in the backwater area near the confluence with Lake Entiat. Several species of wildlife associated with marshes were

Rocky Reach Project No. 2145 Draft Study Report SS/2493 Page 4-12 November 9, 2000 RTE Wildlife & Cover-type Mapping observed in this area, including red-winged blackbird (Agelaius phoeniceus), common yellowthroat (Geothlypis trichas), and muskrat (Ondatra zibethicus).

The vegetation within the Entiat River riparian habitats is relatively undisturbed, with a high prevalence of native wetland species and well-developed structural components. There has been some clearing and fill associated with an old roadbed along the north shore of the Entiat River. During the summer of 2000 additional clearing and grading occurred in this area. There are also several established trails that lead to the Entiat River for fishing access. Numerous people were observed walking along the roadbed during this study, but their activities appeared to be limited to the roadbed and existing trails with little effect on riparian vegetation.

Upstream of the field study area, there has been some relatively recent conversion of riparian habitats to orchards. Further narrowing by development could imperil the riparian corridor along the Entiat. The riparian and wetland habitats along the Entiat River would likely be considered Priority Habitats as defined by WDFW (1996).

Sun Cove Riparian The Sun Cove Riparian site is located on the east bank of Lake Entiat at RM 491.6 to 492.1. This site is on private property; orchards lie immediately adjacent upslope. The area occupied by riparian vegetation is approximately 2,400 feet long, varying in width from approximately 40 to 500 feet. The landscape if fairly flat within the riparian zone and the surrounding areas have low to moderate slopes.

Riparian Deciduous habitats dominate the Sun Cove Riparian site, but there are also Riparian Shrub, Palustrine Emergent wetland, and a small area of Shrub-Steppe habitat. There is one permanent and one temporary pool located in the upstream, widest portion of this site. Western toads (Bufo boreas) were documented breeding in the permanent pool and a painted turtle (Chrysemys picta) was also observed in this pool.

Within the Riparian Deciduous portions of the Sun Cove Riparian site black cottonwood was the dominant tree species, with white alder and weeping willow of secondary importance. Canopy cover was moderate to dense in the riparian woodlands (55-75 percent). Snags were not abundant, but nest cavities were observed in dead limbs of large black cottonwood trees. Riparian Deciduous areas also had a well-developed shrub layer with high shrub cover (2.0-5.0 m) ranging from 12 to 55 percent and low shrub cover (0.5-2.0 m) ranging from 7 to 22 percent. Common shrub species included white alder, willows, red-osier dogwood, and black cottonwood saplings. Ground cover was variable, ranging from 17 to 77 percent, with reed canarygrass, horsetail, and cattail the most abundant herbaceous species. Downed woody debris cover ranged from 12 to 25 percent and consisted of small and large cottonwood limbs and downed trees.

Within the Riparian Shrub portions of the Sun Cove Riparian site there was little or no tree cover. These habitats had very dense shrub cover with high shrub cover (2.0-5.0 m), ranging from 60 to 75 percent, and low shrub cover (0.5-2.0 m) ranging from 20 to 37 percent. Coyote willow, white alder and red-osier dogwood were the dominant shrub species. Ground cover was moderate (45 to 65

Draft Study Report Rocky Reach Project No. 2145 November 9, 2000 Page 4-13 SS/2493 RTE Wildlife & Cover-type Mapping percent), with reed canarygrass and horsetail the most abundant herbaceous species. Downed woody debris cover was minimal and consisted of small limbs.

Emergent wetlands were found in two areas within the Sun Cove Riparian site. One emergent wetland was associated with the permanent and temporary pools located in the upstream, widest portion of the site. These wetlands were dominated by cattail, with small areas of softstem bulrush, and reed canarygrass. A population of a rare plant species, giant helleborine (Epipactis gigantea), was documented in the seasonally wet area. Several pairs of red-winged blackbirds were observed nesting in this wetland. The second emergent wetland complex was located along the shoreline in the downstream, narrow portion of the site. These wetlands were dominated by softstem bulrush with lesser amounts of cattail and reed canarygrass. Great blue herons (Ardea herodias) and mallards (Anas platyrhynchos) were observed frequently in these wetlands.

The vegetation within the Sun Cove Riparian site is relatively undisturbed, with a high prevalence of native wetland species and well-developed structural components. This is probably due to the private ownership, which limits public access. There are several trails and a small dock within this site, but the private use of these is unlikely to disturb the site. The area is evidently used privately for seasonal waterfowl hunting, but may be little visited at other times.

Sun Cove Shrub-steppe The Sun Cove Shrub-steppe site is located just upstream of the Sun Cove Riparian site on the east bank of Lake Entiat at RM 492.4 to 492.4. Most of this site is owned by the Chelan PUD and is one of the largest tracts of Shrub-steppe habitat south of Beebe Bridge. This site is approximately 2,700 feet long and 1,800 feet wide. The first 800 feet from the shore of Lake Entiat is relatively flat with small rolling hills and sandy substrates. This relatively flat area leads into a shallow, relatively narrow depression that runs almost the entire length of the site, essentially bisecting the site. Beyond this shallow depression the landscape becomes considerably steeper and the substrate becomes rocky. The site is bordered by an orchard on the upslope margin. Although Shrub-steppe is the dominant habitat within the Sun Cove Shrub-steppe site, the landscape of the site results in three distinct vegetation zones.

The flat portion of the site contains relatively open Shrub-steppe habitat with areas mapped as Sand Dune. Bitterbrush was the dominant species, with rabbitbrush and big sagebrush of secondary importance. Percent cover was low in the high shrub layer (5-12 percent) and moderate in the low shrub layer (33-37 percent). Ground cover was moderate (42-65 percent), with cheatgrass the dominant species. Several plant species unique to sand dune shrub-steppe habitats were found in this area during botanical surveys, including dune evening primrose (Oenothera pallida), lance-leaf scurf-pea (Psoralea lanceolata), turpentine cymopteris (Cymopteris terebinthinus), Indian ricegrass (Oryzopsis hymemoides), wing-nut cryptantha (Cryptantha pterocarya), tufted phlox (Phlox caespitosa), shy gilia (Gilia sinuata), and veiny dock (Rumex venosus) (F. Caplow, personal communication).

The shallow depression bisecting the site has a mixture of coyote willow thickets, small black cottonwood stands, and an emergent wetland. These habitats likely receive surface runoff from the adjacent steep slopes, which is stored in the shallow depressions. The coyote willow thickets and

Rocky Reach Project No. 2145 Draft Study Report SS/2493 Page 4-14 November 9, 2000 RTE Wildlife & Cover-type Mapping the small black cottonwood stands are interspersed along the length of the shallow depression with the willow thickets being more abundant near the downstream portion of the site and the cottonwood stands more prevalent near the upstream potion of the site. The willow thickets were moderately dense (33 to 52 percent cover) and in some areas mixed with shrub-steppe vegetation. The black cottonwood stands were relatively small, typically with fewer than 10 trees, but provided moderate to dense tree cover (33 to 80 percent). The emergent wetland is located near the upstream end of the shallow depression near the Sun Cove residential development. This wetland had dense herbaceous cover ranging from 75 to 100 percent with cattail, common reed, and reed canarygrass the most abundant species.

The steep portion of the site contains relatively dense shrub-steppe habitat with an abundance of exposed rock and boulders. Bitterbrush was the dominant species in this area, with rabbitbrush and big sagebrush of secondary importance. Percent cover was low in the high shrub layer (7-17 percent) and moderately dense in the low shrub layer (45-65 percent). Ground cover was moderate (45-70 percent), with cheatgrass the dominant species.

The combination of two types of shrub-steppe habitats and the willow, cottonwood, and emergent habitats makes the Sun Cove Shrub-steppe site unique and valuable as wildlife habitat. In addition to shrub-steppe bird species, several wetland nesting bird species were documented at this site, and a great horned owl (Bubo virginianus) was observed roosting in the cottonwood stands on several occasions. This site currently shows some evidence of recent human disturbance. There is a trail through the flat, sandy portion of the site, which the Chelan PUD has posted to restrict ATV traffic. However, there was evidence of ATV use along this trail and several areas of sand dune have been destabilized and the vegetation disturbed. Furthermore, the Sun Cove residential development is encroaching upon this area. Although less than 640 acres in total area, the shrub-steppe habitats on this site would likely be considered Priority Habitats by WDFW due to the prevalence of high quality native shrub-steppe vegetation and the presence of wetland habitats interspersed within the shrub- steppe habitats.

Beebe Bridge Riparian The Beebe Bridge Riparian site is located upstream of the Chelan River confluence on the west bank of Lake Entiat at RM 503.6 to 504.3. The area occupied by riparian vegetation is approximately 4,200 feet long and varies in width from approximately 50 to 350 feet. Most of the site is downstream of Beebe Bridge (3,500 feet) with a smaller portion upstream (700 feet). The landscape is fairly flat within the riparian zone and the surrounding areas have low to moderate slopes. The adjacent upslope areas are developed and include the City of Chelan wastewater treatment plant, an abandoned fruit processing facility, residential dwellings, and recently cleared orchards.

Riparian Deciduous habitats are abundant and occur throughout the Beebe Bridge Riparian site. Riparian Shrub areas are concentrated at the downstream and upstream ends of the site. There is a large emergent wetland associated with a cove at the downstream end of the site and small, narrow emergent wetlands scattered throughout the site along the shore of Lake Entiat.

Within the Riparian Deciduous portions of the Beebe Bridge Riparian site Siberian elm was the dominant tree species downstream of Beebe Bridge and Lombardy poplar the dominant species

Draft Study Report Rocky Reach Project No. 2145 November 9, 2000 Page 4-15 SS/2493 RTE Wildlife & Cover-type Mapping upstream of Beebe Bridge. Black cottonwood, weeping willow, and black locust were of secondary importance. Canopy cover was moderate to dense in the riparian woodlands (45-87 percent). Snags were moderately abundant. Several large snags (greater than 20 inches DBH) with nest cavities were observed at this site. Shrub cover was variable with high shrub cover (2.0-5.0 m) ranging from 0 to 22 percent and low shrub cover (0.5-2.0 m) ranging from 15 to 75 percent. Himalayan blackberry was the most abundant shrub species with white alder, coyote willow, black locust, and Siberian elm of secondary importance. Ground cover was variable, ranging from 5 to 80 percent, with reed canarygrass and western poison ivy the most abundant herbaceous species. Downed woody debris cover ranged from 7 to 27 percent and consisted of small and large limbs and downed trees. There were also several large brush piles in this site as a result of people dumping brush clippings.

Within the Riparian Shrub portions of the Beebe Bridge Riparian site there was little or no tree cover (0-17 percent). These habitats had moderate shrub cover with high shrub cover (2.0-5.0 m) ranging from 27 to 55 percent and low shrub cover (0.5-2.0 m) ranging from 17 to 67 percent. Coyote willow, white alder, Himalayan blackberry and red-osier dogwood were the dominant shrub species. Ground cover was variable (17-85 percent), with reed canarygrass and western poison ivy the most abundant herbaceous species. Downed woody debris cover was minimal and consisted of small limbs.

The large emergent wetland at the downstream end of the site is associated with a cove of Lake Entiat and is periodically flooded. This emergent wetland had thick herbaceous cover (75-95 percent), with reed canarygrass and cattail the dominant species. The narrow, fringing emergent wetlands scattered along the shoreline were variable in percent cover (17-85 percent cover), and consisted primarily of reed canarygrass, with cattail and softstem bulrush of secondary importance.

The landscape and vegetation within the Beebe Bridge Riparian site is highly disturbed with evidence of land alteration and a high prevalence of non-native species. There is evidence of significant fill in some areas of this site, probably resulting in loss of wetlands, loss of native vegetation, and the invasion by non-native plant species. Both of the dominant tree species of this site, Siberian elm and Lombardy poplar, are non-native species with habitat values inferior to native tree species. Himalayan blackberry, one of the dominant shrubs of this site, is also non-native. Although many birds and small mammals use Himalayan blackberry for food and cover, this species often forms extremely dense thickets that displace native vegetation. There is also evidence of recent trash dumping, vehicular traffic, and non-designated camping on this site. Despite the high level of disturbance, the riparian and wetland habitats on this site might be considered Priority Habitats as defined by WDFW (1996).

Gallagher Flats The Gallagher Flats site is located upstream of Beebe Bridge on the west bank of Lake Entiat at RM 506.7 to 507.3. This site is approximately 160 acres and was purchased by the Chelan PUD in the 1960’s for WDFW as part of a mitigation package for the Rocky Reach Project. The Washington State Department of Transportation (WDOT) acquired the land from the Chelan PUD for a highway right-of-way in the early 1980’s. Gallagher Flats continues to be managed by WDFW for public hunting. This site is roughly triangular in shape and is confined in a relatively flat basin surrounded

Rocky Reach Project No. 2145 Draft Study Report SS/2493 Page 4-16 November 9, 2000 RTE Wildlife & Cover-type Mapping by steep, arid hills to the north and Lake Entiat to the south. Highway 97 runs though this site parallel to Lake Entiat.

The majority of the site is north of Highway 97 and consists primarily of meadow-like habitat dominated by forbs and grasses, including knapweed, vetch (Vicia spp.), showy milkweed (Asclepias speciosa), mullein, and spreading dogbane (Apocynum androsaemifolium). Asparagus (Asparagus officionalis) grows throughout this meadow area and many people visit this site to collect it. This area has some small patches of emergent vegetation along the back (northern) edge of the meadow area. These patches are confined to small depressions and tire ruts, and probably receive surface runoff from the surrounding steep hills. Based on 1981 USGS topographic maps the wetland area appeared to be larger prior to construction of the new Highway 97. Old drainage ditches were also observed on the site. Roughly in the center of this large meadow area is a shrub thicket, consisting primarily of coyote willow with lesser amounts of Himalayan blackberry and pearhip rose (Rosa woodsii). On the western edge of the meadow area and also along Highway 97 there are patches of shrub-steppe habitat dominated by bitter brush with lesser amounts of squaw currant and rabbitbrush.

In the easternmost corner of the meadow area is a stand of large black cottonwood and Siberian elm. Although this stand is not along Lake Entiat, it has structural characteristics similar to Riparian Deciduous habitats and was mapped as such. Canopy cover in this stand was high ranging from 72 to 87 percent. This stand had some of the largest trees of the habitats sampled with a mean DBH of 17.4 inches (range of 4.0 to 75.0 inches). Snags were moderately abundant and large (mean DBH of 20.0 inches). This stand had a relatively open understory with high shrub cover (2.0-5.0 m) ranging from 12 to 17 percent and low shrub cover (0.5-2.0 m) ranging from 0 to 5 percent. Understory species consisted of black cottonwood, Siberian elm, black locust, and western sumac (Rhus glabra). Herbaceous ground cover was variable, ranging from 17 to 65 percent. This was the only area sampled that had a significant amount of leaf litter.

The portion of the Gallagher Flats site south of Highway 97 consists primarily of Shrub-steppe with a small pocket of riparian vegetation along Lake Entiat. The Shrub-steppe habitat had gently rolling hills with small areas of sand dune. Bitterbrush was the dominant species in this area, with big sagebrush and rabbitbrush of secondary importance. Percent cover was low in the high shrub layer (17-22 percent) and moderate in the low shrub layer (37-42 percent). Ground cover was moderate (52-60 percent), with cheatgrass the dominant species. The riparian area consisted predominately of Riparian Shrub, with some emergent vegetation and scattered black cottonwoods. White alder, coyote willow, and Himalayan blackberry were the most abundant shrub species. The emergent area is periodically flooded by Lake Entiat and consists primarily of reed canarygrass with a fringe of western poison ivy.

The prevalence of weedy species and the presence of drainage ditches suggest that the hydrology of the site has been altered, although mesic conditions still prevail. Furthermore, the construction of Highway 97 may have isolated this site hydraulically from Lake Entiat. There is also evidence of recent trash dumping, vehicular traffic, and non-designated camping on this site, particularly in the cottonwood stand. Portions of the riparian and wetland habitats on this site might be considered Priority Habitats as defined by WDFW (1996).

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Uplake Shrub-steppe The Uplake Shrub-steppe site is the most upstream Intensive Study Site located on the east bank of Lake Entiat. The downstream limit of this site was near the confluence of Long Draw (RM 510.5) and the upstream limit was near an area of exposed rock and cliff at RM 511.9. This site is a relatively flat, delta-shaped area on a bend in Lake Entiat. The upslope limit of this site was at approximately 800-feet elevation. This is the largest site surveyed, with an approximate length of 6,700 feet and a maximum width of approximately 1,300 feet.

The Uplake Shrub-steppe site consisted primarily of Shrub-steppe of varying densities and species composition. There were abundant grassy openings interspersed with the shrub dominated areas. Although survey efforts were concentrated in the area described above, it is important to note that the Shrub-steppe habitats on this site are part of a much larger tract of this cover-type.

Big sagebrush was the dominant species in this area, with bitterbrush, rabbitbrush and northern buckwheat of secondary importance. Percent cover was low in the high shrub layer (0-12 percent) and moderate to dense in the low shrub layer (22-62 percent). Ground cover was moderate to dense (52-92 percent), with cheatgrass and bunchgrass dominant. Bunchgrass was more abundant on this site than any other shrub-steppe site sampled.

The Uplake Shrub-steppe site is the most remote site surveyed and as a result had limited evidence of human disturbance. There are several fence rows and evidence of grazing, but no livestock were observed in the area during this study. This was the only site where loggerhead shrikes (Lanius ludovicianus) were observed, which might be related to the remoteness of the site. Due to the large size of this site, prevalence of native vegetation, and limited disturbance, the shrub-steppe habitats present would probably be considered Priority Habitats as defined by WDFW (1996).

General Description of Roving Sites In addition to the seven Intensive Study Sites, 11 Roving Sites were surveyed for habitat characteristics and wildlife use. General site characteristics for these sites are provided in Table 4-4 and a brief discussion of the habitats present at these sites follows.

Riparian Habitats Riparian habitats at the Roving Sites were generally small and narrow, and consisted of interspersed small patches of Riparian Deciduous, Riparian Shrub, and Palustrine Emergent Wetlands. Due to the narrowness of these habitats, they often consisted of a single row of trees or shrubs along the shore of Lake Entiat. In some cases the narrow nature of these habitats was due to steep shoreline banks. However, many of the riparian habitats at the Roving Sites had evidence of past disturbance such as clearing or fill which probably limited their size. Past disturbance most likely also contributed to the prevalence of non-native or invasive plant species at these sites. However, these sites are representative of many of the small patches of riparian vegetation found throughout the study area.

Shrub-steppe Habitats Shrub-steppe habitats at the Roving Sites ranged from very small patches on islands (less than 1 acre) to relatively large tracts (approximately 75 acres) on the mainland. Species composition and vegetative structure were similar to the Shrub-steppe at the Intensive Survey Sites. Shrub-steppe

Rocky Reach Project No. 2145 Draft Study Report SS/2493 Page 4-18 November 9, 2000 RTE Wildlife & Cover-type Mapping habitats at the Roving Sites generally showed evidence of past grazing and had an abundance of cheatgrass. The large tract of Shrub-steppe habitat sampled (Bundy Shrub-steppe) had a prevalence of native plant species and might be considered a Priority Habitat by WDFW. Adjacent lands are primarily occupied by orchards and there is currently residential construction underway near this site.

Exposed Rock/Shrub-steppe Goosetail Rock and the Chelan Butte Wildlife Management Area (WMA) both consisted primarily of exposed bedrock and cliffs with some sparse shrub-steppe vegetation at the base of the slopes. Due to the rugged nature of the terrain at both of these sites and the limited access to the Chelan Butte WMA, there was relatively limited evidence of disturbance. The cliffs at both Goosetail Rock and the Chelan Butte WMA would probably be considered Priority Habitats by WDFW. There are some areas of talus along the railroad adjacent to the Chelan Butte WMA, and these areas might be considered Priority Habitats by WDFW.

Recreational The Recreational areas surveyed have habitat components that are valuable to certain wildlife species groups. Large trees that provide suitable nesting habitat for tree and cavity nesting birds were abundant at the sites surveyed. However, these areas did not have well-developed shrub layers or diverse herbaceous vegetation. Herbaceous ground cover at the sites surveyed consisted almost entirely of maintained lawns, which have limited wildlife value.

4.2 Vertebrate Species Surveys

4.2.1 Bird Sureys

4.2.1.1 Breeding Bird Surveys Seventy-three species of birds were documented on the Intensive and Roving Study Sites combined during the breeding bird surveys. An additional eleven species of birds were seen outside of the survey periods and were recorded as incidental observations. Bird species that potentially occur within the study area during the breeding season are given in Appendix C (Table C-1).

Six species of birds documented during the RTE Wildlife Study are considered Priority Species by WDFW. These are common loon (Gavia immer), great blue heron, bald eagle (Haliaeetus leucocephalus), osprey (Pandion haliaetus), golden eagle (Aquila chrysaetos), and loggerhead shrike. A discussion of each potentially occurring RTE wildlife species and documented RTE wildlife species is provided in Section 4.2.5.

The number of species observed during point count surveys ranged from 13 at the Bundy shrub- steppe site to 39 at the Entiat River site (Table 4-5 and Table 4-6). The Entiat River site has extensive and diverse riparian habitats and provides abundant nesting habitat for a variety of bird species. Species richness values may be influenced by sampling effort, and the number of points sampled did vary among the sites surveyed. To address this, the mean number of species detected per survey at each point was calculated. The mean number of species observed per survey ranged from 2.3 at the Islands downstream of the Entiat River to 7.1 at the Chelan Falls Park. The low number of species detected at the island sites is most likely do to their small size and limited

Draft Study Report Rocky Reach Project No. 2145 November 9, 2000 Page 4-19 SS/2493 RTE Wildlife & Cover-type Mapping available habitat. Chelan Falls Park has areas with large trees and some fringing riparian habitats that provide suitable nesting habitat for a variety of bird species.

Relative abundance (the mean number of individual birds observed per survey) ranged from 3.1 at the Islands downstream of the Entiat River to 24.3 at Goosetail Rock. The high relative abundance at Goosetail Rock is due to the large number of cliff swallows and rock doves (Columba livia) nesting on the cliffs in this area.

Because some of the sites surveyed consisted of several habitat types, breeding bird survey data for the Intensive Sites and Roving Sites combined was also summarized by the habitat type in which each individual survey point was located (Table 4-7). The number of species observed per habitat type ranged from 28 for exposed rock to 60 for riparian habitats. The mean number of species observed per survey ranged from 3.4 for shrub-steppe habitats to 6.0 for riparian habitats. Riparian habitats have the most diverse and well-developed vegetative structure of the habitats surveyed. These habitats typically have interspersed patches of deciduous, shrub, and emergent vegetation. This structural diversity provides suitable nesting habitat for many bird species. Riparian habitats had the most diverse species assemblage, with 15 species observed solely in this habitat. Less structurally diverse habitats can not support as many species. Shrub-steppe habitats typically have well-developed shrub layers and moderately abundant herbaceous cover, but lack trees. This limits the available nesting habitat in shrub-steppe habitats. Three species, ring-necked pheasant (Phasianus colchicus), loggerhead shrike, and lark sparrow (Chondestes grammacus) were observed solely in shrub-steppe habitats. Nesting habitat within exposed rock habitat is limited to rock crevices and very sparse vegetation. Three bird species, chukar (Alectoris chukar), rock dove, and canyon wren, were observed solely within exposed rock habitat. The mean number of species detected per survey at recreational facilities (5.8) was similar to riparian habitats (6.0). Recreational facilities often have abundant large trees that provide suitable nesting habitat for tree and cavity nesting birds. However, recreational facilities typically do not have well-developed shrub layers or diverse herbaceous vegetation, which typically consists almost entirely of maintained lawns with limited wildlife value. Although the recreational facilities sampled typically lack well-developed shrub and herbaceous cover, they usually have adjacent riparian habitats due to their shoreline locations. Several species of birds, including American robin (Turdus migratorius), European starling (Sturnus vulgaris), and Brewer’s blackbird (Euphagus cyanocephalus), commonly forage on lawns within recreational facilities. Only one species, dark-eyed junco (Junco hyemalis), was observed solely in recreational facilities.

