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Species at Risk Public Registry - Recovery Strategy for the Dromedary Jumping-slug (Hemphillia dromedarius) in Canada [Final Version]
Recovery Strategy for the Dromedary Jumping-slug (Hemphillia dromedarius) in Canada [Final Version]
Parks Canada Agency. 2017. Recovery Strategy for the Dromedary Jumping-slug (Hemphillia dromedarius) in Canada. Species at Risk Act Recovery Strategy Series. Parks Canada Agency, Ottawa. 2 parts, 32 pp + 31 pp + Appendices.
For copies of the recovery strategy, or for additional information on species at risk, including the Committee on the Status of Endangered Wildlife in Canada (COSEWIC) Status Reports, residence descriptions, action plans, and other related recovery documents, please visit the Species at Risk (SAR) Public RegistryFootnote1.
Cover illustration: © Kristiina Ovaska
« Programme de rétablissement de la limace-sauteuse dromadaire (Hemphillia dromedarius) au Canada »
ISBN no. 978-0-660-08928-7
Catalogue no. En3-4/258-2017E-PDF
Under the Accord for the Protection of Species at Risk (1996), the federal, provincial, and territorial governments agreed to work together on legislation, programs and policies to protect wildlife species at risk throughout Canada.
In the spirit of cooperation of the Accord, the Government of British Columbia has given permission to the Government of Canada to adopt the Recovery Strategy for Dromedary Jumping-slug (Hemphillia dromedarius) in British Columbia (Part 2) under Section 44 of the Species at Risk Act (SARA). Parks Canada Agency has included a federal addition (Part 1) which completes the SARA requirements for this recovery strategy.
The federal recovery strategy for the Dromedary Jumping-slug in Canada consists of two parts:
Part 1 – Federal Addition to the Recovery Strategy for Dromedary Jumping-slug (Hemphillia dromedarius) in British Columbia, prepared by the Parks Canada Agency.
Part 2 – Recovery Strategy for Dromedary Jumping-slug (Hemphillia dromedarius) in British Columbia, prepared by the British Columbia Ministry of Environment.
Part 1 – Federal Addition to the Recovery Strategy for Dromedary Jumping-slug (Hemphillia dromedarius) in BritishColumbia, prepared by the Parks Canada Agency
3. Threats Assessment from COSEWIC
5.1. Identification of critical habitat
5.2. Examples of activities likely to result in destruction of critical habitat
5.3. Schedule of studies to identify critical habitat
Appendix A: Critical Habitat Identification Background
Part 2 – Recovery Strategy for Dromedary Jumping-slug (Hemphillia dromedarius) in British Columbia, prepared by the British Columbia Ministry of the Environment
The federal, provincial, and territorial government signatories under the Accord for the Protection of Species at Risk (1996)Footnote 2agreed to establish complementary legislation and programs that provide for effective protection of species at risk throughout Canada. Under the Species at Risk Act (S.C. 2002, c.29) (SARA), the federal competent ministers are responsible for the preparation of recovery strategies for listed Extirpated, Endangered, and Threatened species and are required to report on progress within five years after the publication of the final document on the Species at Risk Public Registry.
The Minister of Environment and Climate Change and the Minister responsible for the Parks Canada Agency is the competent minister for the Dromedary Jumping-slug and has prepared the federal component of this recovery strategy (Part 1), as per section 37 of SARA. To the extent possible, it has been prepared in cooperation with the Province of British Columbia and Environment and Climate Change Canada, with input from Indigenous Peoples, environmental non-governmental organizations and local industrial groups, as per section 39(1) of SARA. SARA section 44 allows the Minister to adopt all or part of an existing plan for the species if it meets the requirements under SARA for content (sub-sections 41(1) or (2)). The Province of British Columbia provided the attached recovery strategy for the Dromedary Jumping-slug (Part 2) as science advice to the jurisdictions responsible for managing the species in British Columbia. It was prepared in cooperation with the Parks Canada Agency and Environment and Climate Change Canada.
