Arthur Rylah Institute Technical Paper Series
Arthur Rylah Institute for Environmental Research Arthur Rylah Institute for Environmental Research Technical Series Report No. 150
Post-fire recovery of priority populations of threatened flora in north-east Victoria after the 2003 bushfires
F. Coates, M. Taranto, A. Trumbull-Ward and A. Browne
October 2004 Published by the Victorian Government Department of Sustainability and Environment Melbourne, [insert month] 2004 © The State of Victoria Department of Sustainability and Environment 2004 This publication is copyright. No part may be reproduced by any process except in accordance with the provisions of the Copyright Act 1968. Authorised by the Victorian Government, 8 Nicholson Street, East Melbourne. Printed by [insert printer’s name and address] ISBN [insert number] For more information contact the DSE Customer Service Centre 136 186
Disclaimer This publication may be of assistance to you but the State of Victoria and its employees do not guarantee that the publication is without flaw of any kind or is wholly appropriate for your particular purposes and therefore disclaims all liability for any error, loss or other consequence which may arise from you relying on any information in this publication. Citation Coates, F., Taranto, M., Trumbull-Ward, A. and Browne, A. (2004) Post-fire recovery of priority populations of threatened flora in north-east Victoria after the 2003 bushfires. Arthur Rylah Institute for Environmental Research Technical Report No. 150. Department of Sustainability and Environment, Victoria, Melbourne.
Front cover: Banksia canei, Brumby Point, Alpine National Park. Photo: Obe Carter. Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Contents
Executive Summary ...... V
Introduction...... 1
Methods ...... 3
Results ...... 10
Discussion...... 27
Recommendations ...... 34
Acknowledgments...... 36
References...... 37
Appendix 1. Summary of population records for post-fire threatened flora surveys, January – April 2004...... 39
Appendix 2. Fire response characteristics for post-fire threatened flora surveys, January – April 2004...... 45
Appendix 3. Summary of actual and potential threats for populations recorded during post-fire threatened flora surveys, January – April 2004...... 47
Appendix 4. Grevillea alpivaga monitoring data...... 53
Appendix 5. Eucalyptus mitchelliana monitoring data...... 56
Appendix 6. Deyeuxia pungens monitoring data...... 57
Appendix 7. Myoporum floribundum monitoring data...... 60
Appendix 8. Thesium australe monitoring data...... 63
Appendix 9. Barbarea grayi monitoring data...... 65
Appendix 10. Lobelia gelida monitoring data...... 66
Appendix 11. Acacia nanopravissima monitoring data...... 69
III Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
List of Tables
Table 1. Vital attributes and their codes...... 6
Table 2: Example of a life table and hypothetical data...... 8
Table 3. Species Extinct in Victoria: pre-fire conservation status, regenerative response and post-fire conservation status...... 13
Table 4. Species Endangered in Victoria: pre-fire conservation status, regenerative response, post-fire conservation status and the proportion of re-located populations in the study area that were selected for surveying...... 14
Table 5. Species Vulnerable in Victoria: pre-fire conservation status, regenerative response post-fire conservation status and the proportion of re-located populations in the study area that were selected for surveying...... 16
Table 6. Species Rare in Victoria: pre-fire conservation status, regenerative response and post-fire conservation status...... 17
Table 7. G. alpivaga seedling densities...... 21
Table 8. E. mitchelliana seedling densities...... 22
Table 9. D. pungens seedling and resprout densities ...... 22
Table 10. M. floribundum seedling and resprout densities...... 23
Table 11. T. australe resprout densities densities ...... 23
Table 12. Number of points with and without L. gelida and percent cover of post-fire regeneration...... 24
Table 13. Number of resprouting A. nanopravissima plants...... 24
Table 14. Area of occupancy and/or number of individuals for eight burnt populations of E. eichleri...... 25
Table 15. No of resprouting D. nitida plants, resprout number and length...... 26
IV Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Executive Summary
Forty-four species of threatened plants were identified as ‘possibly at risk’ following the bushfires that burnt 1.1 million hectares of public and private land in 2003 (Parks Victoria 2003). The post-fire response of most of these species had not been previously documented. Surveys were conducted for 43 of these species to relocate at least some of their populations within the boundary of the fire-affected area and to assess whether - 1. the target species were burnt and regenerating, 2. were burnt and not yet regenerating but were likely to do so, 3. were burnt and unlikely to regenerate or 4. had not been burnt. Existing population records were prioritised for survey and fieldwork, which was conducted from January to April 2004. Information recorded during the surveys included population size, habitat variables, an estimate of the local fire severity, fire response traits, threats present at the site and management requirements. Information was collected only at burnt sites. By the close of the survey period, 181 populations had been found, including populations that had not been previously recorded. 126 of these populations had been burnt. 17 additional rare or threatened species were found. Twenty-two vascular plant species showed good regeneration at all sites inspected. Seven species were not, or mostly not, burnt across their range within the fire-affected area. Four vascular species and two non-vascular species showed poor regeneration or had not regenerated where burnt. An additional four species were not relocated, but all except one are highly likely to be extant, with no records found for the remaining species. Two species were subject to recovery plan implementation and were not surveyed. Two species are considered to have become extinct pre-fire. Seven species with known locations require further survey to clarify their status. Fire response characters were recorded for 28 species. The majority (14) of species with burnt populations were obligate resprouters with no persistent seed bank. Eight species had the ability to resprout and regenerate from a persistent seed bank. Four species were obligate seed recruiters from a persistent seed bank with no ability to resprout. Two species were short-lived annuals. Threats were recorded in 24% of populations, however most of these threats were relatively minor. Pest plant (environmental weed) management should be given the highest priority. Strategies for pest animal management should be implemented. Rapid monitoring methods were devised to determine the rate of post-fire recovery over time and tested for nine species. These represented the range of functional traits present within the range of species surveyed. Most populations of most species are recovering successfully after the fires, with many having benefited from the stimulus to regeneration. Nevertheless, fire management planning that considers rare and threatened species will be required in the future. At present, little is known of the life histories or regenerative strategies of any of the species targeted during this survey. The fires have presented a unique opportunity to acquire information on the population biology and dynamics of threatened flora and their responses to fire. Species monitoring should continue over the next three to five years.
V Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Introduction
Forty-four threatened plant species were identified as ‘possibly at risk’ following the bushfires that burnt 1.1 million hectares of public and private land in eastern and north- eastern Victoria in 2003 (Parks Victoria and Department of Sustainability and Environment 2003). Thirty-two of these species are listed under the Commonwealth Environment Protection and Biodiversity Conservation Act 1999 as nationally threatened, including sixteen species also listed under the Flora and Fauna Guarantee Act 1988 as threatened in Victoria. The post-fire response of the majority of these species had not been previously documented.
Surveys were conducted for 43 species to relocate some of the populations within the boundary of the fire-affected area and to assess whether the target species were -
1. burnt and regenerating,
2. burnt and not yet regenerating but likely to do so,
3. burnt and unlikely to regenerate, or
4. had not been burnt.
A unique opportunity also existed to compile data on functional traits that characterise plant responses to fire, for inclusion in the Statewide and national fire response databases which underpin ecological fire management protocols currently being developed by DSE and Parks Victoria (Fire Ecology Working Group 2004).
Further opportunity also existed to monitor the post-fire recovery of species. Owing to the scale and extent of the fires and the high number of species and populations affected, detailed monitoring was constrained by time, budget and staff availability. The project aimed to develop monitoring protocols that addressed these concerns and which could also be used after future bushfires.
The specific aims of the project were:
• Determine the current status of priority populations of threatened flora species.
• Identify threats to post-fire recovery of priority populations of threatened flora species.
• Identify management requirements for priority populations of threatened flora species.
• Record “vital attributes”.
• Provide a baseline against which post fire recovery of priority populations of
1 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
threatened flora could be evaluated.
• Develop a protocol for ongoing monitoring suitable for wider application to post-fire monitoring in eastern Victoria.
2 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Methods
Data acquisition
Departmental databases, herbarium records and oral records were interrogated to collate population locations for 43 species. One species (Caladenia concolor) confined to the Stanley/Eldorado rehabilitation area was not considered during this survey. These locality data were superimposed over a map of the fire-affected area using GIS. Species that were outside the fire boundary were removed, as were species that were subject to recovery plan implementation or preparation and therefore currently being managed. The remaining population records were prioritised using a number of criteria. Duplicate records, populations with vague locations and pre-1980 records (unless no other records existed or the population was currently known) were assigned low priority. High priority was given to recent records with accurate locations, populations with recent VrotPop data, records submitted or obtained verbally from reliable sources and records collected during recent recovery plan preparation by DSE or Royal Botanic Gardens scientists.
Finally, each record was assigned an accuracy rating of 1 (useful); 2 (likely to be useful); 3 (unlikely to be useful but worth consideration); 4 (not useful); 5 (unknown). Records rated 1- 3 were mapped on topographic maps at 1:25,000, 1: 50,000 or 1:100,000 depending on available coverage. At the end of the survey, it was apparent that records classified from 1 – 3 were reasonably representative of the distribution of the species within the study area.
Searches were conducted for mapped populations to determine the post-fire regenerative status of the target species. Each search was roughly of two to three hours duration, excluding travel time to the sites. If a site was unburnt in the recent fires, it was usually assigned low priority and no further searches were done, in order to free up as much time as possible for re-locating populations in areas that had been burnt. If a burnt population was found, the population size (area of occupancy and/or number of individuals), mode of regeneration, associated vascular species, habitat information (drainage, geology, aspect, soil type, estimate of fire severity), actual and potential threats, and recommendations for future site management were all recorded. Population locations were recorded using a GPS. The number of burnt populations that were relocated was compared with the total number of records extracted for survey, to determine whether sampling had been extensive enough to predict post-fire regeneration across the burnt range of a species.
Each population was assigned a category to broadly indicate regenerative status -
‘good’ = vegetative regeneration and/or seedling recruitment clearly replacing or exceeding the pre-fire population;
3 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
‘poor’ = more than 50% of the population killed with no significant vegetative regeneration or seedling recruitment;
‘none’ = plants killed with no replacement.
Taxonomic and conservation status for vascular plant species follows Ross and Walsh (2003). The reference for taxonomy of cryptogams and all vernacular names was DSE’s Flora Information System. Conservation status is consistent with IUCN criteria (IUCN 2001).
Field work was carried out from January to April 2004. Mt Buffalo, Mt Beauty, Corryong, Orbost, Omeo/Swifts Creek and Dargo/Heyfield fire rehabilitation areas were visited. Time spent at each location searching and recording population information ranged from 1 hour to 3 hours.
VrotPop forms were completed from information collected for each population. Summaries for each species with burnt populations were compiled from VrotPop forms and for some unburnt populations, where time allowed.
Fire response characteristics
Functional groups
Using field observations, species were allocated to one of four basic fire response groups based on resprouting ability and propagule persistence (Bond & van Wilgen 1996; Pausas et al. 2004). This system was a simple and clear method by which the basic response of a species after a single fire could be recorded and applied in a general sense across each species’ range, and is intended to indicate patterns of persistence and recruitment. Other traits, such as plant response to fire severity, fire season and fire frequency, or the length of time between fires, were not considered. These other traits are certain to influence regeneration, particularly in relation to the obligate seed recruiters, which frequently require relatively high intensity fires to sufficiently heat soil before seed dormancy is broken (Auld & O’Connell 1991; Bond and van Wilgen 1996).
Resprouters were defined as those individuals capable of vegetative regeneration after 100% scorch by fire (Gill 1981). Propagule persisters were defined as species with propagules that survive for long periods as soil or canopy stored seed, or were species with pyrogenic flowering and survive 100% scorch by fire (Pausas et al. 2004). Propagules of such plants are available in the post-fire environment, including after the death of mature adults.
Species could thus be assigned to one of four fire response groups (Bond & van Wilgen 1996;
4 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Pausas et al. 2004).
• R+P+ Resprouter with persistent propagules (facultative resprouters).
• R+P- Resprouter with non-persistent propagules (obligate resprouters).
• R-P+ Non-resprouter with persistent propagules (obligate seed recruiter).
• R-P- Non-persistent species (unable to survive fires, but modified here to include annuals with short-lived seed banks still available post-fire).
Vital attributes
Each taxon was then assigned a set of “vital attributes” (Noble & Slatyer 1980) required for the fire management databases currently being compiled by DSE and Parks Victoria (Fire Ecology Working Group 2004). This information is intended to assist with fire management of specific sites by predicting post-fire vegetation succession based on three attributes: method of persistence, establishment and longevity (Table 1).
Method of Persistence
Seedling establishment
D seed: dispersed long distances
S seed: stored, maintains viability for long period, partial germination per disturbance
G seed: stored, maintains viability for long period, single germination per disturbance
C seed: short-lived, exhausted after single germination
Vegetative mechanisms
V sprouters: all ages survive, all become juvenile
U sprouters: mature remain mature, juveniles remain juvenile
W sprouters: mature remain mature, juveniles die
5 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Dual mechanisms
∆ dispersed seed + mature remain mature + juvenile may or may not resprout (D+ U or W)
Σ seed store + mature remain mature + juvenile may or may not resprout (S+U or W)
Γ seed store with one germination + mature remain mature + juveniles die (G+W)
Conditions for Establishment
T tolerant, will establish in presence of adult competition (multi-aged population)
I intolerant, needs disturbed site with competition removed (single aged population)
R requires some precondition to be met before establishment, delayed establishment
Longevity
Juv Number of years plant remains reproductively immature
Mat Number of years plant remains mature and alive
Ext Number of years any source of regenerative material (seeds, rhizomes etc.) remains on site
Table 1. Vital attributes and their codes.