Relative abundance ranged from 5.4 in shrub-steppe habitats to 12.2 in recreational facilities. The high relative abundance documented at recreational facilities is due primarily to high numbers of European starlings, Brewer’s blackbirds, and tree swallows (Tachycineta bicolor), which are very tolerant of human activities. Abundant tree cavities also provide suitable nesting habitat for cavity nesters, such as European starlings and tree swallows. Exposed rock (9.8) and riparian (9.8) habitats had similar relative abundance values. The relatively high relative abundance documented at exposed rock habitats is due to the presence of cliff nesting colonial species, such as cliff swallows and rock doves. Riparian habitats had a more diverse species assemblage. Shrub-steppe habitats had the lowest relative abundance, possibly because they have limited vegetative structure compared to

Rocky Reach Project No. 2145 Draft Study Report SS/2493 Page 4-20 November 9, 2000 RTE Wildlife & Cover-type Mapping riparian habitats and recreational facilities. In addition there were no colonial species nesting in shrub-steppe habitats.

Because the majority of the breeding bird survey effort was focused on the seven Intensive Study Sites, a brief discussion of the results at each site is provided. Furthermore, these sites have unique habitat characteristics and associations that warrant additional discussion.

Turtle Rock Twenty-seven species of birds were documented at Turtle Rock during the point count surveys (Table 4-5). Although this site had a relatively low number of species documented and mean number of species detected per survey (4.2), it had the second highest relative abundance (10.5) of the Intensive Sites. European starling, violet-green swallow (Tachycineta thalassina), cliff swallow, and black-billed magpie (Pica pica) were the most abundant species observed. The high relative abundance documented at this site is due to the presence of colonial nesting swallows. There were no bird species observed solely at Turtle Rock. Several bald eagles and an osprey were observed flying over Turtle Rock, but no evidence of nesting was found. A great horned owl nest was found on the adjacent Lincoln Rock.

There are two distinct geologic/vegetation sections of Turtle Rock which provide a variety of nesting habitats for bird species. The first section consists of the downstream third of the island, which has gently rolling topography with some exposed bedrock and boulders. Shrub-steppe is the dominant vegetation cover-type and there are narrow riparian habitats along much of the shoreline in this section. Bird species observed in this shrub-steppe area include black-billed magpie, western meadowlark (Sturnella neglecta), and northern flicker (Colaptes auratus). Riparian habitats in this section were generally narrow, although a riparian shrubland and emergent wetland associated with a cove on the south shore was large enough to provide nesting habitat for wetland nesting species, including red-winged blackbird and song sparrow (Melospiza melodia). The upstream section of Turtle Rock consists mostly of steep slopes with abundant boulders, exposed bedrock, and cliffs. There is also a relatively flat open area between this section and the first. Much of this section of Turtle Rock was burned by an accidental fire in 1999. Due to the fire and the rocky substrates, this section of Turtle Rock has very sparse shrub-steppe vegetation. However, exposed rock, boulders, and cliffs are the dominant cover feature in this section. Several species of birds that nest in exposed rock and cliff habitats were observed in this section including cliff swallow, rock wren, and canyon wren.

Entiat River Thirty-nine species of birds were documented at the Entiat River during the point count survey (Table 4-5). Although this site had the highest number of species documented, it had only the third highest mean number of species detected per survey (5.0) and the third highest relative abundance (8.1). Red-winged blackbird, European starling, and violet-green swallow were the most abundant species observed. During the point count surveys three bird species were observed solely at Entiat River, American dipper (Cinclus mexicanus), common yellowthroat, and red-eyed vireo (Vireo olivaceus). An osprey nest was observed to the south of the Entiat River in a large conifer in the Swakane Wildlife Area.

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Riparian deciduous and riparian shrub habitats are abundant and interspersed along the Entiat River within the study area. The vegetation within the Entiat River riparian habitats is relatively undisturbed with a high prevalence of native wetland species and well-developed structural components. These habitats provide abundant nesting and foraging habitat for riparian and wetland nesting bird species. Snags were not abundant but nest cavities were observed in dead limbs of large black cottonwood trees. There is a well-developed emergent wetland located in the backwater area near the confluence with Lake Entiat. Several marsh dwelling bird species were observed in this area including mallard, Canada goose (Branta canadensis), wood duck (Aix sponsa), common merganser (Mergus merganser), red-winged blackbird, and common yellowthroat.

Sun Cove Riparian Twenty-six species of birds were documented at Sun Cove Riparian Site during the point count surveys (Table 4-5). Although this site had the third lowest number of species observed, it had the second highest mean number of species detected per survey (5.8). The overall relative abundance (8.0) was similar to the Entiat River (8.1). Red-winged blackbird, yellow warbler (Dendroica petechia), and American robin were the most abundant species observed. During the point count surveys, no bird species was observed solely at the Sun Cove Riparian Site.

Riparian deciduous habitats dominate the Sun Cove Riparian site, but there are also riparian shrub, emergent wetland, and a small area of shrub-steppe habitat. The vegetation within the Sun Cove Riparian site is relatively undisturbed with a high prevalence of native wetland species and well- developed structural components. These habitats provide abundant nesting and foraging habitat for riparian and wetland nesting bird species. Snags were not abundant but nest cavities were observed in dead limbs of large black cottonwood trees. Emergent wetlands were found in two areas within the Sun Cove Riparian site. One emergent wetland was associated with the permanent and temporary pools located in the upstream portion of the site. These wetlands were dominated by cattail, and several pairs of red-winged blackbirds were observed nesting in this wetland. The second emergent wetland complex was located along the shoreline in the downstream portion of the site. These wetlands were dominated by softstem bulrush, and great blue herons and mallards were observed frequently in these wetlands.

Sun Cove Shrub-steppe Thirty-one species of birds were documented at the Sun Cove Shrub-steppe site during the point count surveys (Table 4-5). Although this site had the third highest number of species observed, it had the second lowest overall relative abundance (7.2). Spotted towhee (Pipilo maculatus), white- crowned sparrow (Zonotrichia leucophrys), American goldfinch (Carduelis tristis), and brown- headed cowbird (Molothrus ater) were the most abundant species observed. During the point count surveys two bird species, calliope hummingbird (Stellula calliope) and ring-necked pheasant were observed solely at the Sun Cove Shrub Steppe Site.

Although, shrub-steppe vegetation is the dominant habitat within the Sun Cove Shrub-steppe site, the landscape of the site results in three distinct vegetation zones. The zone nearest the shore of Lake Entiat is relatively flat with small rolling hills and sandy substrates. This zone contains relatively open shrub-steppe habitat and areas of sand dune. This relatively flat area leads into a shallow, relatively narrow depression that runs almost the entire length of the site, essentially

Rocky Reach Project No. 2145 Draft Study Report SS/2493 Page 4-22 November 9, 2000 RTE Wildlife & Cover-type Mapping bisecting the site. The shallow depression bisecting the site has a mixture of coyote willow thickets, small black cottonwood stands, and an emergent wetland. Beyond this shallow depression the landscape steepens considerably. This steep portion of the site contains relatively dense shrub-steppe habitat with an abundance of exposed rock and boulders. The combination of two types of shrub- steppe habitats and the willow, cottonwood, and emergent habitats makes the Sun Cove Shrub- steppe site unique and valuable as wildlife habitat. In addition to shrub-steppe bird species, several wetland nesting bird species were documented at this site and a great horned owl was observed roosting in the cottonwood stands on several occasions.

Beebe Bridge Riparian Thirty-two species of birds were documented at the Beebe Bridge Riparian site during the point count surveys (Table 4-5). Of the Intensive Sites surveyed this site had the second highest number of species observed, the highest mean number of species detected per survey (7.0), and the highest relative abundance (10.7). Cliff swallow, American goldfinch, brown-headed cowbird, and yellow warbler were the most abundant species observed. The high relative abundance documented at this site was due, in part, to the presence of colonial nesting swallows. During the point count surveys, no bird species was observed solely at the Beebe Bridge Riparian site. A great horned owl was heard calling at this site on several occasions.

Riparian deciduous habitats are abundant and occur throughout the Beebe Bridge Riparian site. Riparian shrub areas are concentrated at the downstream and upstream ends of the site. There is a large emergent wetland associated with a cove at the downstream end of the site and small, narrow emergent wetlands scattered throughout the site along the shore of Lake Entiat. The landscape and vegetation within the Beebe Bridge Riparian site is highly disturbed with evidence of land alteration and a high prevalence of non-native species. There is evidence of significant fill in some areas of this site, which has probably resulted in loss of wetlands, loss of native vegetation, and the invasion of non-native plant species. Both of the dominant tree species of this site, Siberian elm and Lombardy poplar, are non-native species. These trees are not as valuable to wildlife as native tree species. However, snags were moderately abundant and several large snags (greater than 20 inches DBH) with nest cavities were observed at this site. Himalayan blackberry, one of the dominant shrubs of this site, is also non-native. Although many birds use Himalayan blackberry for food and cover, this species often forms extremely dense thickets that displace native vegetation. Despite this high level of disturbance the Beebe Bridge Riparian site had some of highest measures of bird species richness and abundance of the Intensive Study sites. This may be because bird species select habitats based on habitat structure rather than plant species composition; structurally this site was similar to other less disturbed riparian sites. Furthermore, colonial nesting swallows were among the most abundant species at this site and they were most likely nesting in the adjacent industrial buildings.

Gallagher Flats Twenty-three species of birds were documented at Gallagher Flats during the point count surveys (Table 4-5). Of the Intensive Sites surveyed this site had the second lowest number of species observed, the third lowest mean number of species detected per survey (4.7), and the third lowest relative abundance (7.4). Black-billed magpie, American goldfinch, and northern oriole (Icterus bullockii) were the most abundant species observed. During the point count surveys, no bird species

Draft Study Report Rocky Reach Project No. 2145 November 9, 2000 Page 4-23 SS/2493 RTE Wildlife & Cover-type Mapping was observed solely at Gallagher Flats. One adult golden eagle was observed at Gallagher Flats in early September 2000 during habitat surveys.

Gallagher Flats is roughly triangular in shape and is confined in a relatively flat basin surrounded by steep, arid hills to the north and Lake Entiat to the south. Highway 97 runs though this site parallel to Lake Entiat. The majority of the site is north of Highway 97 and consists primarily of meadow-like habitat dominated by weedy species. Roughly in the center of this large meadow area is a shrub thicket. In the easternmost corner of the meadow area is a stand of large black cottonwoods and Siberian elms. This stand has structural characteristics similar to riparian deciduous habitats. This stand had some of the largest trees of the habitats sampled with a mean DBH of 17.4 inches (range of 4.0 to 75.0 inches). Snags were moderately abundant and large (mean DBH of 20.0 inches). The cottonwood stand provided most of the nesting habitat available in this portion of the site. The portion of the Gallagher Flats site south of Highway 97 consists primarily of shrub-steppe habitats with a small pocket of riparian vegetation along Lake Entiat. The shrub- steppe habitat had gently rolling hills with small areas of sand dune. The riparian area consisted predominately of riparian shrub habitat with some emergent vegetation and scattered black cottonwoods. The emergent area is periodically flooded by Lake Entiat and consists primarily of reed canarygrass with a fringe of poison ivy. Although there are a variety of habitat types available at Gallagher Flats, this site had relatively low measures of breeding bird species richness and abundance. This is due to the presence of the large, weedy meadow. This meadow accounted for a large portion of the site and few birds were observed in this habitat. Most of the birds observed were in the cottonwood stand and the riparian habitats.

Uplake Shrub-steppe Fifteen species of birds were documented at the Uplake Shrub-steppe site during the point count surveys (Table 4-5). Of the Intensive Sites surveyed this site had the lowest number of species observed, the lowest mean number of species detected per survey (2.4), and the lowest relative abundance (4.0). The low measures of breeding bird species richness and abundance are due, in part, to the relatively limited vegetative structural diversity of this site. Western meadowlark, Brewer’s blackbird, loggerhead shrike, and lark sparrow were the most abundant species observed. During the point count surveys, one species of bird, loggerhead shrike, was observed solely at the Uplake Shrub-steppe.

The Uplake Shrub-steppe site consisted primarily of shrub-steppe vegetation of varying densities and species composition. There were abundant grassy openings interspersed with the shrub dominated areas. This site is part of a much larger tract of shrub-steppe habitat and provides abundant nesting habitat for shrub-steppe nesting species. However, compared to the other sites surveyed this site has relatively limited vegetative structural diversity. The Uplake Shrub-steppe site is the most remote site surveyed and as a result had limited evidence of human disturbance. There are several fence rows and evidence of grazing, but no livestock were observed in the area during this study. This was the only site were loggerhead shrikes were observed, which may be related to the remoteness of the site. Despite, the large size of the site and relatively undisturbed condition, no shrub-steppe obligate bird species were observed on this site.

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4.2.1.2 Migratory and Wintering Bird Surveys Twenty waterbird survey locations were established along Lake Entiat from Turtle Rock to just below the Wells Dam (Table 4-8). Sites were selected based on the presence of suitable foraging habitat, such as aquatic weed beds, observations of waterfowl concentrations during preliminary surveys, and viewing and access conditions. Of the 20 sites, six were located on the east bank of Lake Entiat and 14 were located on the west bank of Lake Entiat. Observations were made in October 1999, February 2000, and late March 2000 to determine species occurrence on Lake Entiat during the fall, winter, and spring.

Twenty-seven waterbird species were documented during the wintering waterbird surveys. American coot (Fulica americana) and American widgeon (Anas americana) were the most abundant waterbirds observed with a total of 4,872 American coots and 2,145 American widgeons observed. Scaup species (Aytha spp.), ring-necked duck (Aytha collaris), and ruddy duck (Oxyura jamaicensis) were also commonly observed throughout Lake Entiat but the number of individuals observed were much less than American coots or American widgeons. Over half of the waterbird individuals documented over all seasons were observed during the October survey (50.5 percent), with the winter and spring surveys accounting for 32.2 and 17.3 percent of all waterbirds observed, respectively. The large number of birds observed in the fall is most likely due to migrating birds stopping over on Lake Entiat to replenish depleted energy stores before continuing migration. These birds occupy the lake only temporarily resulting in the lower number of true winter resident birds documented in February. By late March many of the wintering birds had left for their breeding grounds.

Site six, located at Entiat Park, had the greatest number and diversity of waterbirds documented. 3,458 individuals of 18 species where observed throughout Entiat Park over the three survey periods. This area consists of several protected coves with abundant aquatic vegetation that provide suitable loafing and foraging habitat. The Entiat River and park area is also where the highest concentration of bald eagles were observed with several seen feeding on American coots.

Several species of birds that were documented during the RTE Wildlife Study are listed as State Priority Species, State Candidate Species, or State or Federally Listed Species. These include common loon, great blue heron, bald eagle, and loggerhead shrike. Common loon was observed 33 times at 12 of the 20 survey locations. Eight of these 12 locations were from Goosetail Rock upstream and almost 70 percent of all common loon observations were from the Chelan River upstream, where the Lake Entiat narrows and becomes more riverine. The number of common loons documented per site ranged from 1 to 10; ten being observed at site 18 (RM 511.0). Great blue herons were observed at six sites during the survey period. One individual was documented at each of these sites and five of the six total individuals observed were downstream of Goosetail Rock. Bald eagles were observed 17 times at ten sites during the survey period. The Entiat River confluence area had the highest concentration of bald eagles with six individuals observed there during the February survey. One loggerhead shrike was observed at the survey site near Turtle Rock during the February survey. A discussion of each potentially occurring RTE wildlife species and documented RTE wildlife species is provided in Section 4.2.5.

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4.2.2 Small Mammal Surveys Ten species of small mammals were documented during the RTE Wildlife Study by standardized trapping methods. Small mammal species that potentially occur within the study area are given in Appendix C (Table C-2). Large mammal species documented by incidental observation are given in Appendix C, Table C-2.

No species of small mammal documented during the RTE Wildlife Study is listed as a State Priority Species, State Candidate Species, or State or Federally Listed Species. A discussion of each potentially occurring RTE wildlife species and documented RTE wildlife species is provided in Section 4.2.5.

The number of small mammal species captured during trapping ranged from six at the Sun Cove Shrub-steppe site to two at the Uplake Shrub-steppe site (Table 4-9). The relative abundance (number of captures per 100 trap nights) of small mammals ranged from 15.4 for Gallagher Flats to 0.8 for Turtle Rock. Deer mouse (Peromyscus maniculatus) was the most abundant small mammal captured overall and was the most abundant species at Gallagher Flats and Beebe Bridge.

Sherman live traps had the highest capture rate (10.4) followed by pitfalls (9.0), snap traps (7.7), and Havahart traps (3.1) (Table 4-10). The Sun Cove Shrub-Steppe site had the highest pitfall capture rate (16.9), while Gallagher Flats had the highest snap trap capture rate (15.3), live trap capture rate (34.4), and Havahart capture rate (16.7).

Due to the high capture rate of deer mice, omnivores comprised the highest percentage of captures at four of the seven sites (Table 4-11). Gallagher Flats had the highest percentage of omnivorous small mammals documented. Insectivorous small mammal species were captured at five of the seven sites with the highest percentage of insectivores captured at the Entiat River. The Entiat River had the highest mean percentage of fallen log cover and downed woody debris and moderate to high amounts of vegetative cover (Table 4-12), providing abundant small mammal foraging and hiding cover. Herbivorous small mammals were captured at six of the seven sites and comprised a small but fairly consistent percentage of captures at most sites. The highest percentage of herbivorous small mammals was documented at Turtle Rock. This is most likely an artifact of the small number of captures overall at Turtle Rock, which had the lowest overall capture rate and the fewest number of species captured.

Turtle Rock Only two species of small mammals were captured at Turtle Rock (Table 4-9). Turtle Rock had the lowest overall capture rate of all the sites surveyed (0.8), with montane vole (Microtus montanus) being the most abundant species captured, comprising 75.0 percent of all captures. Small mammals were captured in only pitfall and snap traps on Turtle Rock, with a pitfall capture rate of 2.5 and a snap trap capture rate of 0.3 (Table 4-10). Turtle Rock had the highest herbivore capture rate (75%), with omnivorous small mammals being the only other feeding group captured (Table 4-11). This is most likely an artifact of the small number of captures overall at Turtle Rock, which had the lowest overall capture rate and the fewest number of species captured.

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There are two distinct geologic/vegetation sections of Turtle Rock which provide a variety of habitats for small mammals. The first section consists of the downstream third of the island, which has gently rolling topography with some exposed bedrock and boulders. Shrub-steppe is the dominant vegetation cover-type and there are narrow riparian habitats along much of the shoreline in this section. The abundance of exposed rocks and boulders in this shrub-steppe area may provide cover for small mammals. Riparian habitats in this section are generally narrow, with the exception of a riparian shrub habitat and emergent wetland associated with a cove on the south shore. A dense stand of Russian olive in this area has nearly complete canopy closure with abundant litter and downed woody debris. The adjacent emergent wetland has abundant herbaceous vegetation. This riparian shrub/emergent wetland complex provides abundant foraging and hiding cover for small mammals. All the small mammals captured at Turtle Rock were in the shrub-steppe or riparian habitats of this section.

The upstream section of Turtle Rock consists mostly of steep slopes with abundant boulders, exposed bedrock, and cliffs. There is also a relatively flat open meadow area between this section and the first. Much of this section of Turtle Rock was burned by an accidental fire in 1999. Due to the fire and the rocky substrates, this section of Turtle Rock has very sparse shrub-steppe vegetation. However, there is abundant cover in the form of crevices among the exposed rock, boulders, and cliffs. Turtle Rock had the highest mean percent rock and boulder cover (Table 4-12). Despite the available cover no small mammals were captured in this section of Turtle Rock. This may be due, in part, to the fire that burned much of this area in 1999.

Five species of small mammals were captured at the Entiat River (Table 4-9). The Entiat River had the third lowest capture rate (6.7). Vagrant shrew was the most abundant species captured, comprising 46.3 percent of all captures. Pitfalls (11.9) and snap traps (5.5) had the highest capture rates at this site (Table 4-10). The Entiat River had a relatively diverse small mammal population, with insectivores comprising 60.9 percent of captures, omnivores 23.2 percent, and herbivores 15.9 percent (Table 4-11). The Entiat River was also one of only two sites where the long-tailed vole (Microtus longicaudus) was captured.

Riparian deciduous, riparian shrub, and emergent wetland habitats are abundant and interspersed along the Entiat River within the study area. The vegetation within the Entiat River riparian habitats is relatively undisturbed with a high prevalence of native wetland species and well-developed structural components. High amounts of fallen logs and downed woody debris are present throughout the riparian corridor (Table 4-12). There is a well-developed emergent wetland located in the backwater area near the confluence with Lake Entiat. Muskrat and beaver (Castor canadensis) were observed in this area. The diversity of vegetative and structural cover present within riparian habitats along the Entiat River provide abundant forage and cover for small mammal species. In addition, these habitats are connected along a continuous riparian corridor allowing small mammals to move freely among them. The riparian zone also consists of several small islands, which may be separated from the mainland during and after high flow events. This would temporally isolate resident small mammal populations, but dispersal and colonization can occur after high flows subside. In addition to the riparian habitats along the river, there is rip-rap, boulder, and talus habitat along the Entiat River Road that may provide cover for small mammals.

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Sun Cove Riparian Five species of small mammals were captured at the Sun Cove Riparian site (Table 4-9). This site had the second highest overall capture rate (12.2). Vagrant shrew was the most abundant species captured, comprising 44.3 percent of all captures. Snap traps (13.8) and Sherman live traps (12.5) had the highest capture rates at this site (Table 4-10). The Sun Cove Riparian site had a diverse small mammal population with relatively similar percentages of omnivores (33.6 percent), herbivores (22.1 percent), and insectivores (44.3 percent). This site was one of only two sites where long-tailed vole was captured.

Riparian deciduous habitats dominate the Sun Cove Riparian site, but there are also riparian shrub, emergent wetland, and a small area of shrub-steppe habitat. The vegetation within the Sun Cove Riparian site is relatively undisturbed with a high prevalence of native wetland species and well- developed structural components. Moderate amounts of downed woody debris and leaf litter are present throughout the riparian corridor (Table 4-12). There is also one permanent and one temporary pool with abundant herbaceous vegetation located in the upstream, widest portion of this site. The diversity of vegetative and structural cover present within riparian habitats at the Sun Cove Riparian site provide abundant forage and cover for small mammal species. In addition, these habitats are connected along a continuous riparian corridor allowing small mammals to move freely among them.