Success in the recovery of this species depends on the commitment and cooperation of many different constituencies that will be involved in implementing the directions set out in this strategy and will not be achieved by Environment and Climate Change Canada, the Parks Canada Agency, or any other jurisdiction alone. All Canadians are invited to join in supporting and implementing this strategy for the benefit of the Dromedary Jumping-slug and Canadian society as a whole.
In the case of critical habitat identified for terrestrial species including migratory birds SARA requires that critical habitat identified in a federally protected areaFootnote 3 be described in the Canada Gazette within 90days after the recovery strategy or action plan that identified the critical habitat is included in the public registry. A prohibition against destruction of critical habitat under ss. 58(1) will apply 90days after the description of the critical habitat is published in the Canada Gazette.
The federal supplementary material to the Province of British Columbia’s Recovery Strategy for the Dromedary Jumping-slug (Hemphillia dromedarius) in British Columbia was produced by the Parks Canada Agency, with support from the British Columbia Invertebrates Recovery Team and Vanessa Craig of Ecologic Research Ltd. In particular, the Parks Canada Agency would like to acknowledge the science support provided by the following recovery team members: Trudy Chatwin, Jennifer Heron, Suzie Lavallee, Kristiina Ovaska and Lennart Sopuck. Helpful comments and input were also provided by Kim Borg, Megan Harrison, Kella Sadler and Dan Shervill. The federal supplementary material was reviewed by the Province of British Columbia. Tyler Innes, Jackie Churchill and Tania Tripp of Madrone Environmental Ltd. assisted with mapping of critical habitat polygons.
The following sections have been included to address specific requirements of the federal Species at Risk Act (SARA) that are not addressed in the Recovery Strategy for Dromedary Jumping-slug (Hemphillia dromedarius) in British Columbia (Part 2 of this document, referred to henceforth as “the provincial recovery strategy”) and/or to provide updated or additional information.
1. COSEWICSection 1 note * Species Assessment Information
This updated COSEWIC species assessment (COSEWIC 2014) replaces the COSEWIC species assessment information provided in the provincial recovery strategy.
Date of Assessment: May2014
This relatively large slug is a member of a small group of slugs that are found globally only in western North America. In Canada, despite a great deal of searching, this species is known from fewer than 20 sites on southern Vancouver Island. There, it is restricted to moist, older-growth (&gt;80 years old) forests. Populations are invariably small, and are fragmented by intervening logged areas and by the species’ poor dispersal ability. Threats include further loss and fragmentation from forestry and the increased frequency and severity of droughts associated with climate change.
COSEWIC Status History: Designated Threatened in May2003. Status re-examined and confirmed in May2014.
Section 1 note *
Return to section 1 note * referrer
This section updates the Populations and Distribution section of the provincial recovery strategy.
The provincial recovery strategy lists 15 locations and COSEWIC (2014) lists 19 locations of Dromedary Jumping-slug in British Columbia. This federal recovery strategy considers 18 locationsFootnote 4. Two of the locations in the provincial recovery strategy and COSEWIC (2014), Rainforest A and B Trail, are considered as one location in this federal recovery strategy because a single threatening event could affect all individuals at Rainforest A and B Trail (International Union for Conservation of Nature and Natural Resources (IUCN) 2012) and slug observations at Rainforest A and B Trail are less than 1km apart (NatureServe 2011). The further discrepancy between the number of locations in the three documents is due to the discovery of four new locations (Site ID No. 11, 17, 18, 19 in Table 2 below from COSEWIC 2014) since the provincial recovery strategy was completed in 2008. This federal recovery strategy adopts the Site ID numbers used in COSEWIC (2014) which differ slightly from those presented in the provincial recovery strategy.
This section updates the Threats section of the provincial recovery strategy by providing an updated summary of threats facing the species, as provided by COSEWIC (2014). For more detailed information on threats, see COSEWIC (2014).
Table 1. Threats calculator assessment.