Monitoring
A range of taxa with varying fire response characteristics was monitored, so that the rate of post-fire survival and mortality of regeneration could be evaluated over time. The aim was to devise a relatively rapid method by logging the performance of the single regenerative attribute thought to best indicate population recovery. This approach was guided largely by the need for a solution to the problems frequently encountered by agency staff required to monitor a growing number of threatened species with limited personnel, time and financial support. Consequently on-site monitoring time needed to be less than three and the method suitable for wide application in the future. Data analyses needed to utilise straightforward methods accessible to a wide range of practitioners.
At least one taxon from each of the four fire response groups was chosen. Species that relied wholly on seedling recruitment to recover populations were given highest priority as these require specific management, particularly from the potential threat of another fire destroying plants before they have reached maturity and replenished seed banks.
6 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Four methods were trialed:
1. Facultative species (R+P+) and obligate seeders (R-P+): 1 m2 quadrats were placed a metre apart over replicated transects through a population. The number, orientation and length of transects depended on population size but at least two transects were established per species. A permanent steel or wooden stake was hammered into the ground at each end of the transect and their locations recorded using a GPS. Each transect was assigned an identity (DSE/number/date). All individuals within each quadrat were tagged with a stainless steel pin (15 cm long and 2 mm wide, hooked at one end) pushed into the soil beside each plant. For East Gippsland species, a coloured disc was attached with a unique number for each individual plant written on the disc with permanent ink. The number of seedlings or the number of seedlings and resprouts was counted in each quadrat.
Species monitored by this method were: Grevillea alpivaga (R-P+), Eucalyptus mitchelliana (R+P+), Myoporum floribundum (R+P+) and Deyeuxia pungens (R+P-). An additional transect was established using the same method to monitor one small unburnt population of Thesium australe.
2. Facultative mat forming perennial (R+P+): replicated transects were placed perpendicular to the longest axis of the population. Wooden stakes were hammered in at each end of each transect and their locations recorded using a GPS. A tape was stretched between the two pegs and a steel rod (approx. 5 mm diameter) was placed perpendicular to the tape at points 10 cm apart, until it touched the ground. Presence/absence of the species, was recorded at each point where plant parts did/did not intersect with the steel rod. Lobelia gelida was monitored using this method.
3. Obligate resprouter (R+P-): replicated transects were placed through a population. A permanent steel or wooden stake was hammered into the ground at each end of the transect and their locations recorded using a GPS. The location of individual plants perpendicular to the transect was marked with stainless steel pins (15 cm long by 2 mm wide and hooked at one end), pushed into the soil beside each plant. The height of resprouting plants was recorded. Individuals tended to be relatively widely spaced so that it was unlikely that the quadrat based method would capture a sufficient number to indicate population recovery. Acacia nanopravissima was monitored using this method.
4. Annual (R-P-): Population size and area of occupancy were estimated for eight populations of Euphrasia eichleri (R-P-) and recorded on VrotPop forms. An individual plant was considered a regenerative unit. All plants were counted individually or an estimate made for large populations. Area of occupancy (m2) was calculated by measuring the outermost boundaries as a straight line to give approximate length by width.
7 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Additional monitoring
1. A single permanent quadrat was established to monitor a small population of Barbarea grayi (R+P+) from its only known occurrence. The number of individuals was counted. Cover/abundance for all species within the quadrat were also recorded using the Braun- Blanquet scale.
2. Discaria nitida plants identified by Downe and Cheal (2002) were relocated at Bundara River Bridge and the four remaining live plants were tagged using the same numbering system. The number and mean length of resprouts were measured for each plant.
Data analysis
Methods 1 and 3: Although no meaningful analyses are possible in the first year of data collection, in the future a life table should be constructed for each population or total population for each species to calculate survivorship and the rate of mortality of recruits over time (Table 2). Density of recruits/resprouts were calculated using preliminary data.
Age (years) Observed no. Proportion No. dying Rate of of plants (n ) surviving at within age mortality (q ) (x) x x start of age interval x to interval x (l ) x+1 (d ) x x
01151.0900.78
1 25 0.217 6 0.24
2 19 0.165 7 0.37
Table 2: Example of a life table and hypothetical data. Age interval is 1 year; lx = nx/n0; qx = dx/nx.
Survivorship curves should be constructed by plotting the number of survivors (n or l ) x x against age (x) on a logarithmic scale.
Method 2: Two-way repeated measures ANOVA (Quinn and Keogh 12002) should be used to compare plant cover in the future to detect the significance of change in population recovery between years. Percent plant cover was calculated for each population using preliminary data.
8 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Method 4: No analysis was possible this year. In future, annual population size can be plotted and compared between years.
9 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Results
1,358 records were collated, reducing to 568 records that were within the study area. After prioritisation, 153 of these were targeted for surveys. In many cases it was impossible to be sure whether known records had been re-located, as grid references extracted from data sources rarely coincided with those measured in the field. In addition, it was often difficult to precisely determine the number of known populations for many species from data bases. It was frequently the case that the same population had been included on the Flora Information System many times but with different locational data. This is mainly due to multiple contributors over time using a range of tools with varying degrees of accuracy, such as topographic maps compared with GPS.
By the close of the survey period, 181 populations had been found, including populations that had not been previously recorded. 126 populations had been burnt and 55 populations were unburnt (Appendix 1). Specific details were recorded on VrotPop forms and the VrotPop summaries are provided with this report.
Twenty-two vascular plant species showed good regeneration at all sites inspected, either from seeds or by vegetative resprouting. These were –
Acacia phlebophylla Euphrasia crassiuscula subsp. eglandulosa Aciphylla glacialis Euphrasia crassiuscula subsp. Barbarea grayi glandulifera
Bertya findlayi Euphrasia eichleri
Carex echinata Euphrasia scabra
Celmisia sericophylla Gingidia harveyana
Chionogentias cunninghamii Grevillea alpivaga subsp. major Lobelia gelida Deyeuxia pungens Myoporum floribundum Eucalyptus elaeophloia Olearia astroloba Eucalyptus mitchelliana Pelargonium helmsii Euphrasia crassiuscula subsp. crassiuscula Westringia lucida
These species appear to have benefited from the fires and are likely to have increased in population size since being burnt. New populations of Pelargonium helmsii, previously thought to be confined to the Mt Bogong area, were recorded at Mt Buffalo and the Cobberas, representing a considerable expansion of its known pre-fire range. Aciphylla glacialis and Gingidia harveyana were recorded for the first time at the Cobberas, and an old record for
10 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Eucalyptus elaeophloia, that was previously known only as a single vague record, was also relocated at the Cobberas. New populations were also recorded for all species of Euphrasia (Bogong High Plains area), Grevillea alpivaga (Mt Buffalo) and Westringia lucida (Mt Arthur).
Some doubt exists as to the regenerative status of Bertya findlayi, as seedlings were difficult to identify. However, observations suggest that this species regenerates from soil-stored seed and is likely to have had a positive response to the fires.
Populations of seven species which were not burnt, or experienced only minor damage, were relocated within the fire perimeter (i.e. Abrotanella nivigena, Acacia binervia, Carex cephalotes, Carex paupera, Craspedia alba, Kelleria laxa, Parantennaria uniceps). C. paupera is considered by some authors as taxonomically dubious and difficult to separate from the widespread species C. inversa (Walsh & Entwisle 1994).
Four vascular species (Acacia nanopravissima, Babingtonia crenulata, Thesium australe and Discaria nitida) and two non-vascular species (Bartramia bogongia, Climacium dendroides) showed poor regeneration. Up to 50% of known populations were not found in spite of having accurate locational information, or were not killed but showed no significant regeneration, or more than 50% of plants were killed at a single site and with no significant seedling recruitment.
Acacia nanopravissima was relocated at one site where plants were regenerating by vegetative resprouts. However, an additional population, apparently nearby but not found during this survey, was not regenerating (B. Molyneux pers. comm.). Records for two additional populations were vague and were not relocated.
Two pre-fire 2002 records for Babingtonia crenulata at Mt Buffalo were not relocated. These sites were severely burnt and are now quite exposed. One re-located population consisted of a single plant within severely degraded habitat. Determination of the post-fire status of other remote populations required more time than was available during the survey. Conversely, there was vigorous regeneration at two other lightly-shaded and moist burnt sites, suggesting that the post-fire response of this species may be contingent on local habitat conditions.
Two burnt populations and one unburnt population of Thesium australe were re-located. Comparisons with VrotPop information suggest that the burnt populations are reduced since the fires. Three populations were not relocated, but the sites where they had been previously recorded had been burnt.
One population of Discaria nitida consisting of 18 plants had been severely burnt, with the majority of adults having been killed. Four adults were resprouting but no seedling
11 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires. recruitment was seen. Sites at Victoria River and Spring Creek (Cobungra Station) consisting of about 30 - 35 plants were not burnt (M. Bramwell, pers. comm.) and were not inspected.
Several populations of Bartramia bogongia seen in 2002 appeared to have been burnt in the 2003 fire and were no longer present. One unburnt population was re-located.
The entire habitat of Climacium dendroides had been burnt and there was no evidence of regeneration.
Four species were not relocated. These were -
Grevillea pachylostyla,
Glycine latrobeana,
Euphrasia collina subsp. muelleri
Almaleea capitata.
Access to Grevillea pachylostyla populations likely to have been burnt was precluded by tracks still blocked by post fire-debris. Other populations at Reedy Creek Chasm were difficult to access but unlikely to have been burnt.
A single record for Glycine latrobeana was not found, even though the general area had not been burnt. This species is known to regenerate well after fires from a well-developed taproot or from seed that germinates in response to a heat stimulus. Further inspections during the flowering season may prove beneficial.
There were no records for Euphrasia collina subsp. muelleri within the fire boundary.
Almaleea capitata was not re-located.
Two species are considered to have been extinct pre-fire (Epilobium willisii and Prasophyllum morganii), with no reliable records since the 1940s and 1980s respectively (N. Walsh pers. comm., Jeanes and Backhouse 2001; Coates et al. 2002; Rouse 2002). Searches were conducted for both species but failed to locate plants.
Two orchid species, known to have been burnt but subject to recovery plan implementation or preparation, were not inspected. Prasophyllum niphopedium has regenerated from tubers protected below ground at the time of the fire (M. Duncan pers. comm.) and is also likely to benefit from reduced competition from the associated grassy vegetation. Pterostylis X aenigma was dormant during the fire and during the survey period. However, site inspections were conducted during the flowering season in 2004 by the Bairnsdale and District Field Naturalists Club (BDFNC) in conjunction with DSE and Parks Victoria and plants were regenerating and flowering (Duncan 2004). VrotPop forms for the population were submitted to DSE (Bairnsdale) by the BDFNC. In any case, this species is thought to be a hybrid (Jones and Clements 2002) and was assigned a low priority.
12 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Conservation status
The results broadly indicated that most species had retained their pre-fire conservation status, with some exceptions. Some species were more abundant than their current conservation status would indicate and may warrant down-listing in future. The scope of the project precluded IUCN assessments for each taxon. However, it was apparent during the project that some species were likely to have been under-sampled.
Extinct species
Two species were listed as extinct (Rx; Vx) and have retained their pre-fire status (Table 3).
Species Pre-fire Regeneration Post-fire status Comments status Epilobium willisii Rx None Unchanged Prasophyllum Vx None Requires Victorian morganii national re- endemic assessment Table 3. Species Extinct in Victoria: pre-fire conservation status, regenerative response and post-fire conservation status.
Endangered species
There were nine species listed as Endangered in Victoria and threatened nationally, including those with unknown status (Ee; Ke; Re; Ve; Kk; e). It is likely that all have retained their pre- fire conservation status (Table 4).
Between 60% and 100% of populations that were burnt were re-located for each Endangered species during this survey or by DSE regional staff as part of recovery plan implementation. Consequently, none was considered under-sampled.
13 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Species Pre-fire Regeneration Post-fire % populations Comments status status surveyed Pterostylis X Ee Good Unchanged 100% Putative aenigma hybrid; recovery plan. Euphrasia Ee Not seen Unknown ⎯ No records collina subsp. in the study muelleri area Prasophyllum Ee Not seen Unchanged 75% niphopedium Kelleria laxa Ve Not burnt Unchanged 100 Euphrasia Ke Good Unchanged 70% scabra Chionogentias Kk Good Requires re- 100% Likely to be cunninghamii assessment more subsp. major abundant than previously thought. Myoporum Re Good Unchanged 70% floribundum Discaria nitida Re Poor Unchanged 100% Unburnt at other known site Acacia e Not burnt Unchanged 100 binervia Table 4. Species Endangered in Victoria: pre-fire conservation status, regenerative response, post-fire conservation status and the proportion of re-located populations in the study area that were selected for surveying.