Sun Cove Shrub-steppe Six species of small mammals were captured at the Sun Cove Shrub-steppe site, the most of any site sampled for small mammals (Table 4-9). This site had the third highest capture rate (8.0). Great Basin pocket mouse (Perognathus parvus) was the most abundant species captured, comprising 53.8 percent of all captures. The Sun Cove Shrub-steppe site had the highest pitfall capture rate (16.9) and moderate snap trap (5.8) and Sherman live trap (7.8) capture rates (Table 4-10). Small mammals captured at the Sun Cove Shrub-steppe site were almost exclusively omnivores (95%), but individuals from all three feeding groups were present at this site (Table 4-11).

Although, shrub-steppe vegetation is the dominant habitat within the Sun Cove Shrub-steppe site, the landscape of the site results in three distinct vegetation zones. The zone nearest the shore of Lake Entiat is relatively flat with small rolling hills and sandy substrates. This zone contains relatively open shrub-steppe habitat with areas of sand dune. This relatively flat area leads into a shallow, relatively narrow depression that runs almost the entire length of the site, essentially bisecting the site. The shallow depression bisecting the site has a mixture of coyote willow thickets, small black cottonwood stands, and an emergent wetland with abundant herbaceous cover. Beyond this shallow depression the landscape steepens considerably. This steep portion of the site contains relatively dense shrub-steppe habitat with an abundance of exposed rock and boulders. The combination of two types of shrub-steppe habitats and the willow, cottonwood, and emergent habitats makes the Sun Cove Shrub-steppe site unique and valuable as wildlife habitat. In addition, there is limited disturbance on this site resulting in high connectivity among these habitats allowing small mammals to move freely among them.

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Beebe Bridge Riparian Three species of small mammals were captured at the Beebe Bridge Riparian site (Table 4-9). The overall capture rate was moderate compared to the other sites (7.9). Deer mouse was the most abundant species captured, comprising 95.0 percent of all captures. Sherman live traps (20.0) and snap traps (10.1) had the highest capture rates at this site (Table 4-10). Due to the high capture rate of deer mice, the small mammals at the Beebe Bridge Riparian site were almost exclusively omnivorous, though individuals from all three feeding groups were captured (Table 4-11).

Riparian deciduous habitats are abundant and occur throughout the Beebe Bridge Riparian site. Riparian shrub areas are concentrated at the downstream and upstream ends of the site. There is a large emergent wetland associated with a cove at the downstream end of the site and small, narrow emergent wetlands scattered throughout the site along the shore of Lake Entiat. The landscape and vegetation within the Beebe Bridge Riparian site is highly disturbed, with evidence of land alteration and a high prevalence of non-native species. There is evidence of significant fill in some areas of this site, vehicular traffic, and trash dumping, which has probably resulted in loss of wetlands, loss of native vegetation, and the invasion of non-native plant species. Both of the dominant tree species of this site, Siberian elm and Lombardy poplar, are non-native species. These trees are not as valuable to wildlife as native tree species. Himalayan blackberry, one of the dominant shrubs of this site, is also non-native. Although small mammal species may use Himalayan blackberry for food and cover, this species often forms extremely dense thickets that displace native vegetation. There are some large brush and other piles of larger woody debris that have been dumped on this site which provide some cover for small mammals. The low diversity of small mammals (only three species and 95 percent of captures were deer mice) is likely due to this high level of disturbance. Some small mammal species are very sensitive to disturbance of ground cover components. Deer mice, however, are habitat generalists and are often among the first species to colonize disturbed sites.

Gallagher Flats Five species of small mammals were captured at Gallagher Flats (Table 4-9). Gallagher Flats had the highest overall capture rate (15.4), and deer mouse was the most abundant species captured, comprising 79 percent of all captures. Sherman live traps had the highest capture rate (34.4); Havahart traps (16.7), snap traps (15.3) and pitfalls (11.3) were also effective (Table 4-10). Bushy- tailed woodrats were abundant at Gallagher Flats and accounted for most of the Havahart captures. Omnivores made up 97.4 percent of the total captures while 2.6 percent of the total captures were herbivores (Table 4-11).

Gallagher Flats is roughly triangular in shape and is confined in a relatively flat basin surrounded by steep, arid hills to the north and Lake Entiat to the south. Highway 97 runs though this site parallel to Lake Entiat. The majority of the site is north of Highway 97 and consists primarily of meadow-like habitat dominated by weedy species. The prevalence of weedy species and the presence of drainage ditches suggest that the hydrology of this area has been altered although mesic conditions still prevail. Roughly in the center of this large meadow area is a dense shrub thicket. In the easternmost corner of the meadow area is a stand of large black cottonwood and Siberian elm, which has structural characteristics similar to riparian deciduous habitats. This stand had some of the largest trees and the most abundant leaf litter of the habitats sampled. Also present in this area are prominent boulders and riprap which are preferred by bushy-tailed woodrats. The cottonwood stand

Draft Study Report Rocky Reach Project No. 2145 November 9, 2000 Page 4-29 SS/2493 RTE Wildlife & Cover-type Mapping has evidence of recent trash dumping, vehicular traffic, and non-designated camping. The portion of the Gallagher Flats site south of Highway 97 consists primarily of shrub-steppe habitats with a small pocket of riparian vegetation along Lake Entiat. The shrub-steppe habitat had gently rolling hills with small areas of sand dune. The riparian area consisted predominately of riparian shrub habitat with some emergent vegetation and scattered black cottonwoods. The emergent area is periodically flooded by Lake Entiat and consists primarily of reed canarygrass with a fringe of Western poison ivy. Despite the disturbances noted, all of these habitats provide suitable cover and foraging habitats for small mammals and small mammals were captured in all of these habitats. On either side of Highway 97, the habitats present are also connected allowing small mammals to move freely among them.

Uplake Shrub-steppe Three species of small mammals were captured at the Uplake Shrub-steppe site (Table 4-9). The Uplake Shrub-steppe site had the second lowest overall capture rate (3.2). Great Basin pocket mouse was the most abundant species captured, comprising 62.5 percent of all captures. Pitfalls had the highest capture rate at this site (10.0), and the capture rate for both snap traps and Sherman live traps was 1.6 (Table 4-10). Omnivores comprised 96.9 percent of the total captures, with insectivores comprising the remaining 3.1 percent (Table 4-11).

The Uplake Shrub-steppe site consisted primarily of shrub-steppe vegetation of varying densities and species composition. There were abundant grassy openings interspersed with the shrub dominated areas. The Uplake Shrub-steppe site had a moderate percent forb cover and the highest percent grass cover of any site sampled (Table 4-12). This site is part of a much larger tract of shrub-steppe habitat and provides abundant habitat for shrub-steppe small mammal species. The Uplake Shrub- steppe site is the most remote site surveyed and as a result had limited evidence of human disturbance. There are several fence rows and evidence of grazing, but no livestock were observed in the area during this study. Despite the large size of the site and relatively undisturbed condition, no sagebrush voles (Lagurus curtatus) or Merriam’s shrews (Sorex merriami) were captured on this site.

4.2.3 Bat Surveys Anabat surveys were conducted at all seven Intensive Study Sites and five Roving Study Sites. Six of these sites had sufficient bat activity to justify trapping. Nine individuals of four bat species were captured at these sites (Table 4-13). The fifteen bat species which potentially occur within the study area are given in Appendix C (Table C-2).

Most bat activity occurred near the confluence of tributaries to Lake Entiat, within protected coves or other backwater areas, and along natural flight corridors. Bats detected during this study appear to be concentrating their foraging activities near calm, protected areas where insects would typically concentrate. Fewer bats were detected foraging within the canopy of forested habitats or high along cliff faces. Because of the limited number of detections and the logistical constraints of trapping in forest canopies and along high cliffs, trapping was not conducted in these areas. Bat trapping efforts were focused on areas of concentrated foraging activity to increase the probability of capture. Bat trapping was conducted in late August. Bats that abandon their summer roosts in August and September (Tuttle 1994) may have already left the study area.

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Anabat recordings were analyzed to provide additional species occurrence data. The known species, which most closely resembles the unknown Anabat recordings, are provided for each site (Table 4-14). However, these results should be interpreted cautiously because trial cluster analysis of known species recordings from tape libraries did not correctly group the known species in some instances. This was a consequence of considerable variation in the attributes of the known species recordings.

Roosting concentrations of all myotis species, big brown bat (Eptesicus fuscus), and Townsend’s big-eared bat have Priority Species status with WDFW. Yuma myotis and Townsend’s big-eared bat are also State Candidate species for possible future listing. No State or Federally listed endangered, threatened or sensitive bat species were documented within the study area. A discussion of each potentially occurring RTE wildlife species and documented RTE wildlife species is provided in Section 4.2.5.

Turtle Rock Visual surveys, Anabat surveys, and mist netting were conducted along the upper northwest rock faces on Turtle Rock during the evening of August 28. Anabat recordings and trapping efforts were concentrated on the edge of an observed flyway running east to west and bordered by rock faces to the north and south. Bats were using this corridor to access over-water foraging areas. Because this corridor concentrated bat activity, one 18-m mist net was placed in this location. One pallid bat (Antrozous pallidus) was captured (0.85 captures per net-hour) (Table 4-13). Bats were also observed flying toward the mist net and then changing course to avoid the net

The exposed rocks and cliffs on the upstream portion of Turtle Rock provide abundant crevices for roosting bats. In addition, the relatively protected channel separating Turtle Rock from the mainland provides suitable foraging habitat. The downstream portion of Turtle Rock is primarily shrub-steppe with some fringing riparian habitats. These riparian habitats are generally small with few if any trees or snags. Potential roosting habitat is limited in this part of the island, although the Chelan PUD does have several maintenance buildings in this area that may serve as potential roosting areas.

Entiat River Visual and Anabat surveys were conducted along the confluence of the Entiat River on one night in late May. Bats were observed throughout the area and many Anabat detections were made over a calm backwater area and the adjacent riparian habitat west of Alternate Highway 97. Anabat recordings were made of individuals traveling throughout the confluence and under both the highway and railroad bridges. Due to the large numbers of individuals observed traveling under the two bridges, bat trapping was conducted on the evening of August 17 in this area. One 9-m mist net was placed parallel to and just below the railroad tunnel from the bridge abutment to the edge of the water. One little brown myotis (M. lucifugus) was captured at this location (0.50 captures per net- hour) (Table 4-13). Bats were also observed flying toward the mist net and then changing course to avoid the net.

A variety of potential roosting and foraging habitats are present near the Entiat River. The Swakane Wildlife Area borders the river to the south. There are several large cliff faces in this area, which

Draft Study Report Rocky Reach Project No. 2145 November 9, 2000 Page 4-31 SS/2493 RTE Wildlife & Cover-type Mapping appears to contain crevices suitable for roosting. This cliff area also has several rock benches with mature coniferous trees that may be used as roosting habitat. There is a relatively large residential development to the north of the Entiat River. Attics, barns, and sheds in this area may serve as roosting habitat for bats, and the streetlights in this area may attract insects. Diverse riparian vegetation along the river may also provide foraging habitat. The highway and railroad bridges could provide roosting habitat, but the disturbance associated with these structures may interfere with the normal activities of roosting and foraging bats.

Daroga Park Visual and Anabat surveys were conducted throughout Daroga Park on one night in June. Surveys were conducted in the downstream walk-in camping area, around the large pond, and along the river’s edge to the upstream end of the park. Few bats were observed around the pond or along the riparian zone; therefore, trapping was not attempted in this area.

Daroga Park contains a large pond that is separated from Lake Entiat by a narrow berm. Lombardy poplar are abundant along this berm and throughout much of the park. The pond is potential foraging habitat and the few bats observed were seen flying over this area. The abundant large trees in the park may provide some roosting habitat but few bats were observed. Several man-made structures in the park may also provide some roosting habitat, although no bats were seen using these areas.

Sun Cove Riparian Visual and Anabat surveys were conducted throughout the Sun Cove Riparian site on one night in June. Surveys were conducted within the riparian zone, around a small pond, and along a sheltered cove upstream of a small peninsula. Bats were observed and recorded along most of the riparian corridor with the highest foraging concentrations around the upstream cove. Several large black cottonwoods were also the focus of bat activity in this area with the observed bats alternately foraging around the cove and then higher up in the trees. One 18-m net was placed along the sandy shore of this cove. The net partially blocked a small flyway connecting a portion of the deciduous riparian zone to the cove. One Yuma myotis was caught at this site (0.62 captures per net-hour) (Table 4-13). Bats were also observed flying toward the mist net and then changing course to avoid the net.

The abundant bat activity observed within the Sun Cove Riparian site suggests that this area provides suitable roosting and foraging habitats. There are abundant large black cottonwoods, Lombardy poplars, and several outbuildings in the area that may provide roosting habitat. There are also prominent cliff faces located on the opposite side of Lake Entiat that may provide abundant roosting habitat. The small sheltered coves located on each side of the small peninsula appear to provide suitable foraging habitat as most of the observed activity was in these locations. The Sun Cove Riparian site is privately owned and is less disturbed than some of the other sites surveyed.

Sun Cove Shrub-steppe Visual and Anabat surveys were conducted at the Sun Cove Shrub-steppe site on one night in June. Surveys were conducted along the thin riparian fringe along Lake Entiat and in the adjacent shrub- steppe habitats. Several bats were seen flying over and foraging around the boat launch associated

Rocky Reach Project No. 2145 Draft Study Report SS/2493 Page 4-32 November 9, 2000 RTE Wildlife & Cover-type Mapping with the Sun Cove residential development. A few bats were also observed foraging over the small pond downstream of the boat launch area. Anabat recordings were concentrated around these areas, but trapping was not conducted due to the sparse and diffuse nature of the bat activity. Winds were relatively strong on the night of the survey, which may partially account for the limited number of bats observed.

The Sun Cove Shrub-steppe site contains some potential roosting and foraging habitat. There are some large deciduous trees associated with the Sun Cove residential development and also within the narrow wetland that bisects the site. Relatively protected foraging habitat occurs near the boat launch and the small downstream pond.

Goosetail Rock Visual and anabat surveys were conducted around Goosetail Rock on one night in June. Surveys were conducted within the riparian habitats and in adjacent upland habitats. Bats were observed foraging over the small sheltered coves on the western side of Goosetail Rock. Bats were also detected flying high above the riparian habitats and associated coves. Trapping was not conducted at Goosetail Rock due to the rugged terrain, the height of the observed bats, and the diffuse nature of the bat activity.

Goosetail Rock has steep cliffs with abundant crevices that could serve as roost sites. The riparian habitats adjacent to Goosetail Rock have large trees with a well-developed canopy that may provide addition roosting habitat. The sheltered coves associated with Goosetail Rock appear to provide suitable foraging and drinking areas, as many of the observed bats were flying over these areas. Furthermore, abrupt topographical features, such as the cliffs on Goosetail Rock, can cause upwelling of insects by air currents resulting in concentrations of potential prey for foraging bats.

Chelan Butte WMA Visual surveys, Anabat surveys, and mist netting were conducted at the downstream end of the railroad tunnel in the Chelan Butte WMA on August 29. Anabat and trapping efforts concentrated on the entrance to the tunnel, which was used as a flyway linking roosting and feeding areas. Bat activity was concentrated in this area facilitating visual and Anabat observations. One 6-m mist net was placed as close to the tunnel entrance as possible resulting in the capture of one Pallid bat (0.50 captures per-net hour) (Table 4-13). Bats were also observed flying toward the mist net and then changing course to avoid the net.

The railroad tunnel in the Chelan Butte WMA is located on the side of a complex cliff system with very sparse vegetation. Although no bats were observed actively roosting in the tunnel many were seen flying through or around the inside of the tunnel and foraging on insects near the entrance. The large and extensive cliffs associated with the Chelan Butte WMA may provide abundant roosting habitat. Lake Entiat is immediately adjacent to the tunnel and the cliffs and may provide suitable foraging habitat.

Chelan Falls Park Visual and Anabat surveys were conducted throughout Chelan Falls Park on one night in mid June. Surveys were conducted along the southern bank of the Chelan River, under both the roadway and

Draft Study Report Rocky Reach Project No. 2145 November 9, 2000 Page 4-33 SS/2493 RTE Wildlife & Cover-type Mapping railroad bridges and in adjacent habitats. Bats were observed traveling throughout the confluence using the area under the two bridges as a flyway. Trapping efforts were concentrated below the roadway-bridge on the northern side of the Chelan River on August 24. One 18-m mist net was placed in this location under the bridge and across a large cobble bar. An additional 9-m mist net was set out parallel to the riparian corridor. Although no bats were captured in the mist nets, four roosting western small-footed myotis were captured by hand under the roadway-bridge. Bats were observed flying toward the mist nets and then changing course to avoid the nets.

The Chelan Falls area has diverse habitats that may be used by bats. Within the Chelan River Gorge and adjacent hillsides, extensive cliff faces with crevices are present. Near the confluence riparian habitats occur, consisting of scattered large trees and patches of dense shrubs. The two bridges also provide suitable roosting habitat for bats. There are several small coves and still water areas near Chelan Falls Park that may provide foraging habitat.

Beebe Bridge Riparian Visual and Anabat surveys were conducted at the Beebe Bridge Riparian site on one night in late May. Surveys were conducted along the inland edge of riparian habitats and over the adjacent grassy areas to the west. Surveys were not conducted along the shoreline due to the dense Himalayan blackberry thickets in this area. Few bats were seen flying over or foraging in riparian habitats. Although some Anabat recordings were made, no concentrated use areas were found within the Beebe Bridge Riparian site, so bat trapping was not attempted.

Although few bats were observed, the Beebe Bridge Riparian site may provide some roosting and foraging habitat for bats. This site has many large Siberian elm trees and two relatively protected coves. Nearby cliffs and human developments may also provide suitable roosting habitats.

Gallagher Flats Visual and Anabat surveys were conducted at Gallagher Flats on one night in early June. Surveys were conducted within riparian habitats, the large cottonwood stand, the shrub-steppe areas, and in adjacent habitats. Only three bats were seen throughout the shrub-steppe areas and none were observed along the riparian zone, therefore, trapping was not attempted in this area. Winds were strong on the night of the survey, approximately 15-20 mph with gusts to 25 mph, and may have contributed to the low number of observations.

The large cottonwood stand and the riparian habitats along Lake Entiat may provide suitable roosting and foraging habitats for bats. The cottonwood stand within Gallagher Flats has some of the largest trees documented within the study area. The riparian habitats also have some large black cottonwoods as well as a large emergent area that is periodically flooded and may provide foraging habitat.

Uplake Shrub-steppe Visual surveys, Anabat surveys and mist netting were conducted at the Uplake Shrub-steppe site on August 30. Surveys were concentrated on the shoreline at the edge of a small alluvial fan. Many bats were observed foraging over Lake Entiat. One 18-m mist nest and one 6-m mist net were set up perpendicular to each other near this location. One western small-footed myotis was captured in

Rocky Reach Project No. 2145 Draft Study Report SS/2493 Page 4-34 November 9, 2000 RTE Wildlife & Cover-type Mapping the 18-m net (0.24 captures per net-hour) (Table 4-13). Bats were also observed flying toward the mist net and then changing course to avoid the net.

Although, shrub-steppe is the dominant vegetation in this area, there are several patches of large ponderosa pine up Long Draw to the east of the Uplake Shrub-steppe site, which may provide suitable roosting habitat. Upstream and downstream from this site there are also small cliff faces with fractures and crevices that may also provide roosting habitat. The abundant bats observed foraging over Lake Entiat suggests that suitable foraging habitat is available.

Azwell Riparian Visual and Anabat surveys were conducted within the Azwell Riparian site on one night in June. Surveys were concentrated along the shoreline of Lake Entiat and around a large seasonal pond. The shoreline in this area is relatively unprotected and few bats were observed in this area. More bats were observed flying and foraging over the large pond. Trapping was not attempted in this area due to the terrain and the diffuse nature of the bat activity.

The Azwell Riparian site has limited potential roosting habitat. There are some large black cottonwoods on this site, but adjacent outbuildings and sheds associated with an orchard are more likely roosting habitats. The seasonal pond provides suitable foraging habitat, although only a few bats were observed foraging over the pond.

4.2.4 Amphibian and Reptile Surveys

Amphibian Results Four species of amphibians were documented during this study: western toad, Great Basin spadefoot toad (Scaphiopus [Spea] intermontanus), Pacific chorus frog (Pseudacris [Hyla] regilla), and long- toed salamander (Ambystoma macrodactylum). The study area is also within the expected distribution (Dvornich et al. 1997) of three other species: tiger salamander (A. tigrinum) (no reported records), Columbia spotted frog (Rana luteiventris) (reported record at Entiat, McAllister 1995), and bullfrog (Rana catesbeiana) (no reported records) (Appendix C Table C-3). Amphibian survey results are summarized in Table 4-15 through Table 4-20

Pacific chorus frog was documented at a total of ten sites in the study area and is almost certainly the most widely distributed amphibian in this area; however, it is unclear whether each of these sites, particularly the five sites where frogs were heard on September 6, 1999, represents a breeding population. Pacific chorus frog, is well known to call sporadically outside of the breeding season and from sites where they do not breed (Leonard et al. 1993). Western toad was found at a total of five sites, including four of the Intensive Sites (Turtle Rock [TR], Entiat River [ER], Sun Cove Riparian [SCR], and Sun Cove Shrub-Steppe [SCS]); larvae were documented at one of these sites (SCR). Great Basin spadefoot toad was found at three sites, two of which were Intensive Sites, SCS and GF, and at AS 7 (Azwell); larvae were found at GF and AS 7. Long-toed salamander was found at a single site, AS 10.

All of the documented species are well adapted for survival in arid regions and may venture far from water. Movement away from the breeding site to other areas with water also complicates the

Draft Study Report Rocky Reach Project No. 2145 November 9, 2000 Page 4-35 SS/2493 RTE Wildlife & Cover-type Mapping interpretation of our results. For these and other reasons we believe that suitable breeding sites for amphibians are relatively scarce in the Rocky Reach study area.

The key factor in the distribution of amphibians is the absence of fish at potential breeding sites. Sites that dry seasonally (or freeze to the bottom) are favored by many species for this reason. Fish are present at all of the sub-impoundments, ponds, and emergent wetlands in the Rocky Reach study area except AS 5, 10, 16, 19, 20, and 22. At two other sites (AS 6 and 7) the only fish apparently present were large carp that could not have survived when the pools later dried. Amphibian larvae were found at four of these eight sites (AS 5, 7, 10, and 19) and there was other evidence that amphibians might breed at two others (AS 6 and 20).

Two highly aquatic frogs, Columbia spotted frog and bullfrog, were not documented in this study. Apparently suitable habitats for Columbia spotted frog, particularly shallow marshy sites without fish, are scarce; however, the same is not true for bullfrog. Most of the sub-impoundments and permanent ponds bordering the reservoir appear suitable for bullfrog. The presence of fish is not inimical to the reproductive success of bullfrog (Werner and McPeek 1994), a species that thrives at permanently flooded, warm water sites with emergent vegetation and aquatic weeds for hiding cover. The spread of this non-native species is not easily controlled, even in arid areas, because bullfrogs readily exploit irrigation canals, ditches, stock tanks, and excavated ponds. Bullfrogs are still commercially distributed for use in ornamental ponds and for commercial propagation.

It is uncertain to what extent amphibians may breed within the shallow margins of Lake Entiat. However, several species of native amphibians, including Great Basin spadefoot toad and western toad, are known to breed in floodwater pools associated with streams and large rivers, and delayed breeding timed to flood stage decline has been documented for both of these species (Metter 1960). Bullfrogs will also breed in reservoirs, but because larvae of this species typically require a second growing season before achieving metamorphosis, they may enjoy diminished success unless there are areas protected from seasonally strong currents.