ImpactTable 1 note a
ScopeTable 1 note b
SeverityTable 1 note c
TimingTable 1 note d
Residential & commercial development Low Small Extreme High (Continuing)
Housing & urban areas Low Small Extreme High (Continuing)
Tourism & recreation areas Negligible Negligible Serious Moderate
Energy production & mining Negligible Negligible Extreme High (Continuing)
Mining & quarrying Negligible Negligible Extreme High (Continuing)
Transportation & service corridors Low Restricted-Small Slight High (Continuing)
Roads & railroads Low Restricted-Small Slight High (Continuing)
Utility & service lines Negligible Negligible Negligible High (Continuing)
Biological resource use Medium Restricted Extreme High (Continuing)
Logging & wood harvesting Medium Restricted Extreme High (Continuing)
Human intrusions & disturbance Low Restricted-Small Slight High (Continuing)
Recreational activities Low Restricted-Small Slight High (Continuing)
Natural system modifications Negligible Negligible Extreme High (Continuing)
Fire & fire suppression Negligible Negligible Extreme Low
Dams & water management/use Negligible Negligible Moderate High (Continuing)
Invasive & other problematic species & genes Medium-Low Restricted Moderate-Slight High (Continuing)
Invasive non-native/alien species Medium-Low Restricted Moderate-Slight High (Continuing)
Pollution Negligible Negligible Slight High (Continuing)
Agricultural & forestry effluents Negligible Negligible Slight High (Continuing)
Geological events Low Small Extreme-Serious High-Moderate
Earthquakes/tsunamis Low Small Extreme Moderate
Avalanches/landslides Negligible Negligible Extreme-Serious High (Continuing)
Climate change & severe weather Medium-Low Pervasive Moderate-Slight High (Continuing)
Habitat shifting & alteration Unknown Unknown Unknown
Droughts Medium-Low Pervasive Moderate-Slight High (Continuing)
Storms & flooding Low Small Moderate High (Continuing)
Scope – Proportion of the species that can reasonably be expected to be affected by the threat within 10 years. Usually measured as a proportion of the species’ population in the area of interest. (Pervasive = 71–100%; Large = 31–70%; Restricted = 11–30%; Small = 1–10%; Negligible &lt; 1%).
Severity – Within the scope, the level of damage to the species from the threat that can reasonably be expected to be affected by the threat within a 10-year or three-generation timeframe. Usually measured as the degree of reduction of the species’ population. (Extreme = 71–100%; Serious = 31–70%; Moderate = 11–30%; Slight = 1–10%; Negligible &lt; 1%; Neutral or Potential Benefit ≥ 0%).
Table 2. Updated threats assessment (adapted from COSEWIC 2014).
Threat Sub-categories
8.1 Invasive non-natives
10.2 Earthquakes, tsunamis
Shawnigan Lake X X X X? X X
Mt. Arrow-smith, Mt. Cokely X X X X X
Mt. Arrow-smith, McBey Cr X X X X
Mt. Brenton X X X X? X X
Mt. Hooper X X X X? X X
Juan de Fuca Prov. Park, Loss Creek X X X X X
Thrasher Cove X X
Clo-oose X X X X X
Keeha Beach Trail X X X X
Bamfield X X X X X X X
Bamfield Marine Station X X X X? X X
Willow-brae X X X X X
Indian Creek X X X X? X X
Goldmine Trail X X X
Rainforest A Trail X X X X
Rainforest B Trail X X X
Highway SE of Pacific Rim NPR border X X X X X
Highway right at the Pacific Rim NPR border X X X X
Tyhistanis, near Pacific Rim NPR X X X X
Total number of sites 3 2 14 8 14 1 13 4 3 5 19 5
% of sites 16 11 74 42 74 5 68 21 16 26 100 26
This section replaces the “Recovery Goal” in the provincial recovery strategy. The federal population and distribution objective for Dromedary Jumping-slug is to:
Ensure the survival of Dromedary Jumping-slug by maintaining the species at its current area of occupancy across its extent of occurrence in Canada.