Vulnerable species
There were 25 species listed as Vulnerable in Victoria (Vv, v, Rv), with 20 of these either rare or threatened nationally (Table 5). The conservation status of six species may need re- assessment.
Between 0% and 100% of burnt populations were re-located for each Vulnerable species during this survey. Seven were considered under-sampled (where the rate of re-location fell below 50%), ie. Acacia nanopravissima; Almaleea capitata, Babingtonia crenulata, Barbarea grayi, Carex cephalotes, Carex echinata and Thesium australe.
14 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Species Pre- Regeneration Post-fire % Comments fire status populations status surveyed Babingtonia Vv Poor Unchanged 50 Requires crenulata further survey Eucalyptus Vv Good Unchanged 100 elaeophloia Euphrasia Vv Good Unchanged 70 crassiuscula subsp. glandulifera Euphrasia eichleri Vv Good Unchanged 100 Glycine latrobeana Vv Unknown Unchanged ⎯ Not found Lobelia gelida Vv Good Unchanged 60 Olearia astroloba Vv Good Unchanged 100 Thesium australe Vv Poor Requires re- 20 Requires assessment further survey Acacia v Poor Requires re- 25 Requires nanopravissima assessment further survey Barbarea grayi v Good Unchanged 50 Carex echinata v Good Unchanged 50 Carex paupera Vv Not burnt Unchanged 70 Climacium v None Requires re- 100 At increased dendroides assessment risk of extinction since the fires Gingidia harveyana v Good Requires re- 70 Likely to be assessment more abundant than previously thought
15 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Species Pre- Regeneration Post-fire % Comments fire status populations status surveyed Abrotanella nivigena Rv Not burnt Unchanged 100 Almaleea capitata Rv Unknown Unknown 0 Requires further survey Bertya findlayi Rv Good (?) Unchanged 100 Few records; requires further survey Carex cephalotes Rv Not burnt Unchanged 25 Craspedia alba Rv Not burnt Unchanged 100 Parantennaria Rv Not burnt Unchanged 100 uniceps Westringia lucida Rv Good Unchanged 100 Pelargonium helmsii Rv Good Requires re- 100 Likely to be assessment more abundant than previously thought Table 5. Species Vulnerable in Victoria: pre-fire conservation status, regenerative response post-fire conservation status and the proportion of re-located populations in the study area that were selected for surveying.
Rare species
Seven species were listed as Rare in Victoria both before and after the fire (Table 6). One species (A. glacialis) appears to be relatively abundant within its range and may require re- assessment. Only one species was under-sampled (Grevillea pachylostyla).
16 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Species Pre-fire Regeneration Post-fire % Comments status status populatio ns surveyed Acacia phlebophylla Rr Good Unchange 80 d Eucalyptus Rr Good Unchange 80 mitchelliana d Euphrasia Rr Good Unchange 70 crassiuscula subsp. d crassiuscula Euphrasia Rr Good Unchange 100 crassiuscula subsp. d eglandulosa Grevillea alpivaga Rr Good Unchange 100 d Grevillea Rr Unknown Unchange 0Requires pachylostyla d further survey Aciphylla glacialis r Good Requires 80 Likely to be re- more assessmen abundant t than previously thought Table 6. Species Rare in Victoria: pre-fire conservation status, regenerative response and post-fire conservation status.
Additional species recorded
The following rare or threatened species were also recorded during the survey. Locations have been submitted for inclusion on the Flora Information System maintained by DSE.
Arthropodium sp. 1 (Rr) Muehlenbeckia diclina subsp. 1 (r)
Discaria pubescens (Rr) Pimelea flava subsp. dichotoma (r) Grevillea willisii (Rr) Pomaderris phylicifolia subsp. Euphrasia caudata (r) ericoides (r)
Irenepharsus magicus (Rr) Pultenaea densifolia (r)
Agrostis australiensis (r) Actinotis forsythii (v)
Asplenium trichomanes (r) Chenopodium erosum (v)
Helichrysum adenophorum var. Poa labillardieri var. acris (v) waddelliae (r) Ozothamnus adnatus (Kv) Isolepis montivaga (r)
17 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Fire response characteristics
Functional groups Functional traits characterising disturbance response were assessed for 28 species from burnt sites (Appendix 2). These included the two orchids (Prasophyllum niphopedium and Pterostylis X aenigma) that were not seen during the survey but have a known fire response. Determination of responses at times proved difficult, and consequently some species were allocated to groups based on assumptions regarding seed bank persistence which may require revision in the future.
As many species would not have had sufficient time to flower and/or set fruit in 2003 (having been only recently burnt), and no plants had set seed by the time the survey was conducted, any seedlings of these species were assumed to have derived from seed produced in previous seasons and stored in persistent seed banks. Taxa where this was the most likely explanation were assigned to the R+P+ or R-P+ categories.
Other species, notably the Euphrasia spp., proved problematic. Alpine taxa growing on relatively thin soils or in acidic peats are typically unable to accumulate soil seed banks. Nevertheless, post-fire populations had clearly derived or partly derived from see, in spite of the adults having been burnt during their fertile phases in 2003 were assigned to the R+P- or R-P- categories. It was assumed that the seed from which these recruits were derived had been produced mainly in the year prior to the fires but would have been unlikely to have persisted for much longer than 12 –36 months previously, and were classified as non- persistent.
It was not possible to assign one particular species to a fire response category. Thesium australe is a semi-parasitic short-lived perennial, which had resprouted after being burnt. No seedlings were seen during the survey. However, seedling recruitment has been observed in the past after fire, as well as between fires and recruitment is thought to be continuous in this species from a soil seed bank that is replenished annually but does not persist. However, the regenerative mechanisms of this species remain unclear (Prober and Thiele 1998) and it would be inaccurate to consider this species as either an obligate resprouter or a facultative resprouter with a persistent seed bank.
For other species, it was clear that plants were obligate resprouters with no evidence of seedling recruitment and were also designated as R+P-. However, a putative lack of seedlings within a population may also have meant that there had been insufficient heat flux through the soil profile to stimulate germination, especially where fire intensity was patchy and may not have coincided with seed banks; seed viability was low; seeds were still dormant in the soil at the time of the survey; soils were too compacted for seed banks to accumulate; or seedlings were simply difficult to detect amongst post-fire debris or within
18 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires. vigorously regenerating grass swards (eg. Chionogentias cunninghamii subsp. major, Thesium australe).
Based on these decisions, the majority of species (14) species were classified as obligate resprouters with no persistent seed bank (R+P-); eight taxa had the ability to resprout and regenerate from a persistent seed bank (R+P+); four species were obligate seed recruiters from a persistent seed bank with no ability to resprout (R-P+). Two species were short lived annuals (R-P-) (Appendix 2).
Vital attributes
Methods of persistence, conditions for establishment and where possible, the length of the juvenile period were recorded for 29 species (Appendix 2). This approach draws on a relatively detailed set of information and it was not possible in such a short field season to estimate the number of years a plant remains mature and alive or the number of years any source of regenerative material (seeds, rhizomes etc.) remains on site.
Interpretation of vital attributes characters also proved challenging, with some species difficult to categorise. For example, the seed viability or germination requirements of some species are not known, although species with hard seed coats would otherwise reasonably be expected to form persistent seed banks, based on seed coat characteristics (Baskin and Baskin 2001). For example, Discaria nitida and Acacia nanopravissima. However, for both these species, no seedlings were observed and plants could also be killed by fire without resprouting. Seed viability in D. nitida is high (Hall and Parsons 1987), although Discaria species are thought to have complex dormancy mechanisms which are poorly understood (Keogh and Bannister 1994). It is believed that A. nanopravissima is incapable of producing viable seeds (B. Molyneux pers. comm).
There were no pre-fire vital attributes data available for any species at any of the sites, meaning that the ability of species to establish with or without competition was in most cases, unknown. Assigning categories for conditions for establishment also proved problematic for some species, in particular herbaceous alpine taxa which, although infrequently burned, are likely to have opportunities for seedling recruitment where bare ground is continuously available as a consequence of frost heave, slow accumulation of biomass and scouring by wind. However, so little is known of the biology of these taxa that categories require review in the future.
The length of the juvenile phase could be determined for only a small number of taxa, the majority of which were mostly herbaceous species found at altitudes above 1200 m and seen in bud, flowering or setting seed during the survey.
19 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Most taxa (18) had regenerated predominantly by vegetative mechanisms, where all ages become juvenile post-fire, with the exception of the two orchids which were dormant at the time of the disturbance and remained in their pre-fire life stage. There was a mixture of post-disturbance establishment strategies. As would be expected, the majority of vegetative regenerators could tolerate competition during the establishment phase. Thesium australe was tentatively assigned to this group as the plants seen had resprouted at sites inspected. However, as discussed above, this is unlikely to be an accurate assessment for the species across its range and “C” may be more widely applicable after survey of disturbances at other sites.
Ten taxa used seed-based regenerative mechanisms to establish after the fires, and were intolerant of competition from established vegetation.
One species had dual mechanisms for post disturbance persistence, but needed a competition-free habitat in which to recruit seedlings.
Threats
Threats were recorded in 34 burnt populations (24%) (Appendix 3). The most common threat was pest plants, recorded in 25 populations (8% of all those burnt). Pest animals were considered a threat in 12 populations. Other threats included recreational vehicles, roadworks or erosion, but these were less common (9 populations).
Potential threats likely to impact on populations in the future were pest animals (11 populations) and pest plants (8 populations). A further six populations were potentially threatened by a range of miscellaneous threats including recreational vehicles and the risk of fire within the next decade.
Populations most seriously threatened by weeds were Discaria nitida (Bundara River Bridge, Alpine National Park), Barbarea grayi (Native Dog Flat, Alpine National Park) and Babingtonia crenulata (Eurobin Creek, Mt Buffalo National Park). However, the threat of weed invasion was relatively minor in most other situations, with most populations not at serious risk.
Pest animals were mainly feral horses and other domestic or feral animals including cattle and rabbits. Feral horses were particularly conspicuous in the Cobberas area, notably at the margins of drainage lines, including creeks and bogs, many of which had been damaged by trampling.
Population summaries and VrotPop forms submitted with this report provide details for specific sites.
20 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Monitoring
Obligate seeders (R-P+) and facultative resprouters (R+P+).
Grevillea alpivaga (R-P+)
One transect was established at each of three sites: Wild Dog Plain, Mackeys Peak and The Font (Appendix 4). The length of transects and hence the number of quadrats was determined by population size; time and staff availability precluded more replication.
Recruitment was highly variable between sites. The highest recruitment was at Wild Dog Plain where the pre-fire adult population occupied an area of approximately 2,500m2 situated on relatively stable rocky slopes. Seedling recruitment was much lower at Mackeys Peak and at The Font (Table 7). The latter two sites supported small populations occupying areas of approximately 25 m2 and 75 m2 respectively, but with far fewer plants growing on steep, unstable slopes where seed banks may be slow to accumulate and seedling establishment difficult.
Site Seedling density (m-2) ± SE
Wild Dog Plain 25 ± 3.3
Mackeys Peak 2.6 ± 1.8
The Font 0.5 ± 0.3
OVERALL DENSITY 11 ± 2.6
Table 7. G. alpivaga seedling densities (number of plants per square metre ±standard error of the mean) recorded in transects at three sites in Mt Buffalo National Park.
21 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Eucalyptus mitchelliana (R+P+)
One 15 m transect was established over a rocky area close to the Chalet-Catani Track to monitor seedling recruitment (Appendix 7). Mean seedling density was 4 seedlings m-2 (Table 8). As most populations of E. mitchelliana were unburnt or only lightly burnt and resprouting, and additional searches failed to locate seedlings at other E. mitchelliana sites (K. Cosgriffe, PV, pers. comm.), further replication was considered a low priority.
Site Seedling density (m-2) ± SE Chalet-Catani Track 4 ± 1.1 OVERALL DENSITY 4 ± 1.1
Table 8. E. mitchelliana seedling densities per square metre (number of plants per square metre ±standard error of the mean) recorded in one burnt transect in Mt Buffalo National Park.
Deyeuxia pungens (R+P-)
Three transects were established at Ballantyne Hills (Appendix 6). Plants were regenerating predominantly by root resprouting and to a lesser extent by seedling recruitment (Table 9). Mean density of resprouting plants was 2 plants m-2, mean seedling density was 0.8 seedlings m-2 and total plant density was 3 plants m-2.
Site Seedling density Resprout density Total plant density (m-2) ± SE (m-2) ± SE (m-2) ± SE
Ballantyne Hills 1 .3 ± 0.3 1.5 ± 0.7 1.8
Ballantyne Hills 2 .6 ± 0.4 1.5 ± 0.4 2
Ballantyne Hills 3 1.2 ± 0.3 2.9 ± 1.1 4
OVERALL 0.8 ± 0.2 2.1 ± 0.5 2.9 ± 0.6 DENSITY
Table 9. D. pungens seedling and resprout densities (number of plants per square metre ±standard error of the mean)recorded in burnt transects at three sites in the Alpine National Park.