Western toad and Columbia spotted frog are considered Priority Species by WDFW, which monitors their occurrence. Some populations of western toad in Washington, particularly in southern Puget Sound and in the North Cascades, have inexplicably declined or disappeared. This remains a common species in many other areas. Columbia spotted frog is found only peripherally in the most arid parts of the Columbia Basin, and within the study area may occur only in the vicinity of the Entiat River. There is no compelling evidence that populations of Columbia spotted frog are in decline in Washington.

Reptile Results Reptile survey results are summarized in Table 4-15, Table 4-18, and Appendix C (Table C-4). Eight species of reptiles were documented in the Rocky Reach study area: painted turtle, western fence lizard (Sceloporus occidentalis), sagebrush lizard (S. graciosus), racer (Coluber constrictor), gopher snake (Pituophis catenifer), common garter snake (Thamnophis sirtalis), wandering garter snake (T. elegans vagrans), and western rattlesnake (Crotalus viridis). An additional six species are known or potentially occur in this area: short-horned lizard (Phrynosoma douglassii), side-blotched lizard (Uta stansburiana), western skink (Eumeces skiltonianus), rubber boa (Charina bottae), night

Rocky Reach Project No. 2145 Draft Study Report SS/2493 Page 4-36 November 9, 2000 RTE Wildlife & Cover-type Mapping snake (Hypsiglena torquata), and sharptail snake (Contia tenuis). The reptiles of the study area include a number of widespread, generalist species (e.g., racer), but at least five species are more-or- less restricted to desert and shrub-steppe habitats (Nussbaum et al. 1983, Stebbins 1985) (sagebrush lizard, short-horned lizard, side-blotched lizard, night snake, and western rattlesnake). Sagebrush lizard, sharptail snake, and night snake are considered Priority Species by WDFW (see discussion in Section 4.2.5).

Based on the number of sites with a detection, the most widespread species were racer (at five sites), sagebrush lizard, western fence lizard, gopher snake, and painted turtle (each at three sites), and common garter snake (two sites). Wandering garter snake and western rattlesnake were each found at only one site. There are, however, some reasons to believe that detection rates can be deceptive for some of these species. For example, western fence lizard is relatively conspicuous, diurnally active, and thus easily documented. In contrast, the smaller sagebrush lizard is more wary and likely to retreat to shelter. Sagebrush lizards were observed incidentally at three sites, in each case only a single individual, but were not recorded during intensive, area-constrained searches. This species may be more widespread than suggested by our results. Both species of garter snake are closely associated with riparian habitats and probably occur throughout the reservoir edge and around the adjacent ponds and wetlands.

Western rattlesnake is almost certainly more widely distributed; rattlesnakes have been observed in the past at Turtle Rock (Kate Beck, personal communication) and at the Earthquake Point islands (Paul Fielder, personal communication). Nonetheless, this species has probably been reduced or extirpated in areas of fragmented shrub-steppe in proximity to human activity centers, particularly where communal den sites are vulnerable. Rattlesnakes also fare poorly in proximity to busy roadways.

Turtle Rock One amphibian and two reptile species were documented at Turtle Rock (Table 4-15). During the area-constrained intensive search, a racer was observed in rocky shrub-steppe habitat and two western toads were found among cattail and sedges at the river edge. Five western toads were captured in pitfall traps in the riparian zone. There was also an incidental observation of a racer and a sagebrush lizard.

The presence of western toad at this mostly arid site is probably attributable to the Turtle Rock fish rearing and holding pond which may be a breeding site. A shallow channel formerly connected to the pond might also be suitable. Western toad is known to sometimes breed in river backwaters and might use the adjacent emergent habitat along the shore of the island.

Much of the shrub-steppe and grassland habitat on the island burned in 1999. As such, hiding cover for small animals is in places limited to excavated burrows, and areas with rock crevices, boulders, or talus. Riparian habitat consists of a narrow, broken band of shrubs, and scattered patches of emergent vegetation along the downstream end of the island. In addition to western rattlesnake, other reptiles associated with shrub-steppe habitats may occur on Turtle Rock. However, because Turtle Rock is an island, albeit a relatively large island, populations of reptiles may be smaller and

Draft Study Report Rocky Reach Project No. 2145 November 9, 2000 Page 4-37 SS/2493 RTE Wildlife & Cover-type Mapping more prone to local extinction than mainland populations. Habitats on Turtle Rock are generally unsuitable for amphibians.

Entiat River Four reptile species and one amphibian were documented at Entiat River (Table 4-15). During the area-constrained surveys, a total of six fence lizards were found, three conclusively identified as western fence lizard, and three that could not be captured for identification. All were in areas with large boulders, including a boulder field. During the same search, two racers were also found in brushy areas. Two Pacific chorus frogs were captured in pitfalls. Species documented by incidental observation were wandering garter snake and common garter snake. Mapped records (McAllister 1995) for Columbia spotted frog and western toad are either from the town of Entiat or Entiat River.

This site is predominately riparian but also includes drier edge habitat and openings. Habitats at Entiat River are most favorable for reptiles associated with riparian areas, and amphibians that sometimes breed in backwaters and flood channel pools. The presence of western fence lizard at this site is not surprising. Western fence lizard is often found in flood scoured, boulder-strewn riparian areas, as well as shorelines more generally (e.g., on lakes or bays) provided there is ample cover in the form of boulders, large woody debris, or strand-line debris. Garter snakes of both species are also closely associated with riparian areas, largely because of available prey (especially fish, amphibians, and aquatic insects). Side channels, flood water pools, and shallow, emergent backwaters along the Entiat River could provide breeding habitat for Pacific chorus frog, and possibly other species (e.g., western toad or Columbia spotted frog), although we did not observe highly suitable areas during this study. Riparian habitats along the Entiat River may constitute a dispersal corridor for reptiles and amphibians, connecting the study area with forested habitats far to the west.

Sun Cove Riparian One species of amphibian and one reptile were documented at the Sun Cove Riparian site (Table 4-15). During the area-constrained intensive search, six western toads were found; two toads were also caught in snap-traps. No amphibians or reptiles were captured in pitfall traps. Painted turtle was documented by incidental observation of an adult in the pond and by hatched eggs in dry, sandy soil north of the pond. No snakes or lizards were observed at this site. The absence of Pacific chorus frog at an apparently suitable breeding site is curious and not easily explained.

This is a sandy site with scrubby vegetation, a relatively large amount of woody debris, and a pond with good hiding cover and no fish. This favorable combination of features may be offset by the relative isolation of the site due to the adjacent orchards. Shrub-steppe adapted species in particular are unlikely to occur at this site because of this isolation.

Sun Cove Shrub-steppe Three species of reptile and two species of amphibian were documented at the Sun Cove Shrub- Steppe site. During the area-constrained intensive search, conducted on two dates, two racers and one gopher snake were found. Five Great Basin spadefoot toads were caught in pitfalls, and a western toad was caught in a snap-trap. Incidental observations included a western toad and a sagebrush lizard.

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Habitats within this site are generally suitable for reptiles, but more limited for amphibians. Native shrub-steppe vegetation is relatively intact and undisturbed. This site is part of one of the largest remaining blocks of shrub-steppe in the study area south of Beebe Bridge. Nonetheless, this block is surrounded by orchards and residential developments and may be too small to support viable populations of most species dependent on shrub-steppe habitats.

The pools at this site are shallow and probably quick to dry. Although these pools may suffice for Great Basin spadefoot toad, it is unlikely that other species could breed here successfully. Western toads at the Sun Cove Shrub-steppe site may have dispersed from the Sun Cove Riparian site.

Beebe Bridge Five reptile species were documented at Beebe Bridge (Table 4-15). No amphibians were detected at this site. During the area-constrained intensive search, six western fence lizards were found, four associated with piles of woody debris, and two associated with small rock piles. A racer and a gopher snake were also found. No amphibians or reptiles were captured in pitfall traps. Species documented by incidental observations included sagebrush lizard and an unidentified garter snake, each based on a single sighting.

Habitats at Beebe Bridge are generally suitable for reptiles that are habitat generalists or closely associated with riparian habitats. The pond is suitable for painted turtle. Interestingly, this was the only site where both species of fence lizard were documented. Habitat suitability for amphibians is uncertain, but may be limited by the likely presence of fish in the pond and poorly developed emergent habitats. However, this pond may be suitable for bullfrog.

Gallagher Flats Three reptile species and one amphibian were documented at Gallagher Flats (Table 4-15). During the area-constrained intensive search, nine western fence lizards were found, seven in a boulder field, and two in the cottonwood-black locust stand (one on a fallen log and one on the ground). Six Great Basin spadefoot toads were captured in pitfall traps, and one western fence lizard was caught in a snap-trap. Species documented by incidental observation were western rattlesnake and racer, both on the basis of single individuals observed in shrub-steppe. A large number of Great Basin spadefoot toad larvae were concentrated in two very small, shallow pools.

This is an unusual site largely comprised of a disturbed, forb-dominated field, small patches of macrophyllous shrubs, and a grove of large trees, surrounded by shrub-steppe habitats. The adjacent railroad embankment constitutes good hiding cover for lizards among the small boulders. The site also encompassed riparian habitats along the river shore. Based on a USGS topographic map (dated 1981) and the presence of drainage ditches, we believe that the field probably was seasonally flooded prior to construction of the new Highway 97 between the site and Lake Entiat. Currently, areas of seasonal standing water at this site are limited to a few small pools in a deeply rutted road, surrounded by seasonally saturated stands of reed canarygrass. These pools provide the only apparent breeding habitat for amphibians, but suitable only for Great Basin spadefoot toad. Spadefoot toads successfully exploit small pools with limited duration because larvae develop rapidly and are assured a food supply by cannibalism under crowded conditions. Boulder fields and

Draft Study Report Rocky Reach Project No. 2145 November 9, 2000 Page 4-39 SS/2493 RTE Wildlife & Cover-type Mapping shrub-steppe habitats on the edge of the site are generally suitable for reptiles. A stand of cottonwoods within the site occupies a small area, but the trees are large and there is ample large woody debris within the stand that could be used as cover by reptiles and amphibians.

Uplake Shrub-steppe No amphibians or reptiles were found at the Uplake Shrub-steppe site. A rocky area on the fringe of the site was intensively searched without success. Except for this area, hiding cover at the site is largely limited to small piles of accumulated leaf litter at the base of sagebrush and other microphyllous shrubs. Reptiles that burrow in loose sand or that exploit existing small mammal burrows might occur; however, this site contains no potential breeding habitat for amphibians.

Results of Roving Sites The results of area-constrained intensive searches at the Roving Sites are presented in Table 4-18. Because less time was devoted to these sites, opportunities to document species by incidental observation were more limited. The only findings were a painted turtle at Daroga State Park observed basking on a log in the pond, a gopher snake at Daroga State Park (incidental observation on one of the park roads), a common garter snake in a boulder areas adjacent to Chelan River at Chelan Falls Park, and a western toad at one of the Earthquake Point islands. The small cluster of islands at Earthquake Point have previous sightings of western rattlesnake and unidentified lizards (probably western fence lizard) (P. Fielder, personal communication).

4.2.5 RTE Wildlife Species Federally and Washington State listed wildlife species that are known to or potentially occur within the study area are given in Table 4-21. Potential occurrence for each species was determined from confirmed records and known distribution and habitat requirements. The Washington Gap Analysis Project and Chelan PUD records were the primary sources used to develop this list.

Ten listed species were documented during the RTE Wildlife Study in the Rocky Reach Study Area. These included common loon (State Candidate), great blue heron (State Monitor), bald eagle (Federal and State Threatened), golden eagle (State Candidate), loggerhead shrike (State Candidate and Federal Species of Concern), little brown myotis (State Monitor and Federal Species of Concern), small-footed myotis (State Monitor and Federal Species of Concern), Yuma myotis (State Monitor and Federal Species of Concern), sagebrush lizard (Federal Species of Concern), and western toad (State Candidate and Federal Species of Concern). We have provided individual accounts for each the species on the RTE list, except for a general account for colonial roosting bat species.

Common Loon The common loon is a Washington State Candidate species for which WDFW maintains records of breeding areas and regular concentrations. This species is vulnerable to shoreline development, water level fluctuations during nesting, and human disturbance near nest sites.

The study area is outside the core breeding habitat zone for common loon (Smith et al. 1997) and there is no evidence that the species breeds in or near the study area. Common loons breed on large

Rocky Reach Project No. 2145 Draft Study Report SS/2493 Page 4-40 November 9, 2000 RTE Wildlife & Cover-type Mapping lakes with undisturbed shorelines within forested landscapes. Nests may be located on hummocks, stumps, beaver lodges, artificial platforms, or within scrapes along the shore. Some evidence suggests that loons prefer to nest on islands (WDFW 2000b). Loons are very sensitive to human disturbance during nesting. Decreased reproductive success in loons has been associated with shoreline development (Vermeer 1973) and recreational boat traffic (Titus and Vandruff 1981). Common loons feed primarily on fish and may be absent from otherwise suitable habitats that have insufficient forage-fish populations.

Common loons were observed regularly during the wintering waterfowl surveys throughout Lake Entiat. In addition, one adult was observed on several occasions near Turtle Rock in May 2000 during breeding bird surveys. This individual was most likely a transient.

Great Blue Heron Great blue herons are colonial nesting long-legged wading birds. This species is a WDFW Monitor species, primarily because nesting colonies, or “rookeries,” are sensitive to disturbance; and because the availability of suitable breeding habitat is declining due to human developments and land-use practices. Great blue herons are common in marshes and mudflats throughout Washington, but are very sensitive to human disturbances during nesting (Smith et al. 1997).

The study area is within the core breeding habitat zone for the great blue heron (Smith et al. 1997). There are possible breeding records for this species within the study area. Great blue herons are colonial nesters in low elevation marshes, swamps, and along water bodies. Nests are typically located in trees, but may be located in shrubs if trees are not present. Fish are the primary prey items, although small mammals, birds, amphibians, and aquatic invertebrates are also consumed. This species is sensitive to human disturbance during nesting; reproductive success may be reduced or entire colonies may be abandoned due to disturbance. The availability of nesting habitat adjacent to suitable foraging areas may also limit the range of this species.

Suitable nesting and foraging habitat occurs within the study area and great blue herons were regularly seen along Lake Entiat. Areas with multiple observations include aquatic beds and emergent vegetation near the Entiat River and the Sun Cove Riparian site.

Osprey The osprey is a WDFW Monitor species primarily because nesting individuals are sensitive to disturbance. This species is a common breeder along large water bodies in low elevation forested landscapes within Washington, but is a rare breeder in steppe zones along large rivers (Smith et al. 1997).

Lake Entiat and several of the larger tributaries are within the core breeding zone, and there are two confirmed breeding records in the study area (Smith et al. 1997). Osprey build large perennial nests on dead or live trees, transmission line poles, or other artificial structures, always near water. This species feeds primarily on fish, but will also prey on rodents, birds, and other small vertebrates.

Suitable nesting locations are relatively abundant along the shore of Lake Entiat and there are abundant forage fish available. Two active osprey nests were document during this study. One active

Draft Study Report Rocky Reach Project No. 2145 November 9, 2000 Page 4-41 SS/2493 RTE Wildlife & Cover-type Mapping nest was observed to the south of the Entiat River in a large conifer in the Swakane Wildlife Area. The second active nest was documented on a utility pole near the confluence of the Chelan River during this study. This nest was near the Chelan Falls Park and the Lake Chelan Hydroelectric Project Powerhouse. Individual osprey were also observed near Turtle Rock and Goosetail Rock during breeding bird surveys.

Bald Eagle The bald eagle is listed as Threatened by USFWS in Washington, but has experienced dramatic increases in numbers throughout the state since DDT use was stopped, and recovery management plans were instituted (USFWS 1986). Bald eagle may be de-listed at the Federal level in 2000.

The study area is outside the core breeding habitat zone for bald eagle (Smith et al. 1997). One nesting pair has been documented near the study area south of McKinstry Creek (Chelan PUD 1999). This nest was established in 1996 and has been active since. Bald eagles are infrequent breeders along major rivers and large lakes in eastern Washington. Wetland and shoreline habitats are preferred, but this species will use most habitats along large water bodies, although moderate to high-density human developments are avoided. Bald eagles regularly overwinter along large ice-free rivers including the Columbia River in the study area. Large roost trees are important habitat features for wintering bald eagles.

Several adult bald eagles were observed near Turtle Rock during summer 2000, but no evidence of nesting was documented during this study. The Chelan PUD estimates that between 20 and 60 bald eagles overwinter on Lake Entiat feeding on the abundant overwintering waterfowl (Fielder 1982). Bald eagles were regularly seen during the winter 1999/2000 waterfowl surveys. Concentrations of bald eagles were observed near the mouth of the Entiat River.

Northern Goshawk The northern goshawk (Accipiter gentilis) is a Washington State Candidate species and a Federal Species of Special Concern. This species is found in mature conifer forests throughout Washington. Harvesting of old growth and mature conifer forests is the primary threat to northern goshawks.

The study area is not in the core or peripheral breeding zones of the northern goshawk. In eastern Washington this species is found in mature conifer forests above the ponderosa pine zone. Thus, there is no breeding habitat within the study area and no nesting records for the area. Northern goshawks are an uncommon winter resident along Lake Entiat (Chelan PUD 1999).

Swainson’s Hawk The Swainson’s hawk (Buteo swainsoni) is listed as a Monitor species in Washington. This species is closely associated with shrub-steppe and prairie habitats. The widespread conversion of these habitats to agriculture in Washington has caused concern, although this species is evidently at least somewhat adaptable to use of agricultural lands.

The study area is within the core breeding habitat zone for Swainson’s hawks (Smith et al. 1997). There are confirmed and possible breeding records within the Project vicinity. Swainson’s hawk breeds in shrub-steppe, prairie, open woodlands, and agricultural areas with scattered trees. Nests

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Although no Swainson’s hawks were observed during this study, they could potentially breed in the study area since there are abundant shrub-steppe and agricultural lands for foraging and nesting.

Golden Eagle The golden eagle is a Washington State Candidate species for which WDFW maintains records of breeding sites. Historically golden eagles were killed in large numbers by ranchers; however, current populations are relatively stable.

The study area is within of the core breeding habitat zone for golden eagles (Smith et al. 1997). Golden eagles are most commonly associated with open country, such as shrub-steppe, grasslands, open ponderosa pine forest, and large clearcuts (Rodrick and Milner 1991). They nest on cliff ledges and large trees. Mid-sized mammals, particularly rabbits, ground squirrels, and marmots, are the principal prey. Breeding pairs require large territories, with estimated territory size ranging from 42 to 52 square kilometers per breeding pair in Utah (Johnsgard 1990).

One adult golden eagle was observed at Gallagher Flats during this study. Although no evidence of nesting was observed, cliffs and escarpments along the Columbia River would appear to provide potential nesting habitat and there is abundant suitable foraging areas within the study area.

Peregrine Falcon The peregrine falcon (Falco peregrinus anatum) was formerly listed as Federally Endangered; de- listing occurred in August 1999 based on successful recovery. The species remains on the Washington state list as an Endangered species. Once relatively secure, even in urban settings, peregrine falcon populations plummeted throughout the U.S. beginning in the 1950’s. These declines closely correspond to the introduction and widespread use of organochlorine pesticides such as DDT. The number of peregrine falcons has steadily increased after the use of DDT was discontinued and recovery plans were instituted. Recovery plans have included aggressive intervention with captive-breeding, and hatching impaired eggs under protected conditions. Hundreds of nestlings have been raised and placed in appropriate habitat where there are suitable natural or artificial nest sites. Natural recolonization has also occurred.

The study area is outside the core breeding habitat zone for peregrine falcons (Smith et al. 1997) and there is no evidence that they breed in or near the study area. Peregrine falcons nest on cliff ledges, or less commonly on large trees or snags. Nests are also found under high bridges, and on skyscrapers that simulate natural eyries. Non-breeding migrants use similar habitats. Principal prey are other birds, especially doves, pigeons, shorebirds, and waterfowl. Peregrines are known to migrate along the coast or elsewhere following migrating waterfowl and shorebirds.

Peregrine falcons may pass through the study area during migration, although there are no records and none were observed during this study. However, peregrine falcons have been observed at nearby Lake Chelan (Chelan PUD 1999).

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Prairie Falcon The prairie falcon (Falco mexicanus) is a state Monitor species. This species is sensitive to human habitation near nest sites; in addition, much of the preferred foraging habitat, grassland and shrub- steppe ecosystems, has been converted to agriculture. Because of this, prairie falcons in Washington are limited by the availability of suitable nesting sites that are adjacent to steppe and shrub-steppe habitats (Denton 1975).

The study area is within the core breeding habitat zone for prairie falcons (Smith et al. 1997). In addition, this species winters in the central Columbia Basin. Prairie falcons inhabit the arid grassland and shrub-steppe habitats of eastern Washington (Denton 1975). Nests have been found on cliffs and escarpments greatly varying in height (2 meters to 122 meters high), but most often with a southerly aspect. Typically, nest sites are sheltered ledges or potholes in a cliff. Prairie falcons will also use abandoned stick nests built by other raptors. Nests almost always have overhead protection (Runde and Anderson 1986). A study in Oregon reported that 76% of nests were within 0.25 miles of a water source, 32% bordered agricultural land, and 62% were within 0.5 mile of a road; however, only 15% were within 0.5 mile of human habitation (Denton 1975). Prairie falcons forage in shrub-steppe and grassland habitats. Primary prey includes small mammals, such as ground squirrels and microtine rodents, and birds, such as western meadowlark, horned lark, and rock dove, with the composition dependent upon local prey availability.

Although suitable habitat occurs in the study area, no prairie falcons were observed in the study area during this study. The large amount of human development in the study area may reduce the areas overall suitability for this species.

Burrowing Owl The burrowing owl (Speotyto cunicularia) is a Washington State Candidate species for which WDFW maintains records of breeding sites. This species is local and uncommon in shrub-steppe and grassland habitats in eastern Washington; populations are declining in most areas (Smith et al. 1997).

The core breeding habitat zone for burrowing owl lies within the Central Arid Steppe (Smith et al. 1997). The area around Wenatchee is within the core zone for this species, and confirmed and probable breeding evidence exists in this area. Burrowing owls require open shrub-steppe or grassland habitats with deep soils, and the presence of burrowing mammals, especially ground squirrels, upon which they largely rely for nest burrows. Nests are also sometimes located in other burrow-like depressions (e.g., in rock outcrops, drainage pipes, and artificial burrows) (Smith et al. 1997). This species often nests in loose colonies, probably an artifact of the colonial habits of most species of ground squirrels. Because they are dependent upon existing burrows, those factors responsible for the decline in ground squirrel populations have also adversely affected burrowing owls. Principal among these factors has been the loss and fragmentation of shrub-steppe and grassland habitats, although ground squirrel control measures are also significant. Agricultural areas are considered suitable for burrowing owls, provided the land is managed to conserve suitable nesting burrows and provide sufficient prey.

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Although suitable habitat occurs within the study area no burrowing owls were observed during this study.

Sage Grouse The sage grouse (Centrocercus urophasianus) is classified as a game species in Washington (harvest closed since 1988), but is also a Threatened species. This species requires large tracts of sagebrush habitat and has undergone a marked reduction in distribution historically, estimated at more than 90%. Formerly found throughout sagebrush habitats within the Columbia Basin, sage grouse are now uncommon, very local, and declining. Currently there are two principal sub-populations of this species remaining in Washington: about 600 birds in Douglas County, and 300-400 in Yakima County (Hayes et al. 1998).