The federal population and distribution objective is designed to be consistent with the recovery goal in the provincial recovery strategy. The objective is centered on species survival to ensure no further species decline in Canada until sufficient data on species life history, population size and distribution is available to determine a quantitative population and distribution objective for species recovery.
Currently, the known extent of occurrence is estimated at 6,695km2 (COSEWIC 2014). This is an increase of 68% from the previous value of 3985km2 (COSEWIC 2003), a result of further surveys expanding the known range.
The current area of occupancy is not known with certainty. COSEWIC (2014) estimated the area of occupancy for this species to range from 72km2 to 2,000km2. The estimate of 72km2 is an underestimate because it assumes that the species only occurs near the known observations. COSEWIC (2014) also provided an estimate of 400km2. This is also an underestimate because it assumes the species only occurs on the coast of Vancouver Island when in fact several locations are known from inland areas. Given the estimated extent of occurrence in Canada of 6,695km2, the species’ patchy distribution and specific habitat requirements, COSEWIC (2014) concluded that the area of occupancy will likely not exceed 2,000km2. An activity to address this knowledge gap is included in Table 5.
The critical habitat identified in this recovery strategy for 14 Dromedary Jumping-slug locations (Table 3) is based on the best available information and is considered to be a partial identification of critical habitat because:
Currently available information is insufficient to identify critical habitat for three locations where the slug was observed on human-made structures,
The current critical habitat identification (255 ha) is considerably less than the estimated area of occupancy for this species of between 72km2 to 2,000km2(COSEWIC 2014), and
Some critical habitat has not been identified due to ongoing cooperation and consultation. The Government of Canada will continue to work cooperatively with applicable organizations to complete the identification of critical habitat.
A schedule of studies (Table 5) has been developed to provide the information necessary to complete the identification of critical habitat that will be sufficient to meet the population and distribution objective.
5.1.1. Geospatial location of areas containing critical habitat
Critical habitat is identified for 14 Dromedary Jumping-slug locations on southern Vancouver Island, British Columbia (Table 3). Three conservation principles were used to identify critical habitat:
The habitat included should be representative of habitat in which Dromedary Jumping-slug is known to occur,
Habitat areas should be large enough to maintain a Dromedary Jumping-slug population at each location, and
If multiple records of Dromedary Jumping-slug have been documented within the same location, they should be connected with corridors to facilitate potential movement of individuals within the location area.
See Appendix A for more detail on these principles.
The three conservation principles guided the creation and use of the following protocol to identify Dromedary Jumping-slug critical habitat:
Terrestrial Ecosystem Mapping, a high resolution habitat mapping method standardized for British Columbia (B.C. Ministry of Environment 2006; RIC 1998), was used to identify habitat types at and near to Dromedary Jumping-slug observation locations.
The primary forest ecotypesFootnote 5 and their age (age defined as per structural stages in RIC 1998) associated with each Dromedary Jumping-slug observation were identified at each location. The age-specific primary forest ecotypes documented across all locations (defined broadly across locations, not specific to individual locations) were defined as suitable habitat for the species.
At each location, all suitable habitat (based on the age-specific primary forest ecotypes) was mapped to a radius of 500m from the centre of each Dromedary Jumping-slug location. This radius was chosen solely to ensure sufficient data availability, even in areas with patchy habitat.
For each individual slug location, contiguous suitable habitat was selected until a target area of 20 ha was reached or no more contiguous suitable habitat was available. Where there was greater than 20 ha of suitable habitat within 500m, suitable habitat was selected so as to minimize fragmentation and edge effect (i.e., to minimize the edge/volume ratio).
The target of 20 ha, used to map critical habitat, reflects the biological needs of the species (i.e., observed dispersing away from occupied areas and low densities; COSEWIC 2014) and will provide a reasonable probability of persistence for known Dromedary Jumping-slug locations. See Appendix A for further details on rationale for the target area of 20 ha.