22 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Myoporum floribundum (R+P-)
Single transects were established to monitor regeneration at each of four sites – Ingeegoodbee Track 1, 2 and 3, and Turnback Track (Appendix 7). Plants were regenerating by root resprouting and seedling establishment. Mean density of resprouting plants was 0.8 plants m-2, mean seedling density was 0.6 seedlings m-2; and total plant density was 1.5 plants m-2 (Table 10).
Site Seedling density Resprout density (m- Total plant density (m-2) ± SE 2) ± SE (m-2) = SE Ingeegoodbee Track 0.7 ± 0.5 0.8 ± 0.4 1.4 ± 0.7 1 Ingeegoodbee Track 0.25 ± 0.1 0.3 ± 0.1 o.6 ± 0.2 2 Ingeegoodbee Track 1.3 ± 0.4 1.1 ± 0.4 2.4 ± 0.6 3 Turnback Track 0 1.1 ± 0.4 1.1 ± 0.4 OVERALL DENSITY 0.6 ± 0.2 0.8 ± 0.2 1.5 ± 0.3 Table 10. M. floribundum seedling and resprout densities (number of plants per square metre ±standard error of the mean) recorded in burnt transects at four sites in the Alpine National Park.
Thesium australe Single transects were established at each of two unburnt populations of T. australe at Stony Creek (Appendix 8). Plants were resprouting from rootstock but no seedlings were recorded at either site. Mean overall density of resprouts was 3 resprouts per m-2. However, resprouting plants at Stony Creek 2 were twice as dense as the population at Stony Creek 1 (Table 11).
Site Resprout density (m-2) ± SE Stony Creek 1 2 ± 0.9 Stony Creek 2 4 ± 2.0
OVERAL DENSITY 3 ± 0.9
Table 11. T. australe resprout densities densities (number of plants per square metre ±standard error of the mean) recorded in transects at two unburnt sites in the Alpine National Park.
23 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Facultative mat forming perennial (R+P+)
Lobelia gelida.
Two sites were monitored, at Wirbill Plain and Hospice Plain (Appendix 10). Four transects were established at each site. Recovery varied significantly between sites (Table 12). However, the area available for recolonisation also varied markedly between sites, suggesting that habitat quality may also vary. The L. gelida population at Wirbill Plain occupied a large depression approximately 180 m2, compared to the much smaller area (15 m2 ) occupied by the population at Hospice Plain. The results suggest that there may be some difference in habitat quality between the two sites, or difference in the pre-fire size of seed banks and/or populations.
Site Transects No. of points Present/absent % Cover Wirbill Plain 3 192 37/155 19 Hospice Plain 4 149 77/72 53 Table 12. Number of points with and without L. gelida and percent cover of post-fire regeneration in seven transects at two sites at Mt Buffalo National Park.
Obligate resprouter (R+P-)
Acacia nanopravissima
Forty resprouting plants of A. nanopravissima were located perpendicular to two transects (Appendix 13). The total population size was estimated to be approximately 80 individuals occupying approximately 1,800 m2. Maximum height of resprouting plants ranged from 40 cm to 330 cm, and more than half of the tagged plants were in the early stages of bud development (Table 12).
Site Transects No. of plants Mean maximum height ± Phenology monitored SE Splitters 2 40 171 ± 10.8 63% in bud Creek
Table 13. Number of resprouting A. nanopravissima plants recorded in two burnt transects at one site in the Alpine National Park.
24 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Annual (R-P-)
Euphrasia eichleri
Estimates of population size (number of individuals) and/or area of occupancy were recorded for eight E. eichleri populations. Populations occupied a range of sites from small patches of less than a square metre, to relatively large areas of approximately 4,000 m-2. The number of plants varied proportionally (Table 14). Quadrat and transect based were also trialed briefly in the field but proved too time consuming, particularly when travel time to sites was considered, and were hence at odds with the aim of keeping monitoring relatively rapid.
Population Name Latitude Longitude Area (m2) Number of Individuals Mt Nelse 1 360 50’ 1470 20’ 0.25 5 37.5” 21.2” Mt Nelse 2 360 50’ 1470 20’ 25 30 39.6” 21.1” Whiterocks Ck 1 360 49’ 1470 20’ 2.0” 1 500 ⎯ 38.1” Big River Fire Tk 1 360 50’ 1470 20’ 100 100 22.6” 13.9” Big River Fire Tk 2 360 51’ 18” 1470 20’ 4 000 100+ 28.8” Watchbed Creek 1 360 50’ 31” 1470 20’ 2 000 ⎯ 11.7” Watchbed Creek 2 360 52’ 22” 1470 19’ 21” 1 500 430 Quartz Ridge 360 44’ 1470 17’ 13” 3 000 200 58.9”
Table 14. Area of occupancy and/or number of individuals for eight burnt populations of E. eichleri in the Alpine National Park.
Additional monitoring
Monitoring data were collected for an additional two species with very small populations, with the broad aim of monitoring population persistence.
25 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Barbarea grayi (R+P+)
A single permanent quadrat was established at Native Dog Flat, at the site of the only re- located record. Fourteen mature plants and seven seedlings were recorded, as well as a number of invasive exotic species (Appendix 9).
Discaria nitida (R+P+)
Mean shoot length was highly variable between individuals, ranging from a few centimetres to over 30 cm (Table 15). Resprouts were generally vigorous, except on plant 2/2 where resprouts were generally weak and showing poor growth.
Plant No. Easting Northing No. of Mean resprout length (tag code). resprouts (cm) ± SE Group 1, plant 2 (1/2) 543855 5907025 5 32.3 ± 0.9 Group 1, plant 6 (1/6) 543854 59070228 10 33 ± 1.1 Group 2, plant 2 (2/2) 543862 5907042 5 6.7 ± 0.9 Group 3, plant 2 (3/2) 543856 59070748 23 19.7 ± 3.0
Table 15. No of resprouting D. nitida plants, resprout number and length at Bundara River Bridge, Alpine National Park.
26 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Discussion
Most populations have retained their pre-fire conservation status. Approximately half the species surveyed (22) were regenerating successfully after being burnt, and some had clearly benefited from the stimulus to regeneration. In addition, the discovery of new populations after the fires (Pelargonium helmsii, Chionogentias cunninghamii subsp. major, Gingidia harveyana and Aciphylla glacialis) indicated that some of these were more widespread than previously believed, although some may decline over time in the absence of fire. For these species, special management requirements are implied if population sizes are to be maintained. Seven species were not burnt and a further six species were not re-located. Six species have declined since the fire and are discussed below.
The conservation status of some taxa is incorrect in the Statewide Rehabilitation Plan. Corrections are included in Appendix 1.
The project aimed to determine post-fire conservation status of rare or threatened flora based on whether burnt populations were regenerating. Although every endeavour was made to survey a representative number of populations, this was not always possible and there are some residual concerns in regard to sample sizes.
VrotPop forms and species summaries submitted with this report include specific details of threats and management requirements.
Extinct taxa Neither Prasophyllum morganii nor Epilobium willisii were re-located. P. morganii is thought to be endemic to Victoria (Rouse 2002) and its conservation status requires re-classification at the national level. Numerous searches have been conducted for both species including after the fire, at the type location and in apparently suitable habitat in the area, but without success. Consequently, both these species should retain their current status.
Endangered taxa No species classified as Endangered within Victoria were considered under-sampled. Most burnt populations that were re-located during the survey were regenerating. An exception was Discaria nitida that was severely burnt at one site where most plants were killed. Although some plants (4) had resprouted it is unknown whether this species has a persistent seed bank and whether seedling recruitment might occur in the future. The remaining plants and any seedlings that may be present at the site are seriously threatened by chronic weed infestations and control is urgently needed. The feasibility of translocating cultivated plants should also be investigated and soil seed bank sampling carried out with view to
27 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires. evaluating the potential for in situ seedling recruitment. Further details are included on VrotPop forms and the species summary attached with this report. The remaining three plants were tagged so that shoot growth can be monitored.
Weeds have also been reported as a potential threat to Pterostylis X aenigma (Duncan 2004), an orchid known from a single population with potentially serious infestations of English Broom (Cytisus scoparius) and blackberry (Rubus fruticosus spp. agg). Deposition of large quantities of silt mobilised after the fires has also contributed to site degradation (Duncan 2004).
Pest animals (feral horses) are abundant at sites that support Prasophyllum niphopedium (Coates et al. 2002) and evidence of trampling and faecal pollution, particularly around watercourses, was seen in the Cobberas and Nunniong Plateau areas. Regenerating plants were not seen during this survey but have been reported during recovery plan implementation in 2004 (M. Duncan pers. comm.).
Live stock (cattle) were absent at the time of the survey but are a potential threat to some populations (eg. Euphrasia scabra) within the Alpine National Park where grazing licences are utilised.
One species (Chionogentias cunninghamii subsp. major) is likely to be more abundant at Mt Buffalo than current database records indicate and this taxon will require re-assessment of its conservation status if populations at Mt Hotham and Nunniong Plateau can be confirmed.
All Endangered taxa that were surveyed had non-persistent seed banks, with the possible exception of D. nitida, although in regard to the latter this is an assumption based on seed coat characteristics. Regeneration was by facultative resprouting in Pterostylis X aenigma, Prasophyllum niphopedium, Chionogentias cunninghamii subsp. major, Myoporum floribundum and Discaria nitida. Euphrasia scabra, an annual species, is thought to regenerate from a short-lived seed bank. No burnt populations of Kelleria laxa, Euphrasia collina subsp. muelleri or Acacia binervia were seen, although the first two are likely to be facultative root resprouters A. binervia probably regenerates from seed.
The results suggest that all Endangered species that were burnt during the bushfires have been able to regenerate and have retained their pre-fire conservation status.
Vulnerable taxa Seven Vulnerable species were under-sampled during the survey (Acacia nanopravissima; Almaleea capitata, Babingtonia crenulata, Barbarea grayi, Carex cephalotes, Carex echinata, Thesium australe). There were problems identifying C. cephalotes and C. echinata owing to
28 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires. the lack of fertile material but these two species are highly likely to resprout if protected from threats. Searches in 2005 to confirm the status of both these species are warranted.
Acacia nanopravissima is an obligate resprouter which, although seen in bud, apparently fails to produce viable seed. Failure to locate more than a single population suggests that further surveys are needed and that monitoring the known population should continue. There is neither a EPBC Act Recovery Plan nor an FFG Action Statement for this species.
Almaleea capitata was not relocated at any sites visited in the Cobberas or Nunniong Plateau areas. The most likely explanation is that plants have had inadequate time to regenerate since the fires. Nothing is known of its fire response, but it probably regenerates from soil- stored seed and by resprouting. Populations are likely to have experienced fire in the past and are highly likely to have survived the 2003 bushfires There is neither a EPBC Act Recovery Plan nor an FFG Action Statement for this species.
Babingtonia crenulata also requires further survey to relocate pre-fire 2002 records from the creek line flowing toward Buffalo Creek between The Font and Stakers lookout (Walsh, unpub. data held at ARI; Frood & Stuwe 1998 P01275). These sites were severely burnt and are now quite exposed. Searches along this and associated creeklines failed to locate at plants. The results of the survey suggest that regeneration may be impeded by post-fire site conditions and that seedlings and young resprouting plants are unable to tolerate desiccation. Further searches and monitoring for post fire recovery are planned in 2005 as part of Recovery Plan implementation (S. Berwick, pers. comm.). Intensive weed management is required in populations close to Eurobin Creek near the park entrance.
Barbarea grayi was relocated at a single site in the Cobberas area. Searches for another population previously recorded in the Mt Hotham area failed to locate plants. Weeds pose a potentially serious threat to ongoing recruitment by occupying bare ground and preventing seedling establishment. The generally weedy appearance of Barbarea grayi suggests that accidental destruction may threaten the known population, particularly by works crews who may not be able to recognize the species. A single quadrat was established to monitor this very small population, although the sample size will be inadequate for statistical analyses.
Populations of Thesium australe were also under-sampled. Two burnt populations and one unburnt population were re-located but T. australe was not found at a further three sites form where it has been previously recorded.. One of these, at 1st Emu Flat, has apparently not been seen for a number of years (D. Tonkinson, pers. comm.). T. australe is very difficult to locate, particularly at the seedling stage, and its post fire response is poorly understood, with a number of confusing and apparently contradictory observations on record. Population numbers appear to have declined when results were compared with information on VrotPop forms recorded in years prior to the fires.
29 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Results of the survey suggest that T. australe is primarily a short-lived resprouter after fire, although seedlings have been seen after fires in the past. Prolific seedling recruitment may only occur when a reasonable size seed bank has accumulated in the two – three year pre- fire period. This in turn is likely to depend on pre-fire habitat condition and pre-fire site management. Reasonably open conditions favoured by intermediate levels of disturbance, such as light seasonal grazing or regular winter burning, have been maintained at other sites in the past (Scarlett et al. 1984, Prober and Thiele 1998) and future management of Thesium populations is likely to require habitat manipulation. Monitoring was established at one site (Stony Creek) and it is recommended that additional monitoring be established at other sites.