Sage grouse require large tracts of sagebrush. Optimal habitat consists of medium to dense, structurally diverse sagebrush steppe habitats with areas of palatable grasses and forbs in a landscape of low rolling hills. Males occupy leks in spring and display to attract mates. The kinds of areas used as leks by sage grouse are diverse, suggesting that the availability of suitable lek areas is probably not a limiting factor. However, loss of traditional lek areas could be disruptive to populations. Sage grouse nests are concealed under sagebrush and lined with grass and other herbaceous material (Ehrlich et al. 1988). Principle forage includes the flowers and buds of forbs and sagebrush leaves in fall and winter. Livestock grazing adversely affects the quality of shrub- steppe habitats for sage grouse by reducing the amount of herbaceous forage and hiding cover. Similarly, areas subjected to brush control measures are not suitable for sage grouse. Some habitats that appear structurally suitable for sage grouse may not be, particularly if critical plant species are uncommon or absent. Most notably, areas with few native bunch grasses, but abundant cheatgrass (a relatively unpalatable food source) are not suitable for sage grouse.

Most of the shrub-steppe habitats in the study area are small and fragmented. There are large tracts of shrub-steppe habitats along the east side of Lake Entiat north of Beebe Bridge. This area is within the core breeding zone and not far from the population in central Douglas County (Smith et al. 1997). However, no sage grouse were observed within the study area during this study. Given the conspicuous nature of this species (when breeding) it seems unlikely that it would be overlooked. There was evidence of grazing in the large shrub-steppe habitats and cheat grass was often the most abundant herbaceous species. These factors may limit the suitability of these habitats for sage grouse. The study area is within the original range of this species and theoretically could be recolonized, provided that the vegetative structure and plant species composition of these areas are suitable.

Sharp-tailed Grouse Sharp-tailed grouse (Tympanuchus phasianellus) is a Washington State Threatened species and a Federal Species of Concern. This species is rare, very local, and declining in grass dominated habitats in the northern Columbia Basin (Smith et al. 1997). Sharp-tailed grouse were formerly widespread throughout eastern Washington in bunchgrass habitats. Conversion of native grasslands to agricultural lands and grazing is suspected to be the primary cause of this species decline.

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Core breeding habitat is restricted to northern Douglas County, the Okanogan valley, and central Lincoln County (Smith et al. 1997). The core zone in Douglas County is near the northernmost portion of the study area, but there are no breeding records in Chelan County.

Sharp-tailed grouse prefer native grasslands including grassy openings in shrublands. Males occupy leks in spring and display to attract mates. Nests are usually concealed in grass or under shrubs and consist of a shallow depression lined with grass, leaves, or other herbaceous vegetation (Ehrlich et al. 1988). Principal forage includes grass blades, flowers, buds, fruits, and grains.

There are some grassy openings in shrub-steppe habitats within the study area, however most of these areas show evidence of grazing and may not be suitable. No sharp-tailed grouse were observed in the study area during this study. The study area is near an existing sharp-tailed grouse population and theoretically could be recolonized, provided that the vegetative structure and plant species composition of these areas are suitable.

Vaux’s Swift The Vaux’s swift (Chaetura vauxi) is a Washington State Candidate Species that is a common breeder in forested parts of Washington (Smith et al. 1997). This species is a local breeder in eastern Washington below the tree line in residential areas.

The west side of Lake Entiat is in the peripheral breeding zone and there are several possible breeding records west of the study area (Smith et al. 1997). This species will nest in a wide variety of habitats, provided that suitable cavities are available, including snags and chimneys.

Suitable forested habitats occur at higher elevations, and to the west of the study area. Potential breeding habitat occurs in developed areas, but no Vaux’s swift were observed during this study.

Lewis’ Woodpecker Lewis’ woodpecker (Melanerpes lewis) is a Washington State Candidate species for which WDFW maintains records of breeding sites. This species is a local and uncommon breeder in the central Columbia Basin (Smith et al. 1997). Competition for nest sites with European starlings and loss of habitat are believed to be responsible for population declines.

The study area is within the core breeding habitat zone and there are several probable and possible breeding records in the vicinity (Smith et al. 1997). Lewis’ woodpeckers inhabit open woodlands and forests, often in burned areas. They are typically associated with wooded riparian corridors in eastern Washington. Nest cavities are excavated in trees, snags, or wooden utility poles. Lewis’ woodpeckers hawk insects, similar to flycatchers, and also glean invertebrates on the ground and from tree bark.

Although suitable habitat for Lewis’ woodpecker occurs within some wooded riparian habitats in the study area, none were observed during the study. Lewis’ woodpeckers have been observed in riparian habitats along the nearby Lake Chelan (Chelan PUD 2000).

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White-headed Woodpecker The white-headed woodpecker (Picoides albolarvatus) is a Washington State Candidate species. This species is a locally common breeder in ponderosa pine forests in the eastern Cascades (Smith et al. 1997). Logging of ponderosa pine stands is thought to be the main reason for the decline of this species.

The east side of Lake Entiat is within the core zone for this species and there is one probable breeding record in this area. White-headed woodpeckers are conifer obligates in Washington and excavate nest cavities in large dead or dying conifers. Suitable habitat for this species generally occurs outside the study area in higher elevation conifer forests.

No white-headed woodpeckers were observed during this study. There are some small patches of ponderosa pine within the study area but their small size may limit their suitability. There have been reports of white-headed woodpeckers in riparian habitats along the nearby Lake Chelan.

Pleated Woodpecker The pileated woodpecker (Dryocopus pileatus) is a Washington State Candidate species. This species is common in low to moderate elevation mature forests (Smith et al. 1997). Because this species requires large trees, timber harvesting may affect their distribution and abundance.

The study area is within the peripheral breeding zone of pileated woodpeckers and there are no breeding records for the study area (Smith et al. 1997). Mature forest stands with abundant large snags are required for this species. Snags are important because pileated woodpeckers excavate a new nesting cavity each year. This species is fairly adaptable to forest stand composition and can be found in coniferous, hardwood, and mixed stands.

Although suitable habitat for pileated woodpecker occurs within some wooded riparian habitats in the study area, none were observed during the study. Pileated woodpeckers have been observed in riparian habitats along nearby Lake Chelan (Chelan PUD 2000).

Olive-sided Flycatcher The olive-sided flycatcher (Contopus borealis) is a Federal Species of Concern but is common in forested habitats in Washington. BBS data shows that this species has declined over most of it’s breeding range (ADF&G 2000). The primary cause for the decline is thought to be deforestation on this species wintering grounds in South America.

The study area is adjacent to core breeding zones and several possible breeding records are in the Project vicinity (Smith et al. 1997). Olive-sided flycatchers prefer large forested areas adjacent to cleared areas, burns, or water bodies.

Suitable large forested areas generally occur at higher elevations in the Project vicinity. Habitats within the study area are of limited suitability and no olive-sided flycatchers were observed during this study.

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Willow Flycatcher The willow flycatcher (Empidonax traillii) is a Federal Species of Special Concern but has no Washington designation. In the Columbia Basin, this species is a local and rare breeder below the ponderosa pine zone. BBS data for Washington indicate that statewide the willow flycatcher has increased significantly (8.4 percent per year) from 1966 to 1991 (Smith et al. 1997).

The west side of Lake Entiat is in the peripheral breeding zone and there are several probable and possible records west of the study area (Smith et al. 1997). This species typically breeds in low elevation wetlands and shrub dominated habitats, but other non-forested habitats may be used such as forest openings, agricultural areas, low-density developments, and clearcuts.

Although suitable habitat for willow flycatcher occurs within some riparian shrub and upland shrub habitats in the study area, none were observed during this study.

Loggerhead Shrike The loggerhead shrike is a Federal Species of Concern and Washington State Candidate species for which WDFW maintains records of breeding sites. This species is uncommon in relatively undisturbed shrub-steppe habitats of the central Columbia Basin (Smith et al. 1997). Loggerhead shrikes were more widespread prior to the massive conversion of shrub-steppe habitats to agricultural lands.

The study area is within the core breeding habitat zone for loggerhead shrikes; there are several possible breeding records within the Project vicinity (Smith et al. 1997). The BBS has reported a slight increase in numbers from 1966 to 1991 in Washington. Over the same period in Oregon, this species has declined by 3.7 percent, and anecdotal evidence indicates declines in Walla Walla and Lincoln Counties in Washington (Smith et al. 1997).

Loggerhead shrikes prefer a mixture of shrub-steppe patches and grassy areas, rather than contiguous shrub-steppe areas (Smith et al. 1997). This species nests in shrubs and trees, and feeds on insects and small vertebrates, such as birds, mice, and lizards (Ehrlich et al. 1988). Loggerhead shrikes often impale their prey on plant spines or barbed-wire either to eat immediately or to store for future use. Conversion of shrub-steppe habitats to agricultural lands has been implicated in the widespread decline of this species.

At least two pairs of loggerhead shrikes were observed at the Uplake Shrub-steppe site during the breeding bird surveys. Although no nests were found these individuals were displaying territorial and nesting behavior and were likely breeding at this site. This was the largest most remote tract of shrub-steppe habitat surveyed and had varying shrub densities and plant species composition. This area also had evidence of grazing and had abundant grassy openings dominated by cheatgrass and bunchgrass. Several smaller fragmented shrub-steppe habitats were also surveyed, but this species was not observed in them. Although difficult to assess from a 1-year study, the pattern of occurrence documented for loggerhead shrikes suggests that small, fragmented shrub-steppe habitats near human developments may be of limited suitability.

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Sage Thrasher The sage thrasher (Oreoscoptes montanus) is a Washington State Candidate species for which WDFW maintains records of breeding sites. This species is common in sagebrush and bitterbrush habitats in the Columbia Basin, but was more widespread prior to the conversion of large tracts of sagebrush habitats to agricultural lands.

The study area is within the core breeding habitat zone for sage thrasher; there are several probable, and possible breeding records within the Project vicinity (Smith et al. 1997). The BBS has reported low and declining numbers over the past 20 years.

Sage thrashers nest in sagebrush and bitterbrush habitats with an associated cover of perennial native grasses (Smith et al. 1997). Sage thrasher is considered a shrub-steppe obligate (WDFW 2000a). Nests are typically on the ground beneath sagebrush or in a sagebrush plant. Sage thrashers generally glean insects and some berries from the ground. Fragmentation of sagebrush habitats and disturbance during nesting may limit the availability and suitability of nesting habitats. Knick and Rotenberry (1995) found that the probability of occupancy within a given area was positively related to sagebrush patch size and total sagebrush cover, and inversely related to human disturbance. The authors speculated that habitat fragmentation adversely affected sage thrasher and other shrub-steppe species through lower reproductive rates and increased predation, although the mechanism is obscure.

Although suitable habitat for sage thrasher occurs within some large tracts of relatively undisturbed shrub-steppe, none were observed during the study. Small, fragmented, and disturbed shrub-steppe habitats within the study area may be of limited suitability.

Sage Sparrow The sage sparrow (Amphispiza belli) is a Washington State Candidate species for which WDFW maintains records of breeding sites. This species is uncommon and declining in sagebrush habitats in the Columbia Basin. Conversion and fragmentation of sagebrush habitats is thought to be a factor in this species’ decline (Smith et al. 1997).

The study area is within the core breeding habitat zone for sage sparrow, but there are no breeding records within the Project vicinity (Smith et al. 1997). The BBS has reported uniformly negative population trends for Washington over the past 25 years (Smith et al. 1997).

Sage sparrows are considered shrub-steppe obligates (WDFW 2000a) and require large tracts of sagebrush. The exact habitat requirements of sage sparrows are not well known; apparently suitable habitats are often lacking this species (Smith et al. 1997). Nests are typically within the shrub canopy and are placed in the densest areas of vegetation or in clumps of shrubs if the overall shrub cover is sparse (Smith et al. 1999). Sage sparrows generally glean insects and seeds from the ground. Fragmentation of sagebrush habitats and disturbance during nesting may limit the availability and suitability of nesting habitats. Knick and Rotenberry (1995) found that the probability of occupancy within a given area was positively related to sagebrush patch size and total sagebrush cover, and inversely related to human disturbance. The specific mechanism by which fragmentation adversely affects sage sparrow is unknown.

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Although suitable habitat for sage sparrows occurs within some large tracts of relatively undisturbed shrub-steppe, none were observed during the study. Small, fragmented, and disturbed shrub-steppe habitats within the study area may be of limited suitability.

Merriam’s Shrew Merriam’s shrew is a Washington State Candidate for which WDFW maintains records of known populations. The status of Merriam’s shrew populations in Washington is largely unknown. Records of occurrence are widely scattered and based mostly on opportunistic captures or retrieval from owl pellets. This species is not known to occur in areas of intensive agriculture (Johnson and Cassidy 1997).

The east bank of Lake Entiat is within the core habitat zone for Merriam’s shrew but there are no confirmed records in the Project vicinity (Johnson and Cassidy 1997). There is no evidence that this species has crossed to the west side of the Columbia River north of Vantage. Merriam’s shrew is most commonly found in shrub-steppe habitats, but also occurs in semi-arid grasslands. In Washington, Merriam’s shrew is closely associated with the sagebrush vole, and has not yet been documented where this vole is absent (Johnson and Cassidy 1997). Several studies suggest that the Merriam’s shrew uses the runways of the sagebrush vole, and other voles, for travel and foraging (Wilson and Ruff 1999). Merriam’s shrew feeds on a wide variety of invertebrates, including spiders, beetle adults and larvae, crickets, caterpillars, and wasps.

Although suitable habitat for Merriam’s shrew occurs within some large tracts of relatively undisturbed shrub-steppe, none were captured during the study.

Colonial Roosting Bats As many as 12 species of colonial roosting bats, and three solitary roosting bats, are possible in the Project vicinity. Six of the colonial species are Federal Species of Concern primarily because populations are potentially vulnerable to great harm if roosts are threatened. WDFW monitors roosting concentrations of big brown bat, pallid bat, and all species of mouse-eared bats (Myotis) as vulnerable aggregations (WDFW 2000a). Townsend’s big-eared bat is a State Candidate species; maternal colonies of this species are also monitored as vulnerable aggregations (WDFW 2000a). Compared to other mammalian taxa, the habitat requirements and other natural history features of bats are poorly understood.

The distribution and abundance of bats is often directly related to the availability of certain prominent physical features, including both natural and man-made structures (Cooperrider et al. 1986). These physical features, described as “unique habitats” by Maser et al. (1979) typically comprise only a small percentage of the total land area, but are often disproportionately important as habitat for roosting and foraging. Although vespertilionid (plain-nose) bats are best known for their use of caves, they have been found roosting in a wide variety of structures, including trees (hollows, under and within bark, in foliage), rock crevices, animal burrows, storm sewers, abandoned mines, buildings, and holes under rocks (Nagorsen and Brigham 1993).

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Small-footed myotis, little brown myotis, and Yuma myotis were captured during this study. Several small-footed myotis were captured under the bridge over the Chelan River and one was captured at the Uplake Shrub-steppe site. A single Yuma myotis was captured at the Sun Cove Riparian site and a single little brown myotis was captured at the Entiat River site. Although there were relatively few bat captures overall, cliffs and other areas of exposed rock in the region contain abundant rock crevices and caves that could potentially be used by many of these colonially roosting bat species. Constructed features such as bridges, tunnels, and buildings also provide suitable roost sites. Species reliant on tree-cavities for roosting have much more limited habitat.

Washington Ground Squirrel The Washington ground squirrel (Spermophilus washingtoni) is a Federal Species of Concern and Washington State Candidate for which WDFW maintains records of known populations. The range of the Washington ground squirrel has recently decreased dramatically, due mostly to loss and fragmentation of habitats (Betts 1999). This species is rare and local, occurring mostly in southeast Washington.

The study area is not within the core habitat zone of this species (Johnson and Cassidy 1997). There are confirmed Washington ground squirrel populations in the eastern half of Grant County and potential core habitat within the southern part of Douglas County near Rock Island Dam. Most of the species’ current range is in uncultivated steppe habitats in Walla Walla, Franklin, Adams, Lincoln, and Grant Counties.

The Washington ground squirrel is most commonly found in dry grasslands or in patches of grass and forbs within low, open sagebrush (Johnson and Cassidy 1997). This species prefers areas with deep, well-drained, loose soils, which are conducive to burrowing (Wilson and Ruff 1999). Washington ground squirrels feed on a wide variety of grasses, green forbs, roots, bulbs, flowers, seeds, and some insects. Conversion of native grasslands to agriculture has fragmented the distribution of this species into isolated and sometimes small populations (Betts 1999). Small populations are particularly vulnerable to extirpation from predation, disease, trapping, poisoning, or loss of remaining habitat. Betts (1999) reported that Washington ground squirrels had disappeared from 48 of 65 (73.8 percent) of previously reported sites in Washington.

No Washington ground squirrels were observed or captured during this study. Although there is some suitable habitat within the study area, it is unlikely that a population of Washington ground squirrels occurs because the species range is mostly outside of the Project vicinity.

Western Gray Squirrel The western gray squirrel (Sciurus griseus) is a Federal Species of Concern and listed as threatened by WDFW. This species occurs in disjunct populations in Washington. The west side of Lake Entiat is in the peripheral zone and there are no confirmed records for either Chelan or Douglas Counties.

Suitable habitats for western gray squirrel are open forests of broadleaf, nut-bearing trees occurring in pure or mixed stands at low elevations (Johnson and Cassidy 1997). Oaks and western hazel (Corylus cornuta) are among the preferred foods.

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This species is unlikely to occur in the study area due to the lack of nut-bearing trees, although pine seeds are sometimes eaten. No western gray squirrels were observed during this study.

Sagebrush Vole The sagebrush vole is a Washington State Monitor species. The status of sagebrush vole populations in Washington is not well known. Records of occurrence are widely scattered and based mostly on opportunistic captures or retrieval from owl pellets.

The east bank of Lake Entiat is within the core habitat zone for sagebrush vole but there are no confirmed records in the Project vicinity (Johnson and Cassidy 1997). There is no evidence that this species has crossed to the west side of the Columbia River north of Vantage. Sagebrush vole is most commonly found in shrub-steppe habitats with well-drained but sometimes rock-covered soils. This species is not known to occur in areas of moist dense grasses (Johnson and Cassidy 1997). This species usually occurs in colonies with intricate burrows (Wilson and Ruff 1999). Despite living in semiarid habitats, sagebrush vole feed entirely on green vegetation including leaves, green seed heads, and pods.

Although suitable habitat for sagebrush vole occurs within some large tracts of relatively undisturbed shrub-steppe, none were captured during the study.

California Bighorn Sheep The California bighorn sheep (Ovis canadensis) is a Federal Species of Special Concern but has no Washington State designation. This species occurs in disjunct populations east of the Cascade crest. California bighorn sheep are affected by human disturbance, and diseases carried by livestock (Johnson and Cassidy 1997).

The west side of Lake Entiat is within the core zone for California bighorn sheep and there are confirmed records within the Project vicinity (Johnson and Cassidy 1997). This species inhabits steep terrain, rocky slopes, ridges, cliffs, and canyons adjacent to grassy habitats.

This species is known to occur on the Chelan County side of the study area near Swakane Canyon (Chelan PUD 1999). Highway 97 probably acts as a barrier between this population and the study area. No California bighorn sheep were observed during this study.

Sagebrush Lizard The northern sagebrush lizard is a Federal Species of Concern but has no Washington State status. Regional herpetological faunas and field guides do not indicate that this species is rare or declining in Washington (Johnson 1954, Nussbaum et al. 1983, McAllister 1995, Storm and Leonard 1995); however, its distribution is fragmented due to habitat loss and this may affect the viability of small populations.

The sagebrush lizard is a characteristic lizard of open, arid habitats, from shrub-steppe to conifer savanna. Favored habitats include sandy areas, including sand dunes, as well as rocky areas. Most of the terrestrial habitats in the study area, except irrigated agricultural lands, are considered suitable

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A single sagebrush lizard was found at each of four sites during this study, each time as an incidental observation: Turtle Rock, Sun Cove Shrub-steppe, Beebe Bridge, and Gallagher Flats. These few observations at sites where we spent considerable time and conducted intensive searches might suggest scarcity, but more likely is evidence of a very wary species adept at avoiding detection. Apparently suitable habitats (sandy or rocky shrub-steppe areas) are widespread in and adjacent to the study area.

Night Snake The night snake is a Washington State Monitor species for which WDFW maintains records of observations. This species is difficult to locate due to its secretive habits; thus, its distribution, habitat preference, and life history are not well documented (Storm and Leonard 1995). The night snake is probably more widespread than current records suggest.

The study area is within the core habitat zone of the night snake (Dvornich et al. 1997). This species occurs throughout the Columbia Basin, although there are no records in the vicinity of the study area. This is a poorly documented species, rarely found without special effort (usually including night surveys, or drift fences and pitfall traps). Habitat associations and modeled distribution presented by Dvornich et al. (1997) for this species are admittedly uncertain and may need to be revised when better information becomes available. Night snakes have been found in a variety of arid habitats including shrub-steppe, scrub, grasslands, and rocky areas (including rubble at the base of cliffs or talus). Riparian habitats were also considered good potential habitats by WSGAP (Dvornich et al. 1997). Night snakes evidently hide in rock crevices, amid shrubs, and in rodent burrows. Prey may mostly consist of side-blotched lizards (Storm and Leonard 1995), suggesting that these snakes should be sought in areas where the lizards have been found. Other prey includes insects, small frogs and toads, and lizard eggs.

No night snakes were observed within the study area during this study. It is unknown whether the fragmented blocks of native shrub-steppe the characterize much of the study area represent suitable habitat for this species. We did not find the principal prey species, side-blotched lizard. Apparently suitable habitats may be concentrated in areas north of Beebe Bridge where there are expanses of shrub-steppe and localized rocky areas, including fractured rock and talus slopes.

Sharptail Snake The sharptail snake is a Washington State Candidate species for which WDFW maintains records of observations. The distribution and habitat requirements of this species are poorly known. Published records are very scarce, with none in the vicinity of the study area. A small portion of the study area on the west side of Lake Entiat extending from Rocky Reach Dam to Entiat is within the modeled core habitat zone (Dvornich et al. 1997), based largely on a single record in forested country 25 mi. to the northwest. Sharptail snakes prey on small slugs, perhaps exclusively (Nussbaum et al. 1983, Storm and Leonard 1995).

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Moist sites with hiding cover under rocks or in rotted logs are evidently favored. If so, suitable habitats in the study area are probably limited only to the best developed riparian habitats, particularly areas along the Entiat River. Because this tributary extends into forested areas west of the study area, riparian habitats along the Entiat River may provide a dispersal corridor for sharptail snake. Other riparian habitats along Lake Entiat, particularly on the west side, are generally narrow and discontinuous, with few trees. No sharptail snakes were observed during this study.

Western Toad Western toad is a Washington State Candidate species for which WDFW maintains records of observation, and a Federal Species of Concern. Some populations of western toad in Washington, particularly in southern Puget Sound and in the North Cascades, have inexplicably declined or disappeared. This remains a common species in many other areas.

The study area is not within an area modeled by Dvornich et al. (1997) as either core or peripheral habitat for this species. There are, however, records outside of the modeled habitat zones, including a record at Entiat. These records may reflect habitat features uncharacteristic of the prevailing habitat.