The age of forest stands was used to map critical habitat because the species has most often been found in mature and old-growth forests (Appendix A; COSEWIC 2014; Part 2). In mapping critical habitat, efforts were made to keep all habitat contiguous (to maintain connectivity within the location) and to minimize edge effects by keeping the edge/volume ratio of the critical habitat polygon as low as possible. For this reason, suitable habitat was added from the centre (observation location) outwards, with no gaps and avoiding long or linear patches of habitat that would have a high edge/volume ratio. See Appendix A for further details on how this protocol was applied to specific locations.
Critical habitat polygons at Mount Cokely and Mount Brenton are significantly smaller than the target of 20 ha because 20 ha of contiguous suitable habitat was not available around these locations at the time critical habitat was mapped. It is unclear whether polygons with significantly less than 20 ha of critical habitat identified will be viable over the long term (Appendix A). As forests around locations with small areas of critical habitat grow older, additional habitat may become suitable and be identified as additional critical habitat.
The Dromedary Jumping-slug occurs in both high elevation ‘cloud’ forests and low elevation ‘fog’ forests that share the following general biophysical attributes (COSEWIC 2014; Part 2):
a well-developed forest canopy (provides cover, shade, and maintains moisture in the forest),
a productive understory (e.g., understory trees, abundant moss and shrubs) that provides for moist micro-climate on the forest floor and cover for the species,
abundant coarse woody debris, especially of a large diameter (i.e., &gt; 50cm diameter), that provides for moist micro-climate on the forest floor, cover for the species, and hidden travel corridors and micro-sites, and
a structurally complex forest floor (e.g., hummocks and cavities) that provides a moist micro-climate on the forest floor, cover for the species, and hidden travel corridors and micro-sites.
The species has most often been found in mature or old forests (those &gt; 80 years old), likely because the above attributes typically take time to develop as forests age, though has occasionally been found in younger forests (Table 3).
In addition to the above general description of the biophysical attributes of critical habitat, Terrestrial Ecosystem Mapping (RIC 1998) primary forest ecotypes and their age class (‘structural stage’ as per RIC 1998) of occupied forests were used to define the biophysical attributes of critical habitat, as outlined in Table 3.
The above biophysical attributes of critical habitat contribute to providing sufficient habitat for foraging, cover, travel, hibernation and reproduction (COSEWIC 2014; Part 2).
The areas containing critical habitat for the Dromedary Jumping-slug are presented in Figures 1-14. Within the area identified as containing critical habitat for Dromedary Jumping-slug, critical habitat is identified wherever any of the above biophysical attributes occur.
Table 3. List of locations with critical habitat identified for Dromedary Jumping-slug, the biogeoclimatic zone in which the location occurs (BECZone), the size of the critical habitat polygon identified for the location, and the primary forest ecotypes that define the biophysical attributes within each critical habitat polygon (ecology and age). Adapted from Churchill et al. (2010).
Site ID No.Table 3 note 1
BEC zoneTable 3 note 2
Critical habitat polygon area (ha)
Primary forest ecotypesTable 3 note 3in critical habitat polygons
EcotypeTable 3 note4
Structural StageTable 3 note5
Shawnigan Lake Figure 1 700 CWHmm2 21 HD, AP 5, 6, 7
Mt.Arrowsmith- Mt.Cokely Figure 2 1200 MHmm1 3 MB 7
Mt.Arrowsmith- McBey Cr. Figure 3 &gt; 950 MHmm1 20 MB 7
Mt.Brenton Figure 4 &gt; 1000 MHmm1 3 MB 6
Mt.Hooper Figure 5 850 MHmm1 20 MB, YS, MT 7
Juan de Fuca Prov. Park, Loss Creek Figure 6 &lt;150 CWHvm1 20 HD, AB, AD 5, 6, 7
Thrasher Cove Figure 7 &lt; 100 CWHvm1 20 AB 7
Clo-oose Bay Figure 8 10 CWHvh1 20 HS 6, 7
Keeha Beach Trail, PRNPR Figure 9 20 CWHvh1 20 HS 7
Bamfield Figure 10 30 CWHvh1 20 HS 4, 5, 6, 7
Bamfield Marine Station N/A &lt; 50 CWHvh1 TBDTable 3 note *
Willowbrae Figure 11 30 CWHvh1 22 HS 6, 7
Indian Creek Figure 12 &lt; 50 CWHvh1 18 HS, SD 6
Goldmine Trail, PRNPR Figure 13 &lt; 30 CWHvh1 20 HS 6, 7
Rainforest A and B Trail, PRNPR Figure 14 &lt; 40 CWHvh1 28 HS, SD 7
Hwy SE of PRNPR border N/A 40 CWHvh1 TBDTable 3 note *
Hwy at PRNPRborder N/A 40 CWHvh1 TBDTable 3 note *
Ty-histanis N/A &lt; 100 CWHvh1 TBDTable 3 note * HS 6, 7
Some critical habitat has not been identified due to insufficient available information or ongoing cooperation and consultation (see schedule of studies in Table 5).