Populations of Euphrasia spp., particularly those with annual life histories, are likely to have similar requirements. Euphrasia is a facultative semi-parasite, with swellings (haustoria) located on fine roots which attach to a wide range of hosts. Plants also root from prostrate stems (Barker 1982). European species are not thought to form persistent seed banks (Kelly 1986 in Grime et al. 1988), and germination and perennation has been linked to moisture availability, with early seasonal droughts negatively affecting successful germination or host- establishment (Silverside, in Wigginton 1999). This may also be the case for Tasmanian Euphrasia species (W. Potts, DPIWE, pers. obs). However, some Tasmanian species of Euphrasia are thought to have relatively long lived seed banks, possibly in the order of 10 – 30 years, but at least for two years (W. Potts, DPIWE Tasmania, unpub. data.).
There was no post-fire regeneration observed for two non-vascular species with burnt populations (Bartramia bogongia and Climacium dendroides). Monitoring has been established at the only unburnt site supporting B. bogongia, but not as part of this survey (D. Meagher pers. comm.). A monitoring transect had been established at some time prior to the fires at the C. dendroides site. Ongoing site inspections are recommended for both these species.
Threats were generally relatively minor for most Vulnerable species. Pest plants were recorded at a number of populations although in few cases could these be described as serious infestations. Pest animals, including livestock (cattle) in the Bogong High Plains area, feral horses in the Cobberas area and rabbits posed the most serious potential threats to populations due to trampling, grazing regrowth of seedlings and the elevated likelihood of weed invasion. Species or habitat of species affected by pest animals were Bartramia bogongia, Eucalyptus elaeophloia and Gingidia harveyana.
Vulnerable species encompassed a range of regenerative strategies. Two obligate seed recruiting taxa (i.e. Bertya findlayi and Westringia lucida) clearly experienced sufficient heat flux (or other germination trigger) to break seed dormancy and stimulate germination of soil
30 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires. stored seed. These populations should be protected from fire until well after plants reach maturity. Other species surveyed were facultative resprouters (12 species), with or without a persistent seed bank. One species was an annual with no persistent seed bank and one species was an obligate resprouter. Other than the seven species discussed above, all other Vulnerable species have been able to regenerate after the fires.
The results suggest that most Vulnerable taxa should retain their pre-fire conservation status in Victoria, with some exceptions. Species requiring re-assessment with a view to raising their conservation status to a higher threat category, pending future searches in 2005, are Bartramia bogongia, Climacium dendroides, Thesium australe and Acacia nanopravissima. Those species which should be reassessed for a possible down-listing to a lesser threat category are Celmisia sericophylla, Gingidia harveyana and Pelargonium helmsii.
Rare taxa All Rare species that were re-located showed good regeneration and were adequately sampled except for Grevillea pachylostyla, which is known from three sites in the upper Buchan River and Reedy Creek areas. Searches for G. pachylostyla are warranted in the upper Buchan River area, as this species is likely to be an obligate seed recruiter requiring fire protection until plants reach maturity and seed banks have accumulated. There was no evidence of seedling recruitment in a population of the closely related species Grevillea willisii, recorded near the Bundara River Bridge, which had been killed during the fire, prompting concerns over the post-fire status of G. pachylostyla. Populations known from Reedy Creek Chasm, a deep, rocky canyon, are unlikely to have been burnt.
Numerous populations of Aciphylla glacialis were recorded during the survey, suggesting that this taxon had clearly benefited from the fires. New populations were also recorded at the Cobberas. Searches for old records at Mt Buffalo were not possible owing to tracks being blocked by post-fire debris but searches in 2005 are warranted.
Threats were generally insignificant at sites supporting Rare species. Minor infestations of Acetosella vulgaris (Sheep Sorrell) were recorded as current or potential threats to populations of Aciphylla glacialis and Euphrasia crassiuscula var. crassiuscula on the Bogong High Plains. Cattle, feral horses and rabbit grazing were also evident at Lankey Plain and in the Cobberas/Nunniong Plateau area near populations of Aciphylla glacialis and at sites likely to support Almaleea capitata.
Rare taxa were either facultative resprouters or obligate seed recruiters and had experienced a range of fire frequencies and intensities. Fire severity had been adequate to promote generally substantial levels of seedling recruitment in Acacia phlebophylla and Grevillea
31 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires. alpivaga. The remaining species had resprouted, with fire intensity insufficiently high to stimulate release of E. mitchelliana seed at most sites inspected.
All Rare species are likely to have retained their pre-fire conservation status, with the possible exception of Aciphylla glacialis which should be reassessed for possible down- listing.
Monitoring Baseline data were collected for nine species against which post fire recovery of priority populations of threatened flora can be evaluated over time.
Three methods were tested in the field. The results suggest that transect based methods (1 and 3), are most likely to be robust and flexible. These allow simple calculations of survivorship and mortality rates, or if extended over a longer time frame, calculation of net reproductive rates and population growth (Harper 1977). A particular advantage of monitoring species after such an event is most populations become even-aged with high levels of recruitment not usually seen, particularly in woody perennials, in the absence of fire. Even-aged cohorts allow direct calculations of survivorship and related life table attributes without assuming population stability (Krebs 1994). This opportunity is rarely available in the high altitude environments represented within the study area and almost no published data of this nature exist for rare or threatened plant species in Australia. Other information that can be derived from monitoring which is useful for fire management planning in the future includes age at, and time to reproductive maturity, recruitment rates in between fires and longevity.
The most time consuming component of the monitoring was establishing the transects and marking plants. However, once set up transects are permanent and follow up monitoring should be reasonably quick, requiring less than a couple of hours per population. However, individual natural resource managers will need to address trade-offs between time and usefulness of the information.
The wider applicability of these methods can best be evaluated after testing with a wider range of species. In the study area, suitable species are Pelargonium helmsii (MBNP, ANP), Babingtonia crenulata (MBNP), Euphrasia crassiuscula subsp. crassiuscula (ANP), E. crassiuscula subsp. eglandulosa (ANP), E. crassiuscula subsp. glandulifera (ANP), Grevillea pachylostyla (ANP), and, if re-located, Almaleea capitata (ANP).
Simple population size counts or estimates were made for the annual species Euphrasia eichleri. These data have limited applicability but are relatively quick and are readily incorporated into DSE’s VrotPop database. However, given the high conservation status of
32 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires. this species and the other annual, E. scabra, it may be more useful in the long term to use quadrat based counts of individuals subjected to life table analyses, to gain better understanding of population dynamics and hence management requirements.
Populations of clonal plants such as Lobelia gelida, where distinguishing individuals is problematic, are particularly difficult to monitor. Although methods exist, these are generally time consuming and tedious (Harper 1977). The point-intercept method tested during this project assumed that plant cover was the best indicator of post-fire recovery in a mat-forming perennial. However, results cannot be used to directly compare rate of recovery, as indicated by survivorship and mortality, with populations data collected using transect methods, or to calculate the same range of population parameters. Consequently, this method has relatively limited interpretative power. However it was extremely quick, requiring less than an hour per population, and allows statistical comparison between years.
The fires have also made available a rare opportunity to monitor seed bank dynamics by sampling populations over time. Such work would be particularly useful for identifying species that require artificial disturbance regimes to maintain or increase population sizes, or where sites need to be protected from events that may cause seed bank losses which cannot be sustained if populations are to remain viable. Examples include Thesium australe, Euphrasia spp. and Pelargonium helmsii. Other taxa identified during the survey occurred on shallow soils or had post-fire seedling densities which suggested that soil seed bank accumulation or persistence varied between sites. These may require management regimes that also vary between sites. Examples include Grevillea alpivaga, Deyeuxia pungens and Lobelia gelida.
The survey also revealed that seed bank persistence was particularly poorly understood for most species surveyed, but is required for fire management planning (Fire Ecology Working Group (2004). Seed bank monitoring or seed burial trials would make a substantial contribution to resolving these and other management problems.
33 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Recommendations
General recommendations
• Assign high priority to pest plant control at sites where Rare or Threatened plant species occur. Implement effective pest plant control at sites identified in this report as subject to threats from pest plants. Ensure that all actions taken to control pest plants do not adversely affect coincident populations of rare and threatened plants.
• Develop strategies for pest animal management, particularly strategies to control feral horses in the Cobberas/Nunniong Plateau area of the Alpine National Park. Implement effective pest animal control at sites identified in this report as subject to threats from pest animals. Ensure that all actions taken to control pest animals do not adversely affect coincident populations of rare and threatened plants .
• Implement management requirements for populations of rare or threatened species as indicated in accompanying VrotPop forms and species summaries.
• Ensure that works crews (DSE, PV, VicRoads) can recognise all species where habitat is targeted for pest plant and animal control or road and track maintenance, and that they avoid any adverse impact on threatened plant species.
• Include locations and management requirements of all species on Parks Victoria’s Environmental Information System.
• Develop research projects that will assist with rare and threatened species management particularly in relation to fire management planning. This research program should include investigation of life histories, population and seed bank dynamics and determination of vital attributes.
Specific recommendations
• Conduct surveys for seven species to clarify their post-fire conservation status (i.e. Acacia nanopravissima, Almaleea capitata, Babingtonia crenulata, Climacium dendroides, Glycine latrobeana, Grevillea pachylostyla, Thesium australe).
• Conduct searches for species not re-located during the survey or under-sampled species (Barbarea grayi, Carex cephalotes, Carex echinata and Grevillea pachylostyla). Search for old records of Aciphylla glacialis at Mt Buffalo.
• Hand weed around all remaining D. nitida plants (dead and alive) to maximise any potential seedling recruitment.
34 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
• Investigate the feasibility of translocating plants to increase D. nitida population size at Bundara River Bridge.
• Re-assess Victorian conservation status of species likely to be more widespread and abundant than indicated pre-fire (Aciphylla glacialis, Celmisia sericophylla, Chionogentias cunninghamii subsp. major; Gingidia harveyana, Pelargonium helmsii).
• Re-assess Victorian conservation status likely to have declined post-fire (Acacia nanopravissima , Bartramia bogongia, Climacium dendroides and Thesium australe).
• Protect all obligate seed recruiting species from fire until vital attributes relating to longevity have been determined (Acacia phlebophylla, Bertya findlayi, Grevillea alpivaga, Grevillea pachylostyla and Westringia lucida).
• Protect species and habitat potentially threatened by feral horses in the Cobberas and Nunniong Plateau areas (Aciphylla glacialis, Almaleea capitata, Eucalyptus elaeophloia, and Gingidia harveyana).
• Protect species and habitat potentially threatened by feral horses and domestic livestock in areas currently leased for grazing on the Bogong High Plains (Bartramia bogongia, Celmisia sericophylla and Euphrasia spp) and Lankey Plain (Aciphylla glacialis, Carex paupera and Gingidia harveyana).
• Support and encourage PV and DSE regional staff, community groups, individuals and universities to continue monitoring Prasophyllum niphopedium (DSE Bairnsdale) the Pterostylis X aenigma population (Bairnsdale and District Field Naturalist Club), Acacia phlebophylla (La Trobe University) and Bartramia bogongia (D. Meagher).
• Continue to monitor Acacia nanopravissima, Barbarea grayi, Deyeuxia pungens, Discaria nitida, Eucalyptus mitchelliana, Euphrasia eichleri, Grevillea alpivaga, Lobelia gelida, Myoporum floribundum and Thesium australe.
• Further test rapid monitoring methods at populations of Pelargonium helmsii (MBNP, ANP), Babingtonia crenulata (MBNP), Euphrasia crassiuscula subsp. crassiuscula (ANP), E. crassiuscula subsp. eglandulosa (ANP), E. crassiuscula subsp. glandulifera (ANP), E. scabra (ANP), and, if re-located, Almaleea capitata (ANP), Grevillea pachylostyla (ANP), Climacium dendroides (ANP), and additional monitoring for Thesium australe (ANP) at burnt sites.
35 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Acknowledgments
We wish to thank all the people who spent many hours in the field and with data collation - Geoff Sutter (ARI), Obe Carter (ARI), Arn Tolsma (ARI), Judy Downe (ARI), Allison Oates (ARI), Rhiannon Apted (Latrobe Uni), Michael Fletcher (Melb. Uni), Angus Tye (Melb Uni), Libby Rumpff (Melb. Uni), Simon Connor (Melb. Uni), Sue Berwick (DSE Benalla), David Meagher, and Kevin Cosgriffe (PV Mt Buffalo).
Neville Walsh, John Reid and Val Stajsic (RBG) assisted with plant identifications and locational information. Information and locations of other species were provided by James Turner (BDFNC), Jeff Jeanes (RBG Melb.) and Mike Duncan (ARI).
David Cheal (ARI), Sue Berwick (DSE Benalla), Mick Bramwell (DSE Bairnsdale), John Wright (PV) and Tony Varcoe (PV) were responsible for administration of this and many other post- fire recovery projects. Assistance was also given by Stephen Henry and Tony Mitchell (DSE, Orbost), Gail Penfold (DSE Orbost – for producing maps) and Max Stuart (DSE Traralgon – for organising vehicle hire).
Felicity Brooke and PV Mt Buffalo staff, Peter Rennick, Peter Jacobs and PV Bright Staff, Glenn Digby (DSE Swifts Creek), Dave Foster, Mike Dower and PV Omeo staff provided additional assistance in the field, track clearing, accommodation and access to facilities. Dale Calnin (Ranger-in-Charge, Buchan Caves) and Gordon, Scott, Cain and Glen (Nowa Nowa DSE) gave advice regarding access to some sites.