Western toads breed in ponds, marshes, the shallow margins of small lakes, and in backwaters of streams and rivers. Along the Snake River, western toads reportedly breed in flood water pools and delay breeding until flood waters recede (Metter 1960). Larvae of this species are not adapted for moving water, but sometimes occur in sluggish streams. Like other toads, western toad is physiologically and behaviorally adapted for surviving relatively dry conditions and often occurs far from water. Western toad was found at four sites during this study (Sun Cove Riparian, Sun Cove Shrub-steppe, Turtle Rock, and at Amphibian Survey site 13, which is about 2 miles north of Orondo). Other populations are possible in the study area.

Columbia Spotted Frog The Columbia spotted frog is a Washington State Candidate species for which WDFW maintains records of observations, and a Federal Species of Concern. There is currently no compelling evidence that this species is in decline in Washington.

Columbia spotted frogs is found only peripherally in the most arid parts of the Columbia Basin. Because these frogs are highly aquatic during all life stages, they may require wetland complexes larger than tend to occur in arid areas. Spotted frogs breed in standing or sluggish water including ponds, lake edges, marshes, slow-moving streams, backwaters, and floodwater pools. Breeding typically occurs in late winter or early spring when waters are ice-free. Egg masses can be found at the water surface in very shallow water (often not completely submerged), and not attached to vegetation. The masses are typically aggregated; most or all of the frogs at a breeding site will have laid their egg masses at the same spot.

Potential habitats for this species are scarce in the study area. The modeled habitat area (Dvornich et al. 1997) encompasses the west side of Lake Entiat; however, there are relatively few ponds and wetlands in this reach, and few of these appear suitable for Columbia spotted frog.

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Most of the ponds have resident predatory fish. The marshy, seasonally flooded pools at Azwell may constitute suitable habitat, provided there are perennial moist refugia. Similarly, Gallagher Flats may have been a suitable site before the hydrology of the site was disrupted by drainage ditches and construction of Highway 97. A collection record for Columbia spotted frog at Entiat or Entiat River (McAllister 1995) might indicate an extant population; however, likely habitat areas were not observed during this study.

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RTE Wildlife & Cover-type Mapping

Table 4-1: Comparison of Cover-Type Summary Data from Ebasco Environmental (1991) and Rocky Reach RTE Wildlife and Cover-Type Mapping Study (2000). Total Area: 1991 Total Area: Current Change COVER TYPE CATEGORY Acres Percentage Acres Percentage Acres Percentage UPLAND COVER TYPES Shrub-steppe (SS) 1032.99 27.86 828.69 22.27 -204.30 -19.78 Grassland (G) 141.88 3.83 60.71 1.63 -81.17 -57.21 Forbland (F) 92.27 2.49 71.49 1.92 -20.78 -22.52 Equisetum/Grassland (EQ) 4.99 0.13 0.51 0.01 -4.48 -89.78 Conifer Shrub (CS) 42.07 1.13 15.06 0.40 -27.01 -64.20 Upland Conifer (UC) 7.37 0.20 7.54 0.20 0.17 0.02 Upland Deciduous (UD) 13.38 0.36 12.53 0.34 -0.85 -6.35 Exposed Rock (ER) 34.22 0.92 30.48 0.82 -3.74 -10.93 Exposed Rock/Shrub- 104.21 2.81 106.31 2.86 2.10 2.02 Steppe (ER/SS) Rock Talus (RT) 1.05 0.03 4.82 0.13 3.77 359.05 Sand Bank (SB) 0.90 0.02 0.83 0.02 -0.07 -7.78 Sand Dune (SD) 11.34 0.31 5.03 0.14 -6.31 -55.64 Unconsolidated Shore (US) 57.36 1.55 71.06 1.91 13.70 23.88 Bare Ground (BG) 11.06 0.30 22.86 0.61 11.80 106.69 TOTAL UPLAND 1555.09 41.94 1237.92 33.27 -317.17 -20.40 RIPARIAN AND WETLAND COVER TYPES Riparian Deciduous and 140.37 3.79 115.42 3.10 -24.95 -17.77 Palustrine Forested (RD, PF) Riparian Shrub and 116.22 3.13 147.65 3.97 31.43 27.04 Palustrine Scrub-Shrub (RS, PS) Riparian Mixed (RM) 0.89 0.02 1.50 0.04 0.61 68.54 Riparian Grassland (RG) 90.91 2.45 56.08 1.56 -32.83 -36.11

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Total Area: 1991 Total Area: Current Change COVER TYPE CATEGORY Acres Percentage Acres Percentage Acres Percentage Emergent Wetlands (PE, 13.26 0.36 18.31 0.49 5.05 38.08 PEB, PEC) Aquatic Bed (PAB) 1.95 0.05 2.11 0.06 2.11 8.21 TOTAL RIPARIAN AND 363.60 9.81 343.07 9.22 -20.53 -5.65 WETLAND DISTURBED/DEVELOPED/ MODIFIED COVER TYPES Residential/Industrial (RI) 350.28 9.45 581.10 15.62 230.82 65.90 Recreational (RE) 153.27 4.13 212.51 5.71 59.24 38.65 Orchard (OR) 951.80 25.67 937.22 25.19 -14.58 -1.53 Grassland/Forbland (G/F) NA NA- 49.91 1.34 NA NA Pasture (P) 90.60 2.44 69.54 1.87 -21.06 -23.25 Disturbed (D) 80.99 2.18 125.57 3.37 44.58 55.04 Rip-rap (RP) 138.34 3.73 135.92 3.65 -2.42 -1.75 Road (ROAD) 21.97 0.59 26.10 0.70 4.13 18.80 Railroad (RR) 2.29 0.06 2.31 0.06 0.02 0.87 TOTAL 1789.54 48.26 2140.18 57.51 350.64 19.59 DISTURBED/DEVELOPED/ MODIFIED TOTAL ALL TERRESTRIAL 3708.23 100.00 3721.17 100.00 12.94 0.35 AND WETLAND OPEN WATER COVER-TYPES Lacustrine Open Water 9210.73 99.88 9179.14 99.89 -31.59 -0.34 (LOW) Riverine Open Water 9.41 0.01 9.55 0.01 0.14 1.49 (ROW) Palustrine Open Water 1.42 0.00 0.32 0.00 -1.10 -77.46 (POW) TOTAL ALL WATER 9221.56 100.00 9189.01 100.00 -32.55 -0.35 COVER-TYPES

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Table 4-2: Mean values of habitat data collected within cover-types during the Rocky Reach RTE Wildlife Study. Habitat Variable RD1 RS PE RE SS ERSS Canopy Height (ft) 12.7 NA NA 10.2 NA NA Canopy Depth (ft) 35.1 NA NA 26.2 NA NA Tree Cover (%) 66.4 17.8 3.8 48.0 2.0 0.6 Deciduous Tree Cover (%) 66.4 17.8 3.8 40.0 0.0 0.0 Conifer Tree Cover (%) 0.0 0.0 0.0 8.3 2.0 0.0 Shrub Cover (2-5m) (%) 18.7 45.8 15.6 11.3 10.4 9.2 Deciduous Shrub Cover (2-5m) (%) 18.7 45.8 15.6 11.3 10.4 9.2 Conifer Shrub Cover (2-5m) (%) 0.0 0.0 0.0 0.0 0.0 0.0 Shrub Cover (0.5-2m) (%) 21.9 32.9 17.2 8.6 40.3 26.2 Deciduous Shrub Cover (0.5-2m) (%) 21.9 32.9 17.2 8.6 40.3 26.2 Conifer Shrub Cover (0.5-2m) (%) 0.0 0.0 0.0 0.0 0.0 0.0 Herbaceous Ground Cover (%) 47.9 57.4 86.6 78.3 67.3 51.0 Downed Woody Debris (%) 14.7 9.2 12.8 0.6 6.4 7.1 Rock/Boulder Cover (%) 4.0 4.4 0.0 7.5 13.5 59.2 Number of Snags (per plot) 0.5 0.0 0.0 0.4 0.0 0.0 Snag DBH (in) 13.8 NA NA 10.8 NA NA Tree DBH (in) 13.1 8.8 6.5 12.7 13.1 14.5 1RD = Riparian Deciduous (N=19); RS = Riparian Shrub (N=14); PE = Palustrine Emergent (N=5); RE = Recreational Facility (N=9); SS = Shrub-steppe (N=25); ERSS = Exposed Rock/Shrub-steppe (N=11).

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Table 4-3: Environmental setting and general conditions at the Seven Intensive Study Sites. Study Site Location1 Regional Setting Habitats Present Common Plant Species Turtle Rock 475.0-476.0 Large island nearest the east bank of Upland types: SS, G, ERSS, and Big sagebrush, bitterbrush, Island Lake Entiat. Part of mainland prior ER, including cliff. Narrow rabbitbrush, Russian olive, cheat to project. fringe of RS, RD, RG, and PE. grass. Entiat River 483.7 W Large tributary in a relatively Mostly RD, RS, and PE Black cottonwood, white alder, red- confined valley. Bordered (south) osier dogwood, willows, cattail, reed by Swakane Wildlife Area and canary grass, horsetail, softstem (north) Town of Entiat. bulrush, and poison ivy. Sun Cove 491.6-492.1 E Relatively flat landscape. Bordered Mostly scrubby RD, RS, and PE, Black cottonwood, white alder, red- Riparian by residential development and including pond. osier dogwood, coyote willow, cattail, orchards. reed canary grass, horsetail, softstem bulrush, and western poison ivy. Sun Cove 492.4-492.8 E Relatively flat landscape. Bordered Upland types: SS and SD; Bitterbrush, big sage brush, Shrub-steppe by residential development and Riparian fringe and inland rabbitbrush, cheatgrass, black orchards. wetland (PS and PE) cottonwood, coyote willow, cattail, and reed canarygrass. Beebe Bridge 503.6-504.3 W Relatively flat landscape. Bordered Mostly riparian types: RD, RS, Siberian elm, Lombardy polar, by industrial sites and residential and PE. LOW pond. blackberry, coyote willow, white development. alder, western poison ivy, reed canarygrass, and cattail. Gallagher 506.7-507.3 W Confined to a relatively flat basin Mostly disturbed F, with PE, SS, Knapweed, vetch, milkweed, dogbane, Flats surrounded by steep arid hills and RD, and RS. black cottonwood, bitterbrush, big Lake Entiat. sagebrush, white alder blackberry, cattail and western poison ivy. Uplake 510.5-511.9 E Relatively flat delta shaped area Relatively uniform SS with some Big sagebrush, bitterbrush, Shrub-steppe surrounded by larger shrub-steppe open G. rabbitbrush, buckwheat, cheatgrass, tract with some steep hills and and bunchgrasses. canyons. 1Location by River Mile (RM) and Bank (E = East Bank, W = West Bank)

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Table 4-4: Environmental setting and general conditions at the 11 Roving Study Sites. Study Site Location Regional Setting Habitats Present Common Plant Species Chelan PUD 475.5-475.8 W Adjacent uplands are shrub- Narrow riparian fringe, mostly RS (some Siberian elm, red-osier dogwood, Riparian steppe. Railroad parallels RD). western sumac, blackberry, site. serviceberry, and western poison ivy. Unnamed 481.8-482.3 W Small islands separated by Mostly open SS with very narrow and Siberian elm, big sagebrush, and Islands narrow channels. Adjacent limited RS. bitterbrush. mainland is steep hills. Orondo School 482.4-482.6 E Directly behind Orondo Riparian deciduous and riparian shrub Choke cherry, red-osier dogwood, Riparian School along a large covet. habitats on a steep bank. willows, and western poison ivy. Orchards occupy adjacent areas. Entiat Park 484.0-484.5 W Adjacent areas are residential Park setting with many large trees. Some Black cottonwood, Siberian elm, and industrial. riparian shrub and emergent habitats along and Lombardy poplar. the shore of Lake Entiat. Extensive lawns. Daroga Park 487.0-487.5 E Located in a large cove. RE with many large planted trees. Small Lombardy poplar and ponderosa Adjacent areas occupied by areas of RS and PE associated with LOW. pine. orchards. Extensive lawns. Earthquake 488.0-488.2 W Small islands separated by Rocky with SS and CS (few trees). Very Ponderosa pine, big sagebrush, Point Islands narrow channels. Adjacent narrow and sparse RS. serviceberry, sumac, and western mainland is steep hills. poison ivy. Bundy Shrub- 490.3-490.6 E Adjacent areas occupied by Relatively uniform SS with some G. Bitterbrush, big sagebrush, steppe orchard and some residential Narrow fringe of RD and RS along Lake rabbitbrush, buckwheat, and dwelling. Entiat. squaw currant. Goosetail Rock 493.4-493.6 W Protected cove. Adjacent RD, RS, and PE along a protected cove. Black cottonwood, white alder, areas occupied by orchards Large ER with sheer cliffs. willows, big sagebrush, and a residential dwelling. serviceberry, and western poison ivy. Chelan Butte 498.6-500.3 W Along railroad on edge of ER (with cliffs) with some RT and SS at Big sagebrush, bitterbrush, WMA Chelan Butte WMA. the base. Several small intermittent serviceberry, and rabbitbrush. Adjacent to steep cliffs drainages. Chelan Falls 503.0-503.2 W At the confluence of the RE with some large planted trees. Some Black cottonwood, weeping Park Chelan River. Adjacent areas RS and PE along the shore of Lake Entiat. willow, Douglas-fir, and coyote industrial and residential. Extensive lawns. willow. Azwell Riparian 513.9-514.0 W Along a small periodically RD, RS, and PE associated with a Black cottonwood, black

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Study Site Location Regional Setting Habitats Present Common Plant Species flooded cove. Adjacent areas periodically flooded protected cove. hawthorn, pearhip rose, black occupied by orchards. locust, willows, and western poison ivy. 1Location by River Mile (RM) and Bank (E = East Bank, W = West Bank)

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Table 4-5: Relative abundance1 of bird species documented by point count surveys at the Intensive Study Sites during the Rocky Reach RTE Wildlife Study. Species TR2 ER SCR SCS BB GF ULS Great blue heron 0.20 0.04 Canada goose 0.04 Wood duck 0.04 0.07 0.08 Mallard 0.04 0.48 0.07 0.21 0.27 Common merganser 0.44 Osprey 0.04 American kestrel 0.13 0.07 Ring-necked pheasant 0.11 California quail 0.11 0.53 0.17 0.13 0.11 Killdeer 0.07 0.07 0.25 Spotted sandpiper 0.07 0.27 California gull 0.08 Rock dove 0.63 Mourning dove 0.46 0.07 0.40 0.28 0.71 0.27 White-throated swift 0.04 0.13 Black-chinned hummingbird 0.07 0.17 Calliope hummingbird 0.06 Belted kingfisher 0.11 0.07 0.08 Downy woodpecker 0.07 0.20 0.06 0.04 Northern flicker 0.13 0.30 0.53 0.11 0.50 0.27 0.04 Western wood-pewee 0.11 0.33 0.06 0.21 Say's phoebe 0.04 0.04 0.06 Western kingbird 0.08 0.07 0.13 0.19 Eastern kingbird 0.13 0.07 0.22 0.08 0.40 0.04 Tree swallow 0.04 0.44 0.21 0.33 Violet-green swallow 1.38 0.63 0.22 Northernrough-winged swallow 0.19 Cliff swallow 1.08 0.04 1.50 0.04 Barn swallow 0.06 Black-billed magpie 0.71 0.11 0.06 1.40 0.04 American crow 0.41 0.04 Black-capped chickadee 0.11 0.53 0.33 Rock wren 0.29 0.07 Canyon wren 0.21 American dipper 0.04 American robin 0.25 0.33 0.67 0.17 0.54 0.47 0.11 Gray catbird 0.07 0.07 0.04 0.13 Cedar waxwing 0.04 0.33 0.38 0.20 Loggerhead shrike 0.63

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Species TR2 ER SCR SCS BB GF ULS European starling 3.00 0.85 0.20 0.56 0.58 0.20 Warbling vireo 0.07 Red-eyed vireo 0.04 Orange-crowned warbler 0.04 Yellow warbler 0.11 0.8 0.06 0.75 0.13 Yellow-rumped warbler 0.06 Common yellowthroat 0.04 Wilson's warbler 0.07 0.13 0.06 0.13 0.07 Yellow-breasted chat 0.11 Western tanager 0.11 0.07 Black-headed grosbeak 0.20 0.11 0.21 Lazuli bunting 0.08 0.28 0.07 Spotted towhee 0.67 0.17 0.11 Lark sparrow 0.33 Song sparrow 0.13 0.26 0.06 0.38 0.20 White-crowned sparrow 0.67 Red-winged blackbird 0.42 1.04 1.00 0.33 0.38 0.47 Western meadowlark 0.08 0.44 0.13 1.15 Brewer's blackbird 0.42 0.48 0.07 0.28 0.21 0.89 Brown-headed cowbird 0.04 0.22 0.40 0.61 0.75 0.27 Northern oriole 0.08 0.19 0.40 0.56 0.50 0.73 0.19 Cassin's finch 0.33 0.13 0.07 House finch 0.06 0.04 American goldfinch 0.25 0.15 0.33 0.61 1.04 0.93 Total Number of Species 27 39 26 31 32 23 15 Mean Number Species/Survey 4.2 5.0 5.8 4.9 7.0 4.7 2.4 Total Relative Abundance 10.5 8.1 8.0 7.2 10.7 7.4 4.0 1 Mean number of individuals recorded per visit at each survey point. 2 TR: Turtle Rock (N=8 points) ER: Entiat River (N=9) SCR: Sun Cove Riparian (N=5) SCS: Sun Cove Shrub-steppe (N=6) BB: Beebe Bridge (N=8) GF: Gallagher Flats (N=5) ULS: Uplake Shrub-steppe (N=9)

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Table 4-6: Relative abundance1 of bird species documented by point count surveys at the Roving Study Sites during the Rocky Reach RTE Wildlife Study. Species PR2 IS EP OS DA BS EP GTR CB CF AZ Great blue heron 0.22 0.17 0.22 Canada goose 0.40 0.44 1.33 1.17 1.67 Wood duck 0.33 Mallard 0.20 0.11 0.22 0.67 0.17 0.11 0.33 Common merganser 0.17 0.50 2.33 Osprey 0.17 Sharp-shinned hawk 0.07 Red-tailed hawk 0.17 American kestrel 0.06 Chukar 0.33 0.06 California quail 0.40 0.67 0.17 0.67 Killdeer 0.67 0.33 0.56 Spotted sandpiper 0.11 0.11 0.33 0.17 0.22 0.22 Ring-billed gull 0.11 1.00 California gull 0.22 Rock dove 3.00 4.67 0.89 Mourning dove 0.40 0.11 0.50 0.33 0.39 0.33 Belted kingfisher 0.13 0.11 0.17 0.11 0.17 0.33 0.06 0.33 0.11 Downy woodpecker 0.11 Northern flicker 0.27 0.11 0.17 0.56 0.06 0.56 Western wood-pewee 0.33 0.11 0.11 0.11 Say's phoebe 0.11 0.28 0.11 Western kingbird 0.13 0.11 0.11 0.25 0.67 0.22 Eastern kingbird 0.13 0.11 0.33 0.83 0.17 0.28 0.33 0.33 Tree swallow 1.13 0.56 0.50 2.44 0.22 Violet-green swallow 4.00 2.33 0.06 Northern rough- 0.13 0.22 0.78 winged swallow Cliff swallow 0.07 4.00 7.17 1.00 1.22 1.56 Barn swallow 1.33 2.33 0.11 Steller's jay 0.17 0.33 Black-billed magpie 0.13 0.33 0.17 0.17 0.22 American crow 1.11 0.17 0.11 0.17 0.22 Black-capped 0.33 0.83 0.83 chickadee Chestnut-backed 0.11 chickadee Rock wren 0.67 Canyon wren 0.56

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Species PR2 IS EP OS DA BS EP GTR CB CF AZ American robin 0.27 0.11 0.33 0.22 0.33 0.33 0.17 1.33 0.11 Gray catbird 0.67 0.08 Cedar waxwing 0.33 0.33 0.11 0.83 0.50 0.22 0.44 European starling 0.87 1.67 2.00 2.67 0.42 0.67 0.06 1.78 0.67 Solitary vireo 0.11 Warbling vireo 0.11 Orange-crowned 0.20 0.17 warbler Yellow warbler 0.13 0.11 0.17 0.67 0.50 0.33 0.22 Yellow-rumped 0.47 0.11 0.11 0.11 warbler Wilson's warbler 0.07 0.17 0.17 Yellow-breasted chat 0.44 Western tanager 0.07 0.17 0.11 0.11 Black-headed grosbeak 0.33 0.11 Lazuli bunting 0.33 0.44 Spotted towhee 0.33 0.11 Chipping sparrow 0.07 Lark sparrow 0.08 Song sparrow 0.07 0.17 0.22 White-crowned 0.13 sparrow Dark-eyed junco 0.11 Red-winged blackbird 0.22 0.67 0.56 Western meadowlark 0.07 0.50 Brewer's blackbird 0.67 0.11 0.67 1.33 0.17 1.78 Brown-headed 0.53 0.33 0.11 0.33 0.33 0.92 0.17 0.33 0.06 0.44 0.44 cowbird Northern oriole 0.47 0.22 0.33 0.33 0.67 0.11 0.33 0.67 Cassin's finch 0.07 0.67 0.28 0.33

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Species PR2 IS EP OS DA BS EP GTR CB CF AZ House finch 0.07 0.33 0.33 0.25 0.17 American goldfinch 0.67 1.11 0.50 0.78 1.42 0.17 0.33 0.22 0.22 House sparrow 0.40 Total Number of 33 17 18 22 19 13 17 23 22 28 25 Species Mean Number 5.7 2.3 4.6 6.3 5.9 3.7 4.2 6.3 3.9 7.1 6.0 Species/Survey Total Relative 9.5 3.1 10.0 9.7 10.9 5.4 17.7 24.3 6.3 15.9 8.9 Abundance 1 Mean number of individuals recorded per visit at each survey point.