Location ID numbers as per COSEWIC (2014).
Biogeoclimatic (BEC) zones as per Ministry of Forests and Range (2012).
Primary forest ecotypes were defined as forest ecotypes (RIC 1998) that comprised at least 25% of habitat polygons in which Dromedary Jumping-slug location records were observed (see Section 5.1.1 and Appendix A for details).
Listed primary forest ecotypes are: HD = Western Hemlock/Amabalis Fir-Deer Fern; AP = Western Hemlock/Amabalis Fir-Pipecleaner Moss; AB = Western Hemlock/Amabalis Fir-blueberry/Salal; AD = Amabalis Fir / Sitka Spruce - Devil’s Club; HS = Western Redcedar/Western Hemlock-Salal; MB = Mountain Hemlock/Amabalis Fir-blueberry; SD = Western Redcedar/Sitka Spruce-Devil’s Club; YS = Mountain Hemlock / Yellow Cedar - Sphagnum; MT = Amabalis Fir / Mountain Hemlock - Twistedstalk; (RIC 1998).
Structural stages of dominant ecotype polygons, as follows: 4, forest &lt; 40 years old; 5, forest 40-80 years old; 6, forest 80-250 years old; 7, forest &gt;250 years old (RIC 1998).
Figure 1. Critical habitat (21 ha) for Dromedary Jumping-slug at Shawnigan Lake.
Figure 2. Critical habitat (3 ha) for Dromedary Jumping-slug at Mount Arrowsmith – Mount Cokely.
Figure 3. Critical habitat (20 ha) for Dromedary Jumping-slug at Mount Arrowsmith – McBey Creek.
Figure 4. Critical habitat (3 ha) for Dromedary Jumping-slug at Mount Brenton.
Figure 5. Critical habitat (20 ha) for Dromedary Jumping-slug at Mount Hooper.
Figure 6. Critical habitat (20 ha) for Dromedary Jumping-slug at Juan de Fuca Park, Loss Creek.
Figure 7. Critical habitat (20 ha) for Dromedary Jumping-slug at Thrasher Cove.
Figure 8. Critical habitat (20 ha) for Dromedary Jumping-slug at Clo-oose Bay.
Figure 9. Critical habitat (20 ha) for Dromedary Jumping-slug at Keeha Beach Trail.
Figure 10. Critical habitat (20 ha) for Dromedary Jumping-slug at Bamfield.
Figure 11. Critical habitat (22 ha) for Dromedary Jumping-slug at Willowbrae.
Figure 12. Critical habitat (18 ha) for Dromedary Jumping-slug at Indian Creek.
Figure 13. Critical habitat (20 ha) for Dromedary Jumping-slug at Goldmine Trail.
Figure 14. Critical habitat (28 ha) for Dromedary Jumping-slug at Rainforest A & B Trail.