We also with to thank John Armit (Bindi Station) for access to Marble Gully through his property, Buchan Motel and the Sykes family and staff at Karoonda Park, Gelantipy, for accommodation and meals.
The project was funded under the Victorian Bushfire Recovery Program (DSE and Parks Victoria).
36 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
References Barker, W. R. (1982) Taxonomic Studies in Euphrasia L. (Scrophulariaceae). A Revised Infrageneric Classification, and a Revison of the Genus in Australia. Journal of the Adelaide Botanic Gardens 5, 1-304.
Baskin, C. C. and Baskin, J. M. (2001) Seeds: Ecology, Biogeography, and Evolution of Dormancy and Germination. Academic Press.
Bond, W. J. and van Wilgen, B. W. (1996) Fire and Plants. Chapman and Hall, London.
Coates, F., Jeanes, J. and Pritchard, A. (2002) Recovery Plan for Twenty-five Threatened Orchid .Taxa of Victoria, South Australia and New South Wales 2003-2007. Department of Natural Resources and Environment, Heidelberg.
Downe, J. and Cheal, D. C. (2002) Rare Species Monitoring. Discaria nitida – Shining Anchor Plant. Arthur Rylah Institute for Environmental Research, unpublished report to Parks Victoria.
Duncan, M. (2004) Draft recovery Plan for Pterostylis aenigma (Enigmatic Greenhood) in Victoria 2005 – 2009. Department of Sustainability and Environment, Heidelberg.
Fire Ecology Working Group (2004) Guidelines and Procedures for Ecological Burning on Public land in Victoria 2004. Department of Sustainability and Environment, Melbourne.
Hall, K. F. M. and Parsons, R. F. (1987) Ecology of Discaria (Rhamnaceae) in Victoria. Proceedings of the Royal Society of Victoria 99, 99-108.
Harper, J. L. (1977) Population Biology of Plants. Academic Press.
Grime, J. P., Hodgson, J. G. and Hunt, R. (1988) Comparative Plant Ecology: A Functional Approach to Common British Species. Unwin Hyman Ltd, London.
IUCN (2001) IUCN Red List Categories and Criteria: Version 3.1. IUCN Species Survival Commission. IUCN, Gland, Switzerland and Cambridge, United Kingdom.
Jeanes, J. and Backhouse, G. (2001) Wild Orchids of Victoria, Australia. Zoonetics, Seaford, Victoria.
Keogh, J. A. and Bannister, P. (1994) Seed structure and germination in Discaria toumatou (Rhamnaceae). Weed Research 34, 481-490.
Krebs, C. J. (1994) Ecology: the experimental analysis of distribution and abundance. HarperCollins College Publishers.
Noble, I. R. and Slatyer, R. O. (1980) The use of vital attributes to predict successional changes in plant communities subject to recurrent disturbances. Vegetatio 43, 5-21.
37 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Parks Victoria and Department of Sustainability and Environment (2003) Statewide Public Land Ecological and Cultural Fire Recovery Plan. Parks Victoria and Department of Sustainability and Environment, Melbourne, Victoria, Australia.
Pausas, J. G., Bradstock, R. A., Keith, D. A., Keeley, J. E. and the GCTE Fire Network (2004) Plant functional traits in relation to fire in crown-fire ecosystems. Ecology 85, 1085-1100.
Prober, S. M. and Thiele, K. R. (1998) Ecology and Management of Austral Toad-flax (Thesium australe) at “Open Grounds”, Gillingal Station, East Gippsland. Unpublished report to the Department of Natural resources and Environment.
Quinn, G. P. and Keogh, M. J. (2002) Experimental Design and data Analysis for Biologists. Cambridge University Press, Cambridge, United Kingdom.
Ross, J. H. and Walsh, N. G. (2003) A Census of the Vascular Plants of Victoria. 7th Edition. Royal Botanic Gardens, Melbourne.
Rouse, D. T. (2002) Report on the taxonomic, ecological and conservation status of taxa in the genus Prasophyllum R.Br. in south-eastern Australia. Unpublished report to the Centre for Plant Biodiversity Conservation, CSIRO, Canberra.
Scarlett, N., Bramwell, M. and Earl, G. (1994) Action Statement No. 56. Austral Toad Flax Thesium australe. Department of Conservation and Natural Resources, Victoria.
Walsh, N. G. and Entwisle, T. J. (1994) Flora of Victoria. Volume 2, Ferns and Allied Plants, Conifers and Monocotyledons. Inkata Press.
Wigginton, M. J. (1999) British Red Data Books 1 Vascular Plants. 3rd Edition. Joint Nature Conservation Committee, Peterborough, United Kingdom.
38 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
Appendix 1. Summary of population records for post-fire threatened flora surveys, January – April 2004.
Conservation status (from Ross and Walsh 2004); species with VrotPop summaries prepared (attached separately); number of population records selected from data sources after removal of records in categories 4 and 5 (see methods), and the number of records prioritised for field searches; total number of burnt and unburnt populations found in the field; regeneration status of burnt populations (see methods).
SPECIES Conservation VrotPop Databases Records Total Number of Number of Regeneration status summary records selected number of un-burnt burnt status prepared extracted for field populations populations populations searches found found found Abrotenella No burnt nivigena Rv X 14 5 7 7 0 records seen Acacia binervia eX4211 0Not burnt Acacia nanopravissima v √ 44 2 0 2 Poor Acacia phlebophylla Rr √ 13 6 5 0 5 Good Aciphylla glacialis r √ 165 2 21 4 17 Good Almaleea capitata Rv √ 32 6 0 0 0 None Babingtonia crenulata Vv √ 76 3 0 3 Poor Barbarea grayi v √ 10 2 1 0 1 Good 39 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
SPECIES Conservation VrotPop Databases Records Total Number of Number of Regeneration status summary records selected number of un-burnt burnt status prepared extracted for field populations populations populations searches found found found Bartramia bogongia Vv √ 82 1 1 0 None Bertya findlayi Rv √ 6 2 2 1 1 Good Carex cephalotes Rv √ 20 11 3 3 0 Good Carex echinata v √ 12 2 1 1 0 Good No burnt Carex paupera Vv X 22 6 4 4 0 records seen Celmisia sericophylla Vv √ 53 8 42 17 25 Good Chionogentias cunninghamii subsp. major Kk √ 2 1 4 0 4 Good Climacium dendroides v √ 21 1 0 1 None No burnt Craspedia alba Rv X 2 2 2 2 0 records seen Deyeuxia pungens Vv √ 6 2 2 0 2 Good Discaria nitida Re √ 16 2 1 0 1 Poor 40 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
SPECIES Conservation VrotPop Databases Records Total Number of Number of Regeneration status summary records selected number of un-burnt burnt status prepared extracted for field populations populations populations searches found found found Epilobium willisii Rx X 5 2 0 0 0 Extinct Eucalyptus elaeophloia Vv √ 4 4 4 0 4 Good Eucalyptus mitchelliana Rr √ 8 3 6 1 5 Good Euphrasia collina subsp. muelleri Ee X 0 0 0 0 0 Unknown Euphrasia crassiuscula subsp. crassiuscula Rr √ 4 3 2 0 2 Good Euphrasia crassiuscula subsp. eglandulosa Rr √ 5 1 9 0 9 Good 41 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
SPECIES Conservation VrotPop Databases Records Total Number of Number of Regeneration status summary records selected number of un-burnt burnt status prepared extracted for field populations populations populations searches found found found Euphrasia crassiuscula subsp. glandulifera Vv √ 7 6 4 0 4 Good Euphrasia eichleri Vv √ 12 8 14 3 11 Good Euphrasia scabra Ke √ 6 5 4 2 2 Good Gingidia harveyana v √ 10 7 5 1 4 Good Glycine latrobeana Vv X 3 1 1 1 0 Unknown Grevillea alpivaga Rr √ 3 3 4 0 4 Good Grevillea pachylostyla Rr X 9 1 0 0 0 Unknown Kelliera laxa Ve X 4 1 1 1 0 Not burnt Lobelia gelida Vv √ 8 18 5 0 5 Good Myoporum floribundum Re √ 24 6 5 1 4 Good 42 Coates et al. Post-fire recovery of threatened flora after the 2003 bushfires.
SPECIES Conservation VrotPop Databases Records Total Number of Number of Regeneration status summary records selected number of un-burnt burnt status prepared extracted for field populations populations populations searches found found found Olearia astroloba Vv √ 5 3 3 0 3 Good Parantennaria No burnt uniceps Rv X 9 9 4 4 0 records seen Pelargonium helmsii v √ 2 1 3 0 3 Good Prasophyllum morganii Vx X 1 1 0 0 0 Extinct Prasophyllum niphopedium Ee X 9 1 1 0 1 Unknown Pterostylis aenigma Ee X 2 2 1 0 1 Good Thesium australe Vv √ 30 11 2 0 2 Poor Westringia lucida Rv √ 2 1 3 1 2 Good TOTAL 30 568 153 181 55 126 43 (yrs) Juvenile period Juvenile own. See methods See own. I* establishment flora surveys, January – April Conditions for Conditions Columns 3 – 5: vital attributes. * = unkn * attributes. 5: vital 3 – Columns Σ Method of Method persistence 2004. **** * * * * ** *** * * * ** *** * ** * * 1 ** * * * R+P-R+P- VR+P- VR+P-R+P-R+P- VR+P- T V T V V V T T * T * T I * * * 1 * R-P+R-P+ G G I I * * R+P+R+P+ S SR+P+R+P+R+P+ I I S S * * T I * * acteristics for post-fire threatened ing ability, P = seed bank persistence. ing ability, bank P = seed persistence. major subsp.