2 PR: PUD Riparian across from Turtle Rock (N=5 points) IS: Islands downstream of Entiat River (N=3) EP: Entiat Park (N=3) OS: Orondo School Riparian (N=2) DA: Daroga Park (N=3) BS: Bundy Shrub-Steppe (N=4) EP: Earthquake Point (N=2) GTR: Goosetail Rock (N=2) CB: Chelan Butte WMA (N=6) CF: Chelan Falls Park (N=3) AZ: Azwell (N=3)

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Table 4-7: Relative abundance1 of bird species documented by point count surveys within cover-types during the Rocky Reach RTE Wildlife Study. Exposed Rock/ Recreational Species Riparian2 Shrub-steppe Shrub-steppe Facility Great blue heron 0.06 Canada goose 0.10 0.18 0.44 Wood duck 0.04 Mallard 0.28 0.03 0.11 Common merganser 0.11 0.09 0.78 Osprey 0.01 0.03 Sharp-shinned hawk 0.01 Red-tailed hawk 0.01 American kestrel 0.04 0.03 Chukar 0.03 Ring-necked pheasant 0.03 California quail 0.19 0.10 0.44 Killdeer 0.08 0.52 Spotted sandpiper 0.12 0.11 Ring-billed gull 0.33 California gull 0.02 0.07 Rock dove 1.79 Mourning dove 0.43 0.14 0.30 White-throated swift 0.01 0.03 Black-chinned 0.01 0.04 hummingbird Calliope hummingbird 0.01 0.11 Belted kingfisher 0.11 0.03 0.15 Downy woodpecker 0.06 0.01 0.04 Northern flicker 0.37 0.07 0.03 0.19 Western wood-pewee 0.15 0.01 0.07 Say's phoebe 0.02 0.01 0.18 Western kingbird 0.02 0.16 0.11 Eastern kingbird 0.18 0.12 0.18 0.22 Tree swallow 0.34 0.03 0.03 1.07 Violet-green swallow 0.31 0.06 1.03 Northern rough-winged 0.13 swallow Cliff swallow 0.83 0.04 1.42 0.41 Barn swallow 0.13 0.01 0.04 Steller's jay 0.03 Black-billed magpie 0.12 0.14 0.27

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Exposed Rock/ Recreational Species Riparian2 Shrub-steppe Shrub-steppe Facility American crow 0.13 0.48 Black-capped chickadee 0.31 Chestnut-backed 0.01 chickadee Rock wren 0.03 0.55 Canyon wren 0.45 American dipper 0.01 American robin 0.38 0.17 0.12 0.63 Gray catbird 0.09 0.01 Cedar waxwing 0.22 0.01 0.15 0.30 Loggerhead shrike 0.25 European starling 0.67 0.61 1.55 2.04 Solitary vireo 0.01 Warbling vireo 0.02 0.04 Red-eyed vireo 0.01 Orange-crowned warbler 0.05 Yellow warbler 0.40 0.01 0.37 Yellow-rumped warbler 0.06 0.01 0.11 Common yellowthroat 0.01 Wilson's warbler 0.09 0.01 Yellow-breasted chat 0.04 0.03 Western tanager 0.03 0.03 0.04 Black-headed grosbeak 0.10 0.03 Lazuli bunting 0.16 0.30 Spotted towhee 0.28 0.06 Chipping sparrow 0.01 Lark sparrow 0.14 Song sparrow 0.24 0.01 White-crowned sparrow 0.03 0.17 Dark-eyed junco 0.04 Red-winged blackbird 0.69 0.09 0.30 Western meadowlark 0.01 0.68 Brewer's blackbird 0.31 0.43 0.15 1.26 Brown-headed cowbird 0.44 0.33 0.06 0.30 Northern oriole 0.42 0.28 0.12 0.30 Cassin's finch 0.07 0.01 0.39 House finch 0.04 0.06 0.11 American goldfinch 0.54 0.48 0.27 0.70 House sparrow 0.06 Total Number of Species 60 43 28 33

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Exposed Rock/ Recreational Species Riparian2 Shrub-steppe Shrub-steppe Facility Mean Number 6.0 3.4 4.1 5.8 Species/Survey Total Relative 9.8 5.4 9.8 12.2 Abundance 1 Mean number of species recorded per visit at each survey point. 2 Riparian, includes RD, RS, and PE (N=36 points) Shrub-steppe (N=23) Cliff/Exposed Rock (N=11) Park/Recreation Facility (N=9)

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Table 4-8:Habitat descriptions and locations of waterfowl survey points for the Rocky Reach RTE Wildlife Study. Site Location1 Habitat Description2 Common Waterbirds Observed Number 1 474.5 E Side channel on east side of Turtle Rock. Narrow RS with American coot, American widgeon, and Scaup PE habitat. spp. 2 478.5 W Calm cove with aquatic beds and some RS. American coot, American widgeon, and Ruddy duck. 3 482.3 E Calm cove with aquatic beds and some RS. Ruddy duck, Hooded merganser, and Western grebe. 4 483.6 W Protected cove at the Entiat River confluence. RS with PE. Mallard duck, Hooded merganser, and Horned grebe. 5 483.7 W Backwater eddy’s of Entiat River. Thick RS with some RD Common merganser, and Bald eagle. and PE. 6 484.3 W RS with some RD edge. Several coves with some PE along American coot, American widgeon, and Canada the shore. goose. 7 487.0 E Protected pool with some RS and PE habitats. Lawns are American coot, Lesser scaup, and Gadwall. also present here. 8 488.0 W Several small backwater areas protected by rocky islands American coot, American widgeon, and Gadwall. with some RS. 9 490.8 W Protected backwater with RS and PE. Sand and grassy areas American coot, American widgeon, and Horned still present. grebe. 10 492.5 W PE vegetation and aquatic beds with fringing RS. American widgeon, American coot, and Western grebe. 11 493.5 W Protected cove with RS, RD, and PE habitats. American widgeon, Mallard duck, and Ring-necked duck.

12 497.8 E Several protected coves with RD and some RS. Abundant Ring-necked duck, Mallard duck, and American PE also present. widgeon. 13 500.5 E Small protected cove with RD, RS and PE habitats. Mallard duck, Canada goose, and Ring-necked

1 Locations are River Miles (RM); E = East bank and W = West bank 2 Habitat codes are RS = Riparian Shrub, RD = Riparian Deciduous, PE = Palustrine Emergent, and US = Unconsolidated Shore.

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Site Location1 Habitat Description2 Common Waterbirds Observed Number duck. 14 502.8 W Sheltered area created by boat docks and swimming area American widgeon, Ring-necked duck, and with shoreline PE. Greater scaup. 15 503.5 W Protected areas around Chelan River confluence. Mostly RS Red-breasted and Hooded merganser, and with US. Common loon. 16 503.8 E Sheltered areas created by boat docks. Some RD but mostly American coot, Bufflehead, and Mallard duck. lawns. 17 506.5 W Sheltered cove with some RS. Sandy shore with pockets of Ring-necked duck, Greater scaup, and American PE. coot. 18 511.0 W Fringing riparian habitat with some emergent vegetation. Ring-necked duck, Common loon, and Pied- billed grebe. 19 513.9 W Dense RD, RS and PE habitat. Also, wetland complex with Mallard duck, Common loon, and Bald eagle. abundant PE. 20 515.2 W Cobble bar below Wells Dam. Sparse grasses and forbs. No water bird species documented.

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Table 4-9: Small mammal capture rates (captures per 100 trap nights) documented during the Rocky Reach RTE Wildlife Study. Species TR1 ER SCR SCS BB GF ULS Total Masked shrew 1.1 0.14 (Sorex cinereus) Vagrant shrew 3.1 5.4 0.3 0.2 0.1 1.38 (Sorex vagrans) Northern pocket 0.1 0.1 0.06 gopher (Thomomys talpoides) Great Basin pocket 4.3 1.7 2.0 1.27 mouse (Perognathus parvus) Bushy-tailed woodrat 0.9 0.12 (Neotoma cinerea) Deer mouse 0.2 1.6 4.1 3.1 7.5 12.2 1.1 4.25 (Peromyscus maniculatus) Western harvest 0.1 0.2 0.04 mouse (Reithrodontomys megalotis) Long-tailed vole 0.2 0.1 0.04 (Microtus longicaudus) Montane vole 0.6 0.8 2.5 0.2 0.4 0.65 (Microtus montanus) House mouse 0.1 0.02 (Mus musculus) Number of Species 25 5 6 3 5 3 10 Captured Total Capture Rate 0.8 6.7 12.2 8.0 7.9 15.4 3.2 8.0 1TR = Turtle Rock; ER = Entiat River; SCR = Sun Cove Riparian; SCS = Sun Cove Shrub-Steppe; BB = Beebe Bridge; GF = Gallagher Flats; ULS = Uplake Shrub-Steppe.

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Table 4-10: Small mammal capture rates (captures per 100 trap nights) by trap type documented during the Rocky Reach RTE Wildlife Study. Trap Type TR1 ER SCR SCS BB GF ULS Total Pitfall Capture 2.5 11.9 8.1 16.9 11.3 0.6 10.0 9.0 Rates Snap Trap 0.3 5.5 13.8 5.8 15.3 10.1 1.6 7.7 Capture Rates Live Trap 0.0 2.8 12.5 7.8 34.4 20.0 1.6 10.4 Capture Rates Havahart 0.0 0.0 4.2 0.0 16.7 0.0 0.0 3.1 Capture Rates Total Capture 0.8 6.7 12.3 8.0 15.3 7.9 3.3 8.0 Rate 1TR = Turtle Rock; ER = Entiat River; SCR = Sun Cove Riparian; SCS = Sun Cove Shrub-Steppe; BB = Beebe Bridge; GF = Gallagher Flats; ULS = Uplake Shrub-Steppe.

Table 4-11: Small mammal captures by feeding group documented during the Rocky Reach RTE Wildlife Study. Feeding Group TR1 ER SCR SCS BB GF ULS Total Omnivore 0.2 1.6 4.1 7.6 15.0 7.5 3.1 5.7 Capture Rate 25.0% 23.2% 33.6% 95% 97.4% 95.0% 96.9% 71.3% (#/100TN) and Percent of Total Capture Herbivore 0.6 1.1 2.7 0.1 0.4 0.2 0.0 0.7 Capture Rate 75.0% 15.9% 22.1% 1.3% 2.6% 2.5% 0.0% 8.7% (#/100TN) and Percent of Total Capture Insectivore 0.0 4.2 5.4 0.3 0.0 0.2 0.1 1.5 Capture Rate 0.0% 60.9% 44.3% 3.7% 0.0% 2.5% 3.1% 20.0% (#/100TN) and Percent of Total Capture Total Capture 0.8 6.9 12.2 8.0 15.4 7.9 3.2 8.0 Rate 1TR = Turtle Rock; ER = Entiat River; SCR = Sun Cove Riparian; SCS = Sun Cove Shrub-Steppe; BB = Beebe Bridge; GF = Gallagher Flats; ULS = Uplake Shrub-Steppe.

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Table 4-12: Mean values of habitat data collected at each small mammal trapping station during the Rocky Reach RTE Wildlife Study. Habitat Variable TR1 ER SCR SCS BB GF ULS Forb Cover (%) 8.2 5.6 15.1 14.6 9.6 17.3 14.8 Grass Cover (%) 53.2 36.1 32.4 44.9 42.3 50.7 58.3 Conifer Shrub 0.0 0.1 0.0 0.0 0.0 0.0 0.0 Cover (%) Deciduous Shrub 12.9 34.8 19.5 45.7 25.1 30.4 33.6 Cover (%) Conifer Tree 0.0 0.0 0.5 0.0 0.0 0.0 0.0 Cover (%) Deciduous Tree 8.7 53.3 45.1 11.5 51.1 24.3 0.0 Cover (%) Downed Woody 5.2 18.4 10.4 11.7 17.6 7.2 6.7 Debris Cover (%) Fallen Log Cover 1.2 16.1 1.73 0.2 3.2 1.3 0.0 (%) Litter Cover (%) 6.0 31.3 55.8 23.0 32.6 40.4 13.9 Amount of Bare 15.1 10.6 6.5 11.0 7.4 1.5 13.3 Ground (%) Rock/Boulder 28.0 0.0 0.7 0.8 2.2 0.2 0.2 Cover (%) 1TR = Turtle Rock; ER = Entiat River; SCR = Sun Cove Riparian; SCS = Sun Cove Shrub-Steppe; BB = Beebe Bridge; GF = Gallagher Flats; ULS = Uplake Shrub-Steppe.

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Table 4-13: Bat species captured during the Rocky Reach RTE Wildlife Study. Species TR1 ER SCR CF CB ULS Little brown myotis 1 (Myotis lucifugus) Western small-footed 42 1 myotis (Myotis ciliolabrum) Yuma myotis 1 (Myotis yumanensis) Pallid bat 11 (Antrozous pallidus) Number of Species111411 Capture Rate 0.85 0.50 0.62 0.00 0.50 0.24 (No. per net-hour) 1 TR = Turtle Rock; ER = Entiat River; SCR = Sun Cove Riparian; CF = Chelan Falls Park; CB = Chelan Butte Wildlife Management Area (Railroad Tunnel); ULS = Uplake Shrub-Steppe. 2 These individuals were captured by hand; none were caught in mist-nets.

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Table 4-14: Possible bat species detected by ultrasonic detection equipment during the Rocky Reach RTE Wildlife Study.

Species TR 1 ER DA SCR SCS GTR CB CF BB GF ULS AZ Little brown myotis XX X (Myotis lucifugus) Long-legged myotis XXX X X (Myotis volans) Yuma myotis XXX XXX (Myotis yumanensis) Big brown bat XXX XXX (Eptesicus fuscus) Townsend’s big-eared XX bat (Corynorhinus townsendii) California myotis XX X (Myotis Californicus) Western pipistrelle XXX (Pipistrellus hesperis) Pallid bat XX (Antrozous pallidus) 1TR = Turtle Rock; ER = Entiat River; DA = Daroga State Park; SCR = Sun Cove Riparian; SCS = Sun Cove Shrub- Steppe; GTR = Goosetail Rock; CB = Chelan Falls Park; CB = Chelan Butte Wildlife Management Area; BB = Beebe Bridge; GF = Gallagher Flats; ULS = Uplake Shrub-Steppe; AZ = Azwell Riparian.

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Table 4-15: Amphibians and reptiles found by all methods at Intensive Study Sites during the Rocky Reach RTE Wildlife Study. Species TR1 ER SCR SCS BB GF ULS Western toad X X X Great Basin spadefoot toad X X Pacific chorus frog X Painted turtle X Sagebrush lizard X X X Western fence lizard X X X Unidentified fence lizard X X Racer X X X X Gopher snake X X Wandering garter snake X Common garter snake X Unidentified garter snake X Western rattlesnake X

Table 4-16: Results of area-constrained searches for amphibians and reptiles at Intensive Study Sites during the Rocky Reach RTE Wildlife Study. Species TR ER SCR SCS BB GF ULS Western toad 2 6 Western fence lizard 3 6 9 Fence lizard spp. 3 2 Racer 1 2 2 1 Gopher snake 1 1 Search Effort (Person Hours) 4.37 4.63 4.50 12.00 3.83 6.83 2.34 Detection Rate Per Person Hour 0.69 1.73 1.33 0.25 2.08 1.61 0.00

Table 4-17: Pitfall trapping results for amphibians and reptiles at Intensive Study Sites during the Rocky Reach RTE Wildlife Study. Species TR ER SCR SCS BB GF ULS Western toad 521 Great Basin spadefoot toad 56 Pacific chorus frog 2 Trapping Effort (Trap Nights) 120 160 160 160 160 160 160 Capture Rate Per 100 Trap Nights 4.20 1.25 1.25 3.75 0.00 3.75 0.00 1TR = Turtle Rock; ER = Entiat River; SCR = Sun Cove Riparian; SCS = Sun Cove Shrub-Steppe; BB = Beebe Bridge; GF = Gallagher Flats; ULS = Uplake Shrub-Steppe.

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Table 4-18: Amphibians and reptiles found by all methods at Roving Study Sites during the Rocky Reach RTE Wildlife Study. Species EP1 DA CF CB AZ EU ED GU GD Western toad 1 Painted turtle 1 Gopher snake 1 Common garter snake 1 Search Effort (Person Hours) 0.96 1.27 2.00 2.00 3.00 1.25 1.25 0.92 0.23 Detection Rate Per Person 0.00 1.57 0.50 0.00 0.00 0.80 0.00 0.00 0.00 Hour 1EP = Entiat Park; DA = Daroga State Park; CF = Chelan Falls Park; CB = Chelan Butte Wildlife Management Area; AZ = Azwell; EU = Earthquake Point Upstream Island; ED = Earthquake Point Downstream Island; GU = Goosetail Rock Upstream; GD = Goosetail Rock Downstream.

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Table 4-19: Summary of dedicated amphibian surveys at Amphibian Sites (AS) for the Rocky Reach RTE Wildlife Study. (a) AS Location (River Mile) Visual Searches AS (b) AS Location (Descriptive) (Terrestrial) Dip Net Surveys Minnow Trapping Night Surveys 1 (a) 477.5 W 05/17/00 05/17/00: 20 sweeps 09/06/99 (b) 7.5 mi S. of Entiat 2 (a) 480.7 W 05/17/00 09/06/99 (b) 4.3 mi S. of Entiat 3 (a) 483.7 W 06/21/00 09/06/99 (b) Entiat River Confluence 4 (a) 503.6 W 05/17/00 05/17/00: 30 sweeps 06/12-06/13/00 09/06/99 (b) Chelan Falls Park 12 Traps 5 (a) 507.2 W 05/17/00 05/17/00: 15 sweeps 05/24/00 (b) Gallagher Flats 6 (a) 513.9 W 05/22/00 05/22/00: 50 sweeps 06/12-06/13/00 05/24/00 (b) Azwell 12 Traps 7 (a) 514.0 W 05/17/00, 05/22/00 05/17/00: 55 sweeps 05/24/00 (b) Azwell 05/22/00: 30 sweeps 8 (a) 477.6 E 06/9/00 06/09/00: 20 sweeps 09/06/99 (b) Estes Fruit Stand, 1.96 mi S. of junction SR 151/US Rte 2 9 (a) 479.7 E 05/16/00 05/16/00: 50 sweeps 09/06/00, 05/24/00 (b) 1.2 mi S. of junction SR 151/US Rte 2 10 (a) 479.75 E 05/16/00 05/16/00: 25 sweeps 09/06/00, 05/24/00 (b) 1.1 mi S. of junction SR 151/US Rte 2 11 (a) 479.8 E 05/16/00 05/16/00: 50 sweeps 05/24/00 (b) 1.0 mi S. of junction SR 151/US Rte 2 12 (a) 480.4 E 09/06/99, 06/13/00 (b) Orondo, 0.5 mi S. of junction SR 151/US Rte 2 13 (a) 484.2 E (Site was dry in 09/06/99

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(a) AS Location (River Mile) Visual Searches AS (b) AS Location (Descriptive) (Terrestrial) Dip Net Surveys Minnow Trapping Night Surveys (b) 1.9 mi N. of Orondo school 2000) 14 (a) 484.6 E 05/16/00 05/16/00 09/06/99, 05/24/00 (b) 2.3 mi S. N. of Orondo school 15 (a) 484.9 E 06/09/00 06/09/00 09/06/99, 05/24/00 (b) 2.3 mi S. of Daroga State Park entrance 16 (a) 485.6 E 05/16/00 05/16/00: 25 sweeps 09/06/99, 05/24/00 (b) 1.4 mi S. of Daroga State Park entrance 17 (a) 486.3 E 05/16/00 05/16/00: 60 sweeps 06/13-06/14/00 09/06/99, 05/24/00 (b) 0.8 mi S. of Daroga State Park 12 Traps entrance 18 (a) 486.6 E 05/16/00 05/16/00: 10 sweeps 05/24/00 (b) 0.4 mi S. of Daroga State Park entrance 19 (a) 491.9 E 05/24/00, 06/09/00 06/09/00: 50 sweeps 05/24/00-05/25/00 (b) 1.75 mi. WSW of Sun Cove Road 12 Traps 20 (a) 492.5 E 05/24/00 05/24/00: 20 sweeps 05/24/00 (b) 1.15 mi W. of Sun Cove Road 21 (a) 496.1 E 05/16/00 09/6/99, 05/24/00 (b) 1.68 mi. E. of Sun Cove Road 22 (a) 496.3 E 5/16/00 05/16/00: 60 sweeps 06/12-06/13/00 05/24/00 (b) 1.70 mi. E. of Sun Cove Road 4 Traps

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Table 4-20: Results of dedicated amphibian surveys at Amphibian Sites (AS) for the Rocky Reach RTE Wildlife Study AS (a) River Mile Location (a) Site Description (b) Descriptive Location (b) Summary of Survey Results 1 (a) 477.5 W (a) Pool to more than 2 m. deep and permanently flooded; surrounded by mostly steep slopes of shrub-steppe vegetation. Only two small (b) 7.5 mi S. of Entiat patches of emergent vegetation (cattail). (b) Fish present. In 20 dip-net sweeps at shallow end of pool, we found no amphibian larvae. A splash heard during survey could have been a frog. Heard a few chorus frogs 9/06/99, but no detections on the night of 6/13/00. Site probably not suitable breeding habitat for native amphibians. Incidental observations: unidentified lizard. 2 (a) 480.7 W (a) Pool more than 3 m. deep; water very clear, bottom rocky, with very little aquatic vegetation; (b) 4.3 mi S. of Entiat and no emergent vegetation. (b) Fish present. Did not dip-net. Site not suitable breeding habitat for amphibians. Incidental observations: Bullock’s oriole, and chipmunk. 3 (a) 483.7 W (a) Perennial tributary with complex channel and wooded riparian corridor. (b) Entiat River (b) Conducted intensive visual searches as well as pitfall trapping. Found 2 adult Pacific chorus frog. Amphibians here might breed in quiet flood water channels of Entiat River after water recedes. 4 (a) 503.6 W (a) Pond of recent origin (since 1990), more than 2 m. deep, and permanently flooded. Very little (b) Chelan Falls Park emergent vegetation. (b) In 30 dip-net sweeps within the shallow edge, we found no amphibian larvae. No amphibians found in intensive searches. No detections on night of 5/24/00 5 (a) 507.2 W (a) Two very small pools in tire-rutted road, maximum depth 30 cm. (b) Gallagher Flats (b) Fish not present. Great Basin spadefoot toad larvae abundant along with mosquito larvae. Caught adult spadefoot toads in pitfalls. No detections on the night of 5/24/00. 6 (a) 513.9 W (a) Pool less than 2 m.; connected to the river by a channel. Pool was dry in September 2000. (b) Azwell Emergent edge is mostly reed canarygrass. (b) Fish present, but evidently just a few large carp stranded by flood water. In 50 dip-net sweeps, we found no amphibian larvae. Heard large number of Pacific chorus frogs on night of 5/24/00. 7 (a) 514.0 W (a) Pool is shallow (40 cm.) on May 17 and dries seasonally; almost entirely filled with reed (b) Azwell canarygrass. (b) Fish present, but evidently just a few large carp stranded by receding flood water. In 55 dip-net sweeps, we found 4 Great Basin spadefoot toad larvae; invertebrates numerous especially water boatmen, midges, snails. Heard large number of Pacific chorus frogs on night of 5/24/00.

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AS (a) River Mile Location (a) Site Description (b) Descriptive Location (b) Summary of Survey Results 8 (a) 477.6 E (a) Pool is more than 2 m. deep, and permanently flooded. Narrow emergent fringe of (b) Estes Fruit Stand, 1.96 mi S of cattail, with aquatic weed beds and floating algal mats. junction SR 151/US Route 2 (b) Fish present, including sunfish. In 20 dip-net sweeps, we found no amphibian larvae. No detections on the night of 9/6/99. 9 (a) 479.7 E (a) Pool is about 2 m. deep, and permanently flooded. Emergent edge, surrounded by steep (b) 1.2 mi S. of junction SR rock on three sides. Most of the pond has aquatic weeds to the surface. 151/US Route 2 (b) Fish present. In 50 dip-net sweeps, we found no amphibian larvae. No detections on the night of 9/6/99, but heard Pacific chorus frogs on the night of 5/24/00. Incidental observations: pair of Bullock’s orioles. 10 (a) 479.75 E (a) Most of the wetland is choked with cattail. Three small pools, the largest less than 1 m2, which (b) 1.1 mi S. of junction SR probably dry by late summer. Duckweed present, but no rooted aquatic plants. 151/US Route 2 (b) No fish. The site is rich in invertebrates. In 25 dip-net sweeps, we found 63 long-toed salamander larvae (the smaller cohort recently hatched on May 16) and 16 Pacific chorus frog larvae. No detections on the night of 5/24/00. Incidental observations: immature racer. 11 (a) 479.8 E (a) Pool is more than 2 m. deep, and permanently flooded. Water is turbid. Narrow emergent edge (b) 1.0 mi S. of junction SR (cattail) and a broken band of willows. 151/US Route 2 (b) Fish present. Few invertebrates (mostly snails). In 50 dip-net sweeps, we found no amphibian larvae. No detections on the night of 5/24/00. Incidental observations: western painted turtle, 2 pairs red-winged blackbird, eastern kingbird, and Nuttall’s cottontail. 12 (a) 480.4 E (a) Deep pool connected to river and surrounded by residential development. (b) Orondo, 0.5 mi S. of junction (b) Did not conduct visual or dip-net survey because of inaccessible private property and the SR 151/US Route 2 improbability of finding amphibians at this site. Fish undoubtedly present. No detections the night of 5/24/00 or 6/13/00. 13 (a) 484.2 E (a) Pool is more than 4 m. deep, and permanently flooded. Shoreline mostly rocky. Aquatic beds (b) 1.9 mi N. of Orondo School dense near edges. Only a small patch of bulrush. (b) Fish numerous. Searched water’s edge, seeing only fish. Heard a few Pacific chorus frogs on the night of 9/6/99. Incidental observations: dead western toad in adjacent orchard. 14 (a) 484.6 E (a) (b) 2.3 mi N. of Orondo School (b) No detections on the night of 5/24/00 or 9/6/99.