Appendix 2. Fire response char response Fire 2. Appendix 45 SPECIES mode Regeneration Abrotanella nivigena Abrotanella Acacia binervia Acacia nanopravissima Acacia phlebophylla glacialis Aciphylla capitata Almaleea crenulata Babingtonia grayi Barbarea Bartramia bogongia Bertya findlayi cephalotes Carex Carex echinata Carex paupera sericophylla Celmisia cunninghamii Chionogentias dendroides Climacium alba Craspedia pungens Deyeuxia nitida Discaria willisiiEpilobium Eucalyptus elaeophloia Eucalyptus mitchelliana Column 2 (regeneration mode): R = resprout = R mode): 2 (regeneration Column codes. of explanations for (yrs) Juvenile period Juvenile establishment Conditions for Conditions Method of Method persistence ** * * ** * 1 or 2 or ** ***** 1 * * 1 1 ** *** 1 **V 1 I 1 R-P-R-P- C C I I * 1 R+P-R+P-R+P-R+P- V V VR+P- V IR+P- IR+P- I S T U U * 2 1 or T * 2 1 or T T * 1 * R-P+ GR-P+ I G 1 * * R+P+R+P+R+P+ V V S I I I 1 1 1 . crassiuscula . eglandulosa . glandulifera . muelleri subsp subsp subsp subsp
46 SPECIES collina Euphrasia crassiuscula Euphrasia crassiuscula Euphrasia crassiuscula Euphrasia eichleri Euphrasia scabra Euphrasia Gingidia harveyana Glycine latrobeana Grevillea alpivaga Grevillea pachylostyla laxa Kelliera Lobelia gelida floribundum Myoporum mode Regeneration astroloba Olearia uniceps Parantennaria helmsii Pelargonium morganii Prasophyllum niphopedium Prasophyllum Pterostylis aenigma australe Thesium Westringia lucida Number of Number burnt populations other with potential threats s or other or s Number of Number burnt populations with potential pest animals Number of Number burnt populations with potential pest plants Number of Number burnt populations with other threats Number of Number burnt populations with pest animals reats for populations recorded during post-fire mberof burnt populationswhere evidence of pest plants, animal Number of Number burnt populations with pest plants Number of Number burnt populations with potential threats threatened flora surveys, January – April 2004. Number of Number burnt populations threats with Poor None Unknown Good Good Good 1 7 1 5 7 Not burnt 1 status
Appendix 3. Summary of actual and potential th 47 Regeneration burnt status of populations (see nu methods); total threats were recorded, or where pest plants, pest animals or other threats were potentially likely to impact on populations. SPECIES Regeneration Abrotenella nivigena Acacia binervia Acacia nanopravissim a Acacia phlebophylla Aciphylla glacialis Almaleea capitata Number of Number burnt populations other with potential threats Number of Number burnt populations with potential pest animals Number of Number burnt populations with potential pest plants Number of Number burnt populations with other threats Number of Number burnt populations with pest animals Number of Number burnt populations with pest plants Number of Number burnt populations with potential threats Number of Number burnt populations threats with Poor 1Poor Unknown 1 1 1 1 1 1 1 None Good 1GoodGood 2Good 1 Good 2Good 8 2 7 Unknown Unknown status . major 48 SPECIES Regeneration Babingtonia crenulata grayi Barbarea Bartramia bogongia Bertya findlayi Carex cephalotes Carex echinata Carex paupera Celmisia sericophylla Chionogentias cunninghamii subsp Climacium dendroides Number of Number burnt populations other with potential threats Number of Number burnt populations with potential pest animals Number of Number burnt populations with potential pest plants Number of Number burnt populations with other threats Number of Number burnt populations with pest animals Number of Number burnt populations with pest plants Number of Number burnt populations with potential threats Number of Number burnt populations threats with GoodGood 2GoodGood 1 2 2 1 Extinct Unknown V. Poor 2 2 Unknown Unknown status . subsp
49 SPECIES Regeneration alba Craspedia Deyeuxia pungens nitida Discaria Epilobium willisii Eucalyptus elaeophloia Eucalyptus mitchelliana Euphrasia collina muelleri Number of Number burnt populations other with potential threats 2 Number of Number burnt populations with potential pest animals Number of Number burnt populations with potential pest plants Number of Number burnt populations with other threats Number of Number burnt populations with pest animals Number of Number burnt populations with pest plants Number of Number burnt populations with potential threats Number of Number burnt populations threats with Good 1Good Good Good 1 Good 3Good 2 2 3 2 status . . . 50 SPECIES Regeneration Euphrasia crassiuscula subsp crassiuscula Euphrasia crassiuscula subsp eglandulosa Euphrasia crassiuscula subsp glandulifera Euphrasia eichleri Euphrasia scabra Gingidia harveyana 1 Number of Number burnt populations other with potential threats 1 Number of Number burnt populations with potential pest animals Number of Number burnt populations with potential pest plants Number of Number burnt populations with other threats Number of Number burnt populations with pest animals Number of Number burnt populations with pest plants Number of Number burnt populations with potential threats Number of Number burnt populations threats with Good 1Good 1Good 3Good 2 1Good 2 1 1 3 1 1 1 Unknown Unknown Unknown Unknown Not burntNot Unknown burntNot Unknown 1 status
51 SPECIES Regeneration Glycine latrobeana Grevillea alpivaga Grevillea pachylostyla laxa Kelliera Lobelia gelida Myoporum floribundum Olearia astroloba Parantennaria uniceps Pelargonium helmsii Number of Number burnt populations other with potential threats Number of Number burnt populations with potential pest animals Number of Number burnt populations with potential pest plants Number of Number burnt populations with other threats Number of Number burnt populations with pest animals Number of Number burnt populations with pest plants Number of Number burnt populations with potential threats Number of Number burnt populations threats with Poor 2 1 1 1 1 Good UnknownGood 2 2 3 1 2 Extinct Unknown Unknown Unknown status
TOTAL 3452 13 25 12 9 8 11 6 SPECIES Regeneration Prasophyllum morganii Prasophyllum niphopedium Pterostylis aenigma Thesium australe Westringia lucida E t; % burnt is t; % burnt ly SW of Mount SW of ly 19/02/2004 Date: monitoring data. SiteMackeys PeakMackeys PeakMackeys Peak PeakMackeys 1 No. Quadrat Mackeys Peak 2 (m) Distance Mackeys Peak 3 Seedlings Burnt % Mackeys Peak 4Mackeys Peak 5Mackeys Peak 6 2 PeakMackeys 7 4 PeakMackeys 8 6TOTAL 9 8 10 10 11 0 12 1 14 1 16 20 18 100 11 3 20 100 0 22 100 0 100 3 100 0 100 0 22 100 0 100 75 50 28 100 quadrats placed one metre apart along each transect; distance refers to refers distance transect; each along apart metre one placed quadrats 2 mn refers to the number of seedlings recorded in eachquadra
Grevillea alpivaga Appendix 4. tion; quadrat number refers to 1 m 18/02/2004. Date: 19/02/2004 Date:
53 Site to the monitored refers popula Locations: direct m 750 about Track, Reservoir the and Point to Eagle track walking the on intersection the of north 100 m Dog Plain: Wild 5933909N). (479582E Dunn 5937125N). The Font: On lower sloperock aboutabove 50 m the road, opposite hairpin bend (484141E5937700N). Wild Dog PlainWild Dog PlainWild Dog PlainWild Dog Plain 1 Dog PlainWild 2 Dog PlainWild 3 Dog PlainWild 4 Dog PlainWild 5 Dog PlainWild 6 2 Dog PlainWild 7 4Wild Dog Plain 8 6Wild Dog Plain 9 8 10TOTAL 10 20 11 12 30 12 14 19 16 100 40 18 28 20 100 19 22 100 12 21 24 100 100 48 100 14 5 100 30 100 24 26 75 50 100 100 300 Mackeys Peak: Walk Along Big track on steep slopes,rock roughly 75m above directly the hairpin bend at Mackeys Lookout (484456 the of quadrat theproportion plants adult All were that had been by the killed burnt. fires. Site No. Quadrat (m) Distance Seedlings Burnt % thequadrat the each of along position the transect; seedlings colu 55 SiteThe FontThe Font No. Quadrat The Font (m) Distance The Font 1 SeedlingsThe Font Burnt % 2The Font 3The Font 4TOTAL 5 6 2 7 4 6 7 8 10 0 12 0 14 0 14 0 100 2 100 1 100 0 100 100 3 100 100 . t (483612E t; % burnt is t; % burnt monitoring data. quadrats placed one metre apart along each transect; distance refers to refers distance transect; each along apart metre one placed quadrats 2 mn refers to the number of seedlings recorded in eachquadra eachto thequadrat by exposed proportion of occupied bed rock
Eucalyptus mitchelliana tion; quadrat number refers to 1 m Appendix 5. 19/02/2004. Site Quadrat Distance Seedlings Burnt % %Rock 56 Chalet Track120100. Track247100. Track365100. Track487100. Location: Chale the of SSW directly 500m Catani, Lake and Chalet Buffalo Mt between track walking the of side west the on outcrop Granite 5935160N). Track132641005 Track142821000 Date: Track1530151000 Site to the monitored refers popula Chalet Chalet Chalet Chalet TrackChalet TrackChalet TrackChalet TrackChalet 5Chalet Track 6Chalet Track 7Chalet Track 8Chalet Track 10 9Chalet 12 10Chalet 14 11Chalet 16 12TOTAL 7 18 10 20 22 2 24 1 100 0 100 0 15 100 0 100 6 30 20 100 100 30 70 100 60 100 5 80 66 25 50 the of quadrat refers the % rock proportion that had been burnt; thequadrat the each of along position the transect; seedlings colu - along - along (along Total refers to Transect Bearing: Transect West Transect runs Transect West ° West. Transect north runs east west, north beginning– ° monitoring data. quadrats placed one metre apart along each transect; Root sprouters transect; each along apart metre one placed quadrats 2 25/03/2004. along track at Ballantyne Gap then 500m NE from track terminus terminus track from NE 500m then Gap at Ballantyne track along Date: ngs refers to the number of seedlings recorded in eachquadrat;
Deyeuxia pungens 25/03/2004. Date: is NW on minor peak of hill No. 1 (616 373E 5906607N). Transect Bearing: 250 Bearing: Transect 5906607N). 373E 1 (616 hill No. of peak minor on NW is Appendix 6. tion; quadrat number refers to 1 m West. Locality is approx 450m from NE 008/2004. Date: 25/03/2004. ° 57 Ballantyne Hills 3 (Permanent Monitoring Site: 010/2004).300m saddle onto Ballantyne Hills - hill 1No. (616654E 5906849N). Transect runs east beginning–west, with square, red, ear tag. 240 Site to the monitored refers popula Ballantyne Hills 2 (Permanent Monitoring Site: 009/2004).300m along track at Ballantyne then track Gap 500m from terminus NE saddle onto Ballantyne Hills - hill 1No. (616601E5906803N). Transect Bearing: 240 with square, red, ear tag. Locality is 400m NE from 008/2004. 008/2004. from NE 400m is Locality tag. ear red, square, with east west, beginning – with square, ear red, tag. Locations: terminus track from NE 500m then Gap at Ballantyne track along 300m Site: 008/2004). Monitoring 1 (Permanent Hills Ballantyne saddle Hills). onto Ballantyne Locality refers to the of number plants regenerating vegetatively; Seedli the total number of number in eachplants quadrat. the of recorded total Seedlings Total Root sprouters 010203 204 205 406 0 107 4 108 2 2 009 0 6 010 0 6 011 0 1 2 0 1 3 0 0 1 0 0 1 0 0 2 4 1 no. Site Quadrat Hills 2 Hills 2 Hills 2 Hills 2 Hills 2 Hills 2 Hills 2 Hills 2 Hills 2 Hills 2 Hills 2 Ballantyne Ballantyne Ballantyne Ballantyne Ballantyne Ballantyne Ballantyne Ballantyne Ballantyne Ballantyne Ballantyne TOTAL 11 16 7 23 Seedlings Total Root sprouters 010203 304 1 0 1 2 0 0 4 0 1 0 2 no. Site Quadrat Hills 1 Hills 1 Hills 1 Hills 1 Ballantyne Ballantyne Ballantyne Ballantyne 58 TOTAL 4 6 1 7 Seedlings Total Root sprouters 010203 104 205 1206 1 107 1 008 3 2 409 3 3 010 15 1 211 0 4 6 0 1 3 1 4 1 2 0 0 3 1 8 3 2 no. Site Quadrat Hills 3 Hills 3 Hills 3 Hills 3 Hills 3 Hills 3 Hills 3 Hills 3 Hills 3 Hills 3 Hills 3 TOTAL 11 32 13 45 Ballantyne Ballantyne Ballantyne Ballantyne Ballantyne Ballantyne Ballantyne Ballantyne Ballantyne Ballantyne Ballantyne 59 49N). – west, runs east runs ransect Total refers to 11/03/2004. Date: 11/03/2004. Date: West. ° West. West (620195E 5912552N). ° ° monitoring data. quadrats placed one metre apart along each transect; Root sprouters transect; each along apart metre one placed quadrats 2 ngs refers to the number of seedlings recorded in eachquadrat;
Myoporum floribundum tion; quadrat number refers to 1 m Appendix 7. 11/03/2004. Date: West. ° 11/03/2004. 60 Date: Site to the monitored refers popula Turnback Track (Permanent Monitoring Site: 004/2004).180m west from Turnback Track (620686E 5895441N). Transect eastruns beginning with square, red, ear tag (5m north of Deddick River Road). Transect Bearing: 260 Ingeegoodbee Track 3 (Permanent Monitoring Site: 003/2004).2.5km west along Ingeegoodbee Track and10m then Transect north. – west, – beginning with square, tag ear red, (5m below transect 002/2004). Bearing: 270 Transect runs east west, – beginning with square, red, ear tag (opposite side of Ingeegoodbee Track from Transect 001/2004). T Bearing: 240 Ingeegoodbee Track 2 (Permanent Monitoring Site: 002/2004).2.5km along Ingeegoodbee Track and then (620193E 5m north. 59125 Locations: Ingeegoodbee Track 1 (Permanent Monitoring Site: 001/2004).5km west along Ingeegoodbee Track and then 10m south (620198E 265 tag Bearing: ear red, square, with beginning west, – east runs Transect 5915526N). refers to the of number plants regenerating vegetatively; Seedli the total number of number in eachplants quadrat. the of recorded total Seedlings Total Root sprouters no. Site 2 Track Ingeegoodbee 2 Track Ingeegoodbee 2 Track Ingeegoodbee 01 2 Track Ingeegoodbee 02 2 Track Ingeegoodbee 03 2 Track Ingeegoodbee 04 1 2 Track Ingeegoodbee Quadrat 05 0 2 Track Ingeegoodbee 06 2 2 Track Ingeegoodbee 07 1 2 Track Ingeegoodbee 08 1 2 Track Ingeegoodbee 0 09 0 2 Track Ingeegoodbee 2 10 0 2 Track Ingeegoodbee 0 11 0 2 Track Ingeegoodbee 0 12 1 0 2 Track Ingeegoodbee 0 13 2 0 2 Track Ingeegoodbee 0 14 2 0 2 Track Ingeegoodbee 0 15 1 1 2 Track Ingeegoodbee 0 16 1 0 2 Track Ingeegoodbee 0 17 0 0 2 Track Ingeegoodbee 1 18 0 0TOTAL 0 19 0 0 0 20 0 0 0 1 0 0 0 0 0 1 0 1 0 0 0 1 20 0 0 1 0 0 1 6 0 0 5 11 Seedlings Total Root sprouters no.
61 Site 1 Track Ingeegoodbee 1 Track Ingeegoodbee 1 Track Ingeegoodbee 01 1 Track Ingeegoodbee 02 1 Track Ingeegoodbee 03 1 Track Ingeegoodbee 04 1 1 Track Ingeegoodbee Quadrat 05 2 1 Track Ingeegoodbee 06 4 1 Track Ingeegoodbee 07 1 1 Track Ingeegoodbee 08 0 1 Track Ingeegoodbee 2 09 0 1 Track Ingeegoodbee 6 10 0TOTAL 0 11 0 0 12 3 0 0 8 0 0 4 0 0 1 1 0 0 0 0 0 12 0 0 0 0 0 0 9 0 1 8 17 Seedlings Total Seedlings Total Root Root sprouters sprouters no. no. Ingeegoodbee Track 3 Track Ingeegoodbee 3 Track Ingeegoodbee 3 Track Ingeegoodbee 22TOTAL 23 24Site 0 0Turnback Track 0Turnback TrackTurnback Track 0Turnback Track 24 0Turnback Track 01 0Turnback Track 02Turnback Quadrat Track 0 03 27Turnback Track 0 04Turnback Track 1 0 05Turnback Track 0 06Turnback Track 0 31 07Turnback Track 0 08Turnback Track 0 0 09TOTAL 0 0 58 10 4 0 11 3 0 12 1 2 0 13 0 0 0 0 3 0 0 0 0 0 1 0 13 0 0 4 0 3 0 14 2 0 0 3 0 0 1 14 Site Quadrat Seedlings Total Root sprouters no.
62 Site 3 Track Ingeegoodbee 3 Track Ingeegoodbee 3 Track Ingeegoodbee 01 3 Track Ingeegoodbee 02 3 Track Ingeegoodbee 03 3 Track Ingeegoodbee 04 3 3 Track Ingeegoodbee Quadrat 05 1 3 Track Ingeegoodbee 06 1 3 Track Ingeegoodbee 07 0 3 Track Ingeegoodbee 08 0 3 Track Ingeegoodbee 1 09 0 3 Track Ingeegoodbee 0 10 4 3 Track Ingeegoodbee 0 11 3 3 Track Ingeegoodbee 1 12 4 2 3 Track Ingeegoodbee 0 13 1 0 3 Track Ingeegoodbee 1 14 1 2 3 Track Ingeegoodbee 0 15 1 0 3 Track Ingeegoodbee 5 16 0 8 3 Track Ingeegoodbee 2 17 1 0 3 Track Ingeegoodbee 2 18 4 0 3 Track Ingeegoodbee 1 19 8 1 6 20 4 0 4 21 2 0 1 3 0 0 6 2 2 12 0 0 1 0 0 3 3 0 0 2 0 3 2 2 1E G:595798E Total refers to is rock outcrop rocky outcrop near base of spur). Transect Bearing: Transect spur). of base near outcrop rocky nd monitoring data. quadrats placed one metre apart along each transect; Root sprouters transect; each along apart metre one placed quadrats 2 square, red, ear tag (150m east of transect 005/2004).Site ngs refers to the number of seedlings recorded in eachquadrat;
Thesium australe West ° Appendix 8. tion; quadrat number refers to 1 m 16/03/2004. Date: 16/03/2004. West. ° 63 Stony Creek 2 (Permanent Monitoring Site:006/2004). 9kmalong track opposite Native Cat Track then 300m east track of (59590 270 with beginning west, north – east north runs Transect 5920125N). 300 Bearing: Transect spur. of base near Date: Site to the monitored refers popula Locations: Stony Creek 1 (Permanent Monitoring Site:005/2004). 2.9km along track opposite Native Cat Track, then 150m east track of (AM 2 tag (amongst ear red, with square, beginning west, – east runs ). Transect 5920173N refers to the of number plants regenerating vegetatively; Seedli the total number of number in eachplants quadrat. the of recorded total burnt. NB. were Neither sites 131415 016 017 0 0 0 11 0 0 0 0 0 0 0 0 11 Site no. Quadrat Root sprouters Seedlings Total Stony 1 Creek Stony 1 Creek Stony 1 Creek Stony 1 Creek Stony 1 Creek TOTAL 17Site 2 Creek Stony 01 2 Creek Stony 02 2 Creek Stony 03 2 Creek Stony no. Quadrat 32 04 2 Creek Stony Root sprouters 05 2 Creek Stony Seedlings 0 06 2 Creek Stony Total 7 07TOTAL 0 13 0 0 7 0 0 7 0 0 32 0 0 27 0 0 7 0 0 13 0 0 0 7 27 010203 204 005 606 007 0 1108 0 009 0 0 2 10 0 2 0 11 0 0 6 12 0 0 0 0 11 0 0 0 0 0 0 0 2 0 0 0 0 0 0
64 SiteStony 1 Creek Stony no. Quadrat 1 Creek Stony Root sprouters 1 Creek SeedlingsStony Total 1 Creek Stony 1 Creek Stony 1 Creek Stony 1 Creek Stony 1 Creek Stony 1 Creek Stony 1 Creek Stony 1 Creek Stony 1 Creek utton ear tags. utton ear monitoring data.
Barbarea grayi Appendix 9. + + + + + + 1 1 + + + + + 1 2 1 1 zelandiae - gunnianum sp.
Native Dog Flat (Permanent Monitoring Site: 007/2004).100m downstream of along River Buchan Black Mountain Road coming novae
sp. sp. sp. 65 Epilobium involucratus Euchiton Senecio Blechnum penna-marina Blechnum Geranium Barbarea grayi Barbarea Carex scorpioides Helichrysum Poa Acaena Rumex crispus Rumex Holcus lanatus vulgare Cirsium Prunella vulgaris repens Trifolium Hypochoeris radicata dubiumTrifolium
* * * * * * * Location: Location: b white 3 tag and ear red, 1 square, with marked is Quadrat N). 5915881 E 596865 (AMG: place fire from 15m - Gelantipy from 2m 6 x Size: Quadrat Site.Native Dog Flat 14Associated Species: Mature plants Cover/abundance Seedlings Total. 7 21 * = introduced species absent; 5E gelida long the walking . L laced proximately 500 m SW a 500 m proximately on Wirbill Plain. Ap Plain. Wirbill on Wirbill Plain21AAA Plain22AAA Plain23AAA Plain24AAA Plain30AAA Plain33AAA Wirbill PlainWirbill Plain 19Wirbill 20Wirbill Wirbill PWirbill PWirbill PlainWirbill Plain 25Wirbill Plain A 26Wirbill Plain A 27Wirbill Plain A 28Wirbill A 29Wirbill Plain A P Wirbill Plain P P 31Wirbill P P 32Wirbill Plain P P P 34 A P A A A P A A A A A A A A A Wirbill Plain 18 P A A Site Point 1 Transect 2 Transect 3 Transect 4 Transect t at 10 cm intervals along each transect where a steel rod was p was rod a steel where transect each along intervals cm t at 10 recorded; transect refers to one of four set at each up site; transect four of refers to one “A” = recorded; gelida . L ts the Nature Walk Track (480616E5930461N). monitoring data. ite outcrop, associated with a swampy area swampy a with associated ite outcrop,
Lobelia gelida present. gelida . L 3/06/2004. 18/02/2004. 66 Wirbill Plain1AAA Plain2AAA Plain3AAA Plain4AAA Plain5AAA Plain6AAA Plain8AAA Plain9AAA Plain11AAA Plain13AAA Wirbill Wirbill Wirbill Wirbill Wirbill Wirbill Wirbill PlainWirbill 7Wirbill Wirbill PlainWirbill 10 AWirbill PlainWirbill 12Wirbill Plain AWirbill Plain 14 AWirbill Plain P 15Wirbill Plain 16 P A 17 P P A P P P P P A A A A A A A Site Point 1 Transect 2 Transect 3 Transect 4 Transect “P” = perpendicular and presence/absence to the tape of Appendix 10. Site locations: gran a large of base At the Plain: Wirbill from where it intersec Wall, to thetrack Back Date: Rd. (48241 Tourist Buffalo Mt the on bridge the of north 100 m approx Brook, Crystal of west 10 m approximately Plain: Hospice 5935853N). Date: Site to the monitored refers point population; refers to a poin 54 67 71 0 TOTAL POINTS TOTAL A/PTOTAL 37/7 59/8 59/12 0 Wirbill PlainWirbill Plain 56Wirbill Plain 57Wirbill Plain 58Wirbill Plain 59Wirbill Plain 60Wirbill Plain 61Wirbill Plain 62Wirbill Plain 63 AWirbill Plain 64 AWirbill Plain 65 AWirbill Plain 66 AWirbill Plain 67 A AWirbill Plain 68 A AWirbill Plain 69 P AWirbill Plain 70 P A 71 P A P A A A A A A A P A P P P A Wirbill Plain 55 A A Site Point 1 Transect 2 Transect 3 Transect 4 Transect
67 Wirbill Plain36AAA Plain41AAA Plain43AAA Plain44AAA Plain45AAA Plain46AAA Plain47AAA Plain48AAA Plain49AAA Plain50AAA Plain51AAA Plain52AAA Plain53AAA Plain54AAA Wirbill PlainWirbill 35Wirbill PlainWirbill Plain P 37Wirbill Plain 38Wirbill Plain 39Wirbill P 40Wirbill Plain A PWirbill P 42Wirbill PWirbill AWirbill A A AWirbill AWirbill PWirbill A Wirbill A PWirbill A Wirbill A Wirbill Wirbill A Site Point 1 Transect 2 Transect 3 Transect 4 Transect TOTAL A/PTOTAL 16/16 33/26 14/20 9/15 Hospice PlainHospice PlainHospice 31 PlainHospice 32 PlainHospice 33 PlainHospice P 34 PlainHospice A 35 PlainHospice 36 PlainHospice 37 PlainHospice A 38 PlainHospice A 39 PlainHospice 40 P PlainHospice 41 P PlainHospice A 42 P PlainHospice P 43 P PlainHospice 44 A PlainHospice P 45 P PlainHospice P 46 P PlainHospice 47 P PlainHospice 48 A PlainHospice 49 P PlainHospice 50 P PlainHospice 51 A PlainHospice 52 P PlainHospice 53 P PlainHospice 54 P PlainHospice 55 P PlainHospice 56 P PlainHospice 57 P PlainHospice 58 A 59 P P P P P A A P TOTAL POINTSTOTAL 32 59 34 24
68 Hospice Plain2AAAA Plain5AAAP Plain6PPPP Plain7AAAP Plain9AAAP Plain12AAAP Plain14PPPA Plain16AAAA Plain19AAAP Plain27AAA PlainHospice Plain30PPP Hospice 1 PlainHospice PlainHospice 3Hospice 4 PHospice Hospice A PlainHospice PHospice 8 PlainHospice P PlainHospice 10 PHospice 11 A A PlainHospice Hospice A P 13 PlainHospice A PHospice 15 A P PlainHospice P PlainHospice P A 17Hospice A P 18 PlainHospice P P PlainHospice P P A 20 PlainHospice P P 21 PlainHospice P A 22 PlainHospice P 23 P PlainHospice A A P 24 PlainHospice P A 25 P Hospice A A P 26 PlainHospice P A PlainHospice A A P A 28Hospice A P A 29 A A A P A A P A A P A P P P A P A P A P A P A A P Site Point 1 Transect 2 Transect 3 Transect 4 Transect Site Point 1 Transect 2 Transect 3 Transect 4 Transect State 500 (cm) Max Height nce from zero nce from level to the highest (m) Y co-ordinate (m) to the distance from ground to the distance from monitoring data. 111 111 121 131 141 8.5 151 9.6 161 13.2 171 13.55 18 13.9 19 1.1E 15.3 20 1.93E 15.6 1.0W 17.55 2.0W 28.8 0.53E 28.8 1.03W 80 195 0.33W 170 0.17E 150 1.59E 250 S S 165 2.1E S 165 S 90 S S 110 S 110 S S S Transect Plant No X co-ordinate litters Creek along the Limestone - Black Mountain Rd, then about about Rd, then Mountain Black - Limestone the along Creek litters ansect; Max. height refers State e number assigned to each tagged plant; X co-ordinate is the dista e number
Acacia nanopravissima (cm) = buds, S sterile). Max Height ance perpendicular to the tr (m) Y co-ordinate fe history state (B Appendix 11. (m) Splitters Creek. Approx 250 m south from the bridge over Sp over bridge the from south 250 m Approx Creek. Splitters 609198E 5905249N 609198E 20/04/2004.
111 11 21 31 41 2.94 51 2.98 61 3.04 71 3.28 869 3.48 0.25W 9 3.48 10 0.24W 3.48 0.1W 3.58 0.24W 3.65 190 4.2 0 0.62W 125 0.74W 85 0.71W B 40 0.72W B 1.72W 195 175 210 B B 120 115 B B 185 B B B B Transect Plant No X co-ordinate Location: m south west to just before the first drainage line (609193E 5905252N). Date: 1: Transect Start End 609168E5905251N 2: Transect Start 609223E 5905218N End 609214E 5905248N 20m. and 10m at stake wooden a and end each at stake a metal with long, 30 m is transect Each is th 1 or 2; plant number Transect refers to transect number along the transect; Y co-ordinate is dist point of the plant; State refers to li 2222 12 22 32 42 52 0.25 62 0.56 72 1.4 82 10.1 92 15.4 10 15.552 0.75N 11 15.552 1.82S 12 15.652 13 0.1N2 15.8 14 1.2S 16.352 2.55N 15 16.44 1.1N2 175 16 16.9 1.75N2 17 330 21.7 0.22S 18 21.95 295 2.86S 2.05S 19 22.1 135 0.38N 155 20 B 24 270 26.4 0.75N 220 B 27.95 110 3.3S 2.63S 28.67 B 275 S 29.45 170 2.35S B 280 B B 1.64S 1.92N 145 0.23N S 0.32S 310 100 B B 0.73N B 175 S 195 115 155 B S 100 200 B B S B B B 70 Transect Plant No X co-ordinate (m) Y co-ordinate (m)Height Max (cm) State