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AS (a) River Mile Location (a) Site Description (b) Descriptive Location (b) Summary of Survey Results 15 (a) 484.9 E (a) Pool more than 2 m. deep, and permanently flooded. Large area of open water; aquatic weed (b) 2.3 mi S. of Daroga St. Park beds present, and bulrush along half of shoreline. (b) Fish present. No detections on the night of 5/24/00, but heard a few Pacific chorus frogs on the night of 9/6/99. 16 (a) 485.6 E (a) Wetland is almost entirely choked with cattail (some sedge and reed canarygrass). Two small (b) 1.4 mi S. of Daroga St. Park areas of open water (about 30 cm. of water over mud more than 1 m. deep) (b) Fish not found. In 25 dip-net sweeps, we found no amphibian larvae; invertebrates (especially dragonflies and snails) abundant. No detections on the night of 5/24/00, but heard a few Pacific chorus frogs on the night of 9/6/99. 17 (a) 486.3 E (a) Pool is about 2 m. deep, and permanently flooded. Aquatic weed beds present, with emergent (b) 0.8 mi S. of Daroga St. Park cattail along about 30 percent of shore. (b) Fish numerous. In 50 dip-net sweeps, we found no amphibian larvae; invertebrates scarce. No detections on the night of 5/24/00, but we heard a few Pacific chorus frogs on the night of 9/6/99. 18 (a) 486.6 E (a) Pool is 3-4 m. deep, and permanently flooded; little emergent vegetation. Eutrophic (b) 0.4 mi S. of Daroga St. Park conditions (algal bloom). Artesian well discharging water vigorously (pool over-filled recently). (b) Fish present. In 10 dip-net sweeps, we found no amphibian larvae; snails numerous. No detections on the night of 5/24/00. 19 (a) 491.9 E (a) Pool mostly less than 1 m. deep, but apparently permanently flooded; bottom sandy to silty. (b) Sun Cove area; 10 mi W. of US Dense aquatic beds dominated by milfoil. Cattail stands adjacent and on fringe of pool. 2 (b) Fish not found. In 50 dip-net sweeps, we found 236 western toad larvae. Incidental observation: painted turtle. 20 (a) 492.5 E (a) Emergent wetlands (cattail) bordered by willows, all shallow and temporarily flooded. On (b) Sun Cove area; 11.8 mi W. of 5/24/00, 4 of the 5 pools still held water (but less than 15 cm. deep). US 2 (b) In 20 dip-net sweeps, we found no amphibian larvae; invertebrates scarce. No detections on the night of 5/24/00. Captured Great Basin spadefoot toads in pitfalls and observed a western toad in one of the pools on an earlier date. 21 (a) 496.1 E (a) Pool is more than 4 m. deep, and permanently flooded; no emergent vegetation. Water clear and (b) 1.68 mi. E. of Sun Cove Road cool (pool connected by culvert to river). (b) Fish present. Did not dip-net. No detections on the night of 5/24/00 or 9/6/99.

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AS (a) River Mile Location (a) Site Description (b) Descriptive Location (b) Summary of Survey Results 22 (a) 496.3 E (a) Pool 0.8 to 1.6 m deep, probably temporarily flooded. Much of the pool is filled with emergent (b) 1.70 mi. E. of Sun Cove Road cattail and reed canarygrass. (b) Fish not found. In 60 dip-net sweeps, we found no amphibian larvae; invertebrates rich and diverse. No detections on the night of 5/24/00.

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Table 4-21: State and Federally listed and monitored wildlife species known or possible from the vicinity of the Rocky Reach Project. Common Name Scientific Name Status Observed during Study Common loon Gavia immer State Candidate Yes Great blue heron Ardea herodias State Monitor Yes Osprey Pandion haliaetus State Monitor Yes Bald eagle Haliaeetus leucocephalus State/Federal Threatened Yes Northern goshawk Accipiter gentilis State Candidate, Federal No SOC Swainson’s hawk Buteo swainsoni State Monitor No Golden eagle Aquila chrysaetos State Candidate Yes Peregrine falcon Falco peregrinus State Endangered, No Federal SOC Prairie falcon Falco mexicanus State Monitor No Burrowing owl Speotyto cunicularia State Candidate, No Federal SOC Sage grouse Centrocercus urophasianus State Threatened, No Federal SOC Sharp-tailed grouse Tympanuchus phasianellus State Threatened, No Federal SOC Vaux’s swift Chaetura vauxi State Candidate No Lewis’ woodpecker Melanerpes lewis State Candidate No White-headed Picoides albolarvatus State Candidate No woodpecker Pileated woodpecker Dryocopus pileatus State Candidate No Olive-sided flycatcher Contopus borealis Federal SOC No Willow flycatcher Empidonax traillii Federal SOC No Loggerhead shrike Lanius ludovicianus State Candidate, Yes Federal SOC Sage thrasher Oreoscoptes montanus State Candidate No Sage sparrow Amphispiza belli State Candidate No Merriam’s shrew Sorex merriami State Candidate No Colonial roosting bats Various species State Monitor, Yes Federal SOC Washington ground Spermophilus washingtoni State Candidate, No squirrel Federal Candidate Western gray squirrel Sciurus griseus State Threatened, No Federal SOC Sagebrush vole Lemmiscus curtatus State Monitor No California bighorn sheep Ovis canadensis Federal SOC No Sagebrush lizard Sceloporus graciosus Federal SOC Yes Night snake Hypsiglena torquata State Candidate No Sharptail snake Contia tenuis State Candidate No Western toad Bufo boreas State Candidate, Yes Federal SOC Columbia spotted frog Rana luteiventris State Candidate, No Federal SOC

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SECTION 5: CONCLUSIONS

5.1 Wildlife Habitat The condition and extent of wildlife habitats within a given region typically reflect a complex interaction of many factors. These include the occurrence of human activities, such as residential development, agricultural use, recreational use, and hydroelectric project operation. Within the Rocky Reach study area, human development and the clearing of native plant communities for agricultural use have resulted in a highly fragmented landscape with relatively few large tracts of native plant communities and many small habitat patches. Habitat fragmentation affects the character of small patches, which are predominantly comprised of “edge” and are subjected to the invasion of plants and animals from adjacent habitats. Furthermore, many of these habitats have been disturbed by grazing, recreational activities, irrigation runoff, or fire. Physical and geologic factors, such as dominant substrate type, topography, aspect, and elevation also influence wildlife habitats, but these factors were relatively consistent within the study area and mainly influenced the extent of riparian habitats.

Approximately 57 percent of the study area is comprised of Disturbed/Developed/Modified cover- types. Of all cover-types within the study area orchards occupy the largest area (25.2 percent) and Residential/Industrial the third largest area (15.6 percent). The Residential/Industrial cover-type increased more than any cover-type from 1991 to 1999 (approximately 230 acres), followed by the Recreational cover-type (increase of approximately 59 acres). Residential and industrial development results in the conversion and permanent loss of native wildlife habitats.

The Shrub-steppe cover-type is the predominant native terrestrial habitat in the study area (22.3 percent), but this cover-type decreased more than any other cover-type from 1991 to 1999 (approximately 204 acres). Most of this change was associated with new residential development and the expansion of existing orchards. Much of the Shrub-steppe cover-type consists of small patches fragmented by orchards, residential developments, recreational facilities, and roads. Only north of Beebe Bridge is there a large unbroken expanse of shrub-steppe habitat. Wildlife species associated with shrub-steppe habitats in Washington are diverse and include several species that are considered obligate to this unique habitat (Dobler et al. 1996). Eleven of the 40 RTE wildlife species potentially occurring within the Project vicinity are closely associated with shrub-steppe habitats. Steppe zones are considered of highest conservation priority by the Washington State Gap Analysis Project (Cassidy et al. 1997) due to the high conversion rate by human activities.

With few exceptions, riparian and shoreline wetland habitats observed in the study area are small, isolated, and distinctly linear. Collectively these habitats constitute a small portion of all habitats in the area (9.2 percent), but contribute disproportionately to the biodiversity of the region. Approximately 85 percent of Washington’s wildlife species use riparian habitats at some time during their life cycle (Knutson and Naef 1997). Some of the reasons that riparian and wetland habitats are so important to wildlife include: 1) the presence of water for drinking, bathing, or reproduction (amphibians); 2) high vegetative biomass; 3) high structural diversity; 4) the presence of edge habitats; 5) the presence of cool, shaded, and humid microclimates; and 6) readily usable corridors

Draft Study Report Reach Project No. 2145 November 9, 2000 Page 5-1 SS/2493 RTE Wildlife & Cover-type Mapping for migration and travel (Thomas 1979). Riparian habitats within arid or semi-arid environments are particularly distinctive, and support species assemblages that could not occur otherwise.

Riparian cover-types collectively decreased by approximately 20 acres (approximately 5.6 percent) within the study area from 1991 to 1999. Approximately seven acres of this decrease was associated with the development of new recreational facilities. The majority of the loss of riparian habitats occurred in the Riparian Grassland cover-type; however, this net loss is largely attributable to the reclassification of lawn areas, previously mapped as Riparian Grassland, to Residential/Industrial or other non-riparian cover-types. Riparian Deciduous cover-types decreased by approximately 25 acres and Riparian Shrub cover-types increased by approximately 31 acres; thus, the combined area of these cover-types has remained almost unchanged. It is unclear whether this reflects changes in vegetation or merely differences in the interpretation of field features. Possibly, some areas previously classified as Riparian Deciduous by Ebasco Environmental (1991) were assigned to Riparian Shrub in the current study. Because riparian cover-types typically occur in areas immediately adjacent to the project reservoir, the relatively small changes documented during this study suggest that riparian habitats within the study area are stable and have adapted to the water level fluctuations associated with Project operation. Some riparian habitats within the study area may be influenced by irrigation runoff from adjacent orchards. This supplemental ground water may promote riparian development in areas that would otherwise be too dry. Furthermore, some existing riparian vegetation may be more lush because of this supplemental water source.

Although some of the cover-types mapped within the study area constitute a very small proportion of the available wildlife habitat, they may nonetheless represent unique and important wildlife habitats. For example, the Exposed Rock/Shrub-steppe cover-type included some cliffs, which may serve as nesting habitat for several species of raptors and swallows and roosting habitat for several bat species. The area occupied by this cover-type changed little from 1991 to 1999 and was located primarily on Turtle Rock and in the adjacent Chelan Butte Wildlife Management Area. Similarly, the series of Palustrine Open Water ponds, Lacustrine Open Water ponds, and emergent wetlands impounded by the roadways paralleling Lake Entiat may constitute a major portion of the available amphibian breeding habitat within the study area, along with a few other scattered sites (Sun Cove, Gallagher Flats, and Azwell). Amphibian breeding was documented in several of these pools. In some cases these pools also had associated emergent wetlands which provided suitable habitats for species such as red-winged blackbird and muskrat. Snags and large trees with nest cavities are also important wildlife habitats. Snags were generally not abundant in the study area and were most often found in Riparian Deciduous cover-types. Live black cottonwood and Lombardy poplar with nest cavities were relatively abundant in both Riparian Deciduous and Recreational cover-types.

Human activities other than development or clearing may also influence the extent and condition of wildlife habitats. There was evidence of fill, trash dumping, off-road vehicle use, and non- designated camping and gathering at several of the sites surveyed. Fill and ground disturbance may result in loss of wetlands, loss of native vegetation, and the invasion by non-native plant species. Furthermore, uncontrolled camping, gathering, or vehicular traffic may result in the trampling or cutting of vegetation and disturbance of wildlife. Sites with evidence of significant disturbance, such as the Beebe Bridge Riparian site, had a high prevalence of non-native plant species, which typically have wildlife habitat values inferior to native plant species. Siberian elm, which is dominant at the

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Beebe Bridge site and abundant at several others, is considered to provide few benefits to native wildlife species (Grant 1997). This species is likely unattractive to nesting by large birds of prey because of its finely dissected branching pattern.

5.2 Wildlife Communities The wildlife communities associated with habitats within the study area are influenced by a complex interaction of factors including the size of habitat patches, interspersion of habitats, geographic isolation of habitats, vegetative structural diversity, and level of disturbance. These factors affect species groups to varying degrees depending upon characteristics such as mobility, size, and habitat specificity. For example, birds are able to disperse over long distances and are less likely to be affected by separation between habitats. Conversely, small mammal, amphibian, and reptile species have limited dispersal capabilities, and therefore a relatively small area of inhospitable habitat may act as a dispersal barrier.

The landscape within the study area is highly fragmented with relatively few large tracts of native plant communities and many small habitat patches. Many of these habitat patches are also geographically isolated from other similar habitats by human altered habitats; making them essentially “islands” of wildlife habitat in a “sea” of human developments and orchards. Given this setting, the theory of island biogeography (MacArthur and Wilson 1967) may be applicable in explaining some of the observed wildlife species richness and abundance values at the sites studied. Island biogeography incorporates elements of both the size of the habitats and geographic isolation. Island biogeography theory maintains that larger islands should have more species, presumably due to sufficient resources to support larger populations, more diverse habitats, and lower rates of species loss (Brewer 1979). Species richness is also related to geographic isolation; islands far from the mainland tend to have fewer species than nearer islands because rates of colonization are lower. Within terrestrial landscapes, the types of habitats surrounding a habitat “island” are also important. For example, a habitat “island” surrounded by human developments is much more isolated than a habitat “island” surrounded by other native plant communities. The relative ease or difficulty by which wildlife species may traverse the habitats surrounding a habitat “island” is referred to as edge permeability (McComb 1999) or resistance to flow (Wiens 1989, Freemark and Collins 1992).

The number of species and individuals that occur within a given habitat is often directly related to habitat area. Small patches of habitat contain fewer resources than larger patches of habitat, and so are capable of supporting fewer individuals of fewer species. In addition, many wildlife species establish territories and exclude other individuals of the same species (intraspecific competition); thus, small patches of habitat will only support a small population, possibly even a single pair. Small populations are inherently vulnerable to extirpation. Small populations in a confined area are especially susceptible to extirpation by disturbance, such as habitat alteration or fire. Furthermore, if a population is extirpated in a small isolated habitat, the potential for recolonization is low. Larger habitats generally have larger populations, thus reducing the likelihood that a species will be extirpated by a disturbance or stochastic event. The relationship of habitat area to species richness was apparent in the results of the avian surveys, at least for some habitat types. The Entiat River and Beebe Bridge Riparian sites contained the largest blocks of riparian habitats and had the highest and third highest number of breeding bird species observed, respectively. The Entiat River site is also part of a larger riparian corridor along the length of the river, which provides an even larger area to

Draft Study Report Reach Project No. 2145 November 9, 2000 Page 5-3 SS/2493 RTE Wildlife & Cover-type Mapping support wildlife populations and allows wildlife species to travel and disperse over a large area. In contrast, the unnamed islands downstream of the Entiat River were the smallest riparian habitat patches sampled and had the fewest bird species observed and the lowest relative abundance. The size of a habitat patch may also influence the suitability for individual species that are area sensitive. For example, the Uplake Shrub-steppe site was the largest patch of shrub-steppe habitat surveyed and was the only site where loggerhead shrikes were documented during breeding bird surveys. Structurally this site appeared similar to the smaller shrub-steppe patches surveyed, suggesting that the size of shrub-steppe habitat patches or interrelated disturbance factors are important to loggerhead shrikes. This species establishes relatively large breeding territories in arid environments (10 to 16 hectares) which may limit the suitability of small habitat patches (Bartgis 1992). Sage sparrow is a shrub-steppe obligate species (Dobler et al. 1996) that also requires relatively large undisturbed patches of shrub-steppe habitat in eastern Washington (not found in patches smaller than 130 hectares) (Paige 1999).

Geographic isolation is most pronounced within developed areas and for small riparian habitats surrounded by arid shrub-steppe habitats. The potential for wildlife species to colonize isolated patches of habitat is most important in explaining the distribution of small mammal, amphibian, and reptile species, which have limited dispersal capabilities. It is unlikely that a habitat-specific small mammal, amphibian, or reptile would easily disperse across a large expanse of developed or inhospitable cover-types (low edge permeability). This would be particularly difficult for riparian- dependant species given the arid nature of the region. Recolonization of the burned portions of Turtle Rock by small mammals and reptiles may take longer than similar mainland habitats due to the high degree of isolation of this island. Birds are able to disperse over long distances and are less likely to be affected by separation between habitats (high edge permeability). This may explain the relatively high measures of bird species richness and abundance, but low small mammal species richness documented at the highly disturbed Beebe Bridge Riparian site.

In addition to the landscape-level factors previously discussed, site specific characteristics, such as vegetative structural diversity and disturbance may affect wildlife communities. Riparian areas had the most diverse and well-developed vegetative structure of the habitats surveyed. These habitats typically consist of interspersed patches of Riparian Deciduous, Riparian Shrub, and Palustrine Emergent cover-types. A structurally diverse area affords breeding, cover, and foraging habitat for a wide variety of wildlife species. Riparian habitats had the highest mean number of breeding bird species observed and the second highest number of small mammal species captured. In terms of tree structure characteristics, the Recreational cover-type was similar to Riparian Deciduous and had the second highest mean number of bird species observed and the highest bird species relative abundance. However, the high relative abundance documented at recreational facilities is due primarily to high numbers of European starlings, Brewer’s blackbirds, and tree swallows, which are very tolerant of and may be aided by human activities. Furthermore, recreational facilities typically did not exhibit well-developed shrub layers. Herbaceous vegetation was also not diverse, consisting almost entirely of maintained lawns, which have limited wildlife value.

Areas with an interspersion of several different habitat types are also likely to support a more diverse wildlife community. For example, the Sun Cove Shrub-steppe site consisted of two distinct types of shrub-steppe habitat interspersed with patches of Riparian Deciduous, Riparian Shrub, and

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Palustrine Emergent habitats and it had the highest number of small mammal species captured. This site has a unique juxtaposition of habitats and supports both shrub-steppe and riparian wildlife species. Similarly, Gallagher Flats consisted primarily of Forbland and Shrub-steppe cover-types, but had interspersed patches of Riparian Deciduous, Riparian Shrub, and Palustrine Emergent cover- types that resulted in the highest small mammal relative abundance. The Sun Cove Shrub-steppe site is at risk to encroaching residential development. Gallagher Flats appears to be subject to on- going human disturbance and disrupted hydrology. This site is currently managed for public hunting by WDFW.

Human disturbance, including fill, trash dumping, vehicular traffic, and non-designated camping, was evident at several of the sites surveyed and may influence the suitability of wildlife habitats. The landscape and vegetation within the Beebe Bridge Riparian site is highly disturbed with evidence of land alteration and a high prevalence of non-native species. Fill has been dumped in some areas of this site, which has probably resulted in loss of wetlands, loss of native vegetation, and the invasion of non-native plant species. Both of the dominant tree species of this site, Siberian elm and Lombardy poplar, are non-native species. These trees are potentially not as valuable to wildlife as are native tree species. Himalayan blackberry, one of the dominant shrubs of this site, is also non- native. Although many wildlife species may use Himalayan blackberry for food and cover, this shrub often forms extremely dense thickets that displace native vegetation. Beebe Bridge Riparian had a low diversity of small mammals (only three species and 95 percent of captures were deer mice) which is likely due to this high level of disturbance. Some small mammal species are very sensitive to disturbance of ground cover components. In contrast, deer mice are habitat generalists and are often among the first species to colonize disturbed sites (Wirtz et al. 1988). However, species groups may differ in their sensitivity to disturbance. For example, despite the high level of disturbance, the Beebe Bridge Riparian site had some of highest measures of bird species richness and abundance of the Intensive Study sites. This may be because bird species select habitats based on habitat structure rather than plant species composition; structurally this site was similar to other less disturbed riparian sites. Portions of Turtle Rock were burned in 1999, which may explain the low small mammal relative abundance and species richness documented at this site. The Entiat River and Sun Cove Riparian sites are relatively undisturbed and have well-developed vegetative structure with a high prevalence of native plant species. These sites had the highest relative abundance of shrews and voles of the sites surveyed and relatively diverse bird communities.

In conclusion, the extent, structure, and suitability of wildlife habitats within the Rocky Reach study area are influenced by current human activities, past land-use practices, and physical landform characteristics. Each of the sites studied has unique characteristics resulting from the interactions of these factors. Some areas have limited wildlife habitat due to human factors, such as development, modification, and disturbance. Others areas have suitable wildlife habitat, but these may be isolated or insufficient to support persistent populations of some wildlife species. Large, relatively undisturbed habitat patches that are not isolated by human altered habitats provide the highest quality wildlife habitat within the study area. Examples include Turtle Rock, the Entiat River, Sun Cove Shrub-steppe, and Uplake Shrub-steppe. With the exception of the Uplake Shrub- steppe site these areas are not privately owned and receive some protection from disturbance. However, the Sun Cove Shrub-steppe site is being encroached upon by the Sun Cove residential development. Several smaller privately owned sites have unique habitat features, such as the pools

Draft Study Report Reach Project No. 2145 November 9, 2000 Page 5-5 SS/2493 RTE Wildlife & Cover-type Mapping at Sun Cove Riparian and Azwell Riparian. The most productive habitats documented had diverse vegetative structural characteristics (riparian habitats) or an interspersion of several cover-types (Sun Cove Shrub-steppe). Several of the sites surveyed are currently being encroached upon by human developments or exhibited signs of human disturbance, which may diminish, fragment, or alter available habitats resulting in reduced habitat suitability. Based on the results of this study, we believe that other researchers could successfully predict the habitat suitability of wildlife habitats within the study area using the factors discussed above without conducting intensive field surveys.

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SECTION 6: REFERENCES

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APPENDIX A: COVER-TYPE MAPS FOR THE ROCKY REACH PROJECT AREA RTE Wildlife & Cover-type Mapping

APPENDIX B: COVER-TYPE MAPS FOR THE SEVEN INTENSIVE STUDY SITES RTE Wildlife & Cover-type Mapping

APPENDIX C: WILDLIFE SPECIES THAT POTENTIALLY OCCUR IN THE ROCKY REACH STUDY AREA AND THOSE DOCUMENTED DURING THE RTE WILDLIFE STUDY