Understanding what constitutes destruction of critical habitat is necessary for the protection and management of critical habitat. Examples of activities likely to destroy critical habitat are provided below (Table 4); however, destructive activities are not limited to those listed. Destruction is determined on a case by case basis. Destruction would result if part of the critical habitat were degraded, either permanently or temporarily, such that it would not serve its function when needed by the species. Destruction may result from single or multiple activities at one point in time or from cumulative effects over time. It is important to note that some works or activities performed outside critical habitat have the potential to destroy critical habitat especially if they alter ecological dynamics and ecological processes (e.g., through edge effects or introduction of exotic plants or animals) such that the critical habitat attributes are no longer present to support the species.
It is recognized that existing facilities and land uses in and adjacent to critical habitat already affect critical habitat, to various degrees, and may decrease the quality of certain portions of critical habitat that remain in the area. Lower quality or sub-optimal areas are nonetheless included as critical habitat because they still serve a biological function for the species (e.g., shading). Any new, additional, or increases in activity (including the construction of new facilities) inside or outside of critical habitat polygons may cause destruction of critical habitat. Some human activities in or adjacent to critical habitat will require careful assessment for possible effects, including cumulative effects on critical habitat and the potential for destruction.
Table 4. Examples of activities likely to result in destruction of critical habitat of the Dromedary Jumping-slug.
Works or activities within the boundaries of critical habitat
Works or activities within critical habitat that result in loss of forest canopy cover (e.g., typically larger developments such as logging, building houses, golf courses, mineral or aggregate extraction, building roads, wide trails or transmission lines).
Forest clearing results in the loss of forest canopy cover (reducing cover, shade and moisture for the forest floor). It is also likely to result in a change to the overall age of the forest stand and may alter the ecotype of the habitat (see Table 3), making it less suitable for the species. Forest clearing may also result in the direct or indirect loss of other important biophysical attributes: such as a productive understory (e.g., small trees, shrubs, moss), abundant coarse woody debris (especially that with a large diameter), and a structurally complex forest floor (e.g., cavities, travel corridors) (COSEWIC 2014, Part 2).
In addition, such activities are likely to introduce alien invasive species which can affect habitat functions (e.g., exotic plants can alter food availability; COSEWIC 2014, Part 2).
Works or activities within critical habitat that do not affect the forest canopy but that still affect the understory, coarse woody debris, or forest floor structure (e.g., typically smaller developments such as small trails, platforms, kiosks).
Works that may not cause loss of the forest canopy may still result in the loss of important biophysical attributes: such as a productive understory (e.g., small trees, shrubs, moss), abundant coarse woody debris (especially that with a large diameter), and a structurally complex forest floor (e.g., cavities, travel corridors) (COSEWIC 2014, Part 2). These works may also alter the ecotype of the habitat (see Table 3), making the habitat less suitable for the species.
Application of herbicides and other chemicals within the boundaries of critical habitat. Chemical application can result in destruction of biophysical attributes such as moss or shrub cover, and food resource availability (e.g., fungus; COSEWIC 2014, Part 2).
Works or activities outside the boundaries of critical habitat
Forest clearing within 120m of critical habitat that results in loss of biophysical attributes within critical habitat (see above examples of works or activities resulting in a loss of forest canopy cover) Loss of well-developed forest canopy within 120m of critical habitat can affect critical habitat due to edge effects that reduce moisture on the forest floor for this species threatened by desiccation (COSEWIC 2014; Part 2). An edge in this context is defined as a gap in the forest that is wider than the average surrounding stand height and with a ‘hard’ edge (defined as where the average canopy height abruptly declines by at least 50%). This guideline is based on edge effects on soil moisture (Chen et al. 1995).
A list of studies and activities required for additional critical habitat to be identified for Dromedary Jumping-slug is included in Table 5.
Table 5. Studies and activities required for a full identification of critical habitat for Dromedary Jumping-slug.
Some critical habitat has not been identified due to ongoing cooperation and consultation. The Government of Canada will continue to work cooperatively with applicable organizations to complete the identification of critical habitat and will update this document as appropriate. Increased amount of critical habitat. On-going, pending progress respecting cooperation and consultation.
Conduct modelling to determine the area of occupancy for the species. Current mapping and the geography of known locations can be used to estimate the area of occupancy. This will allow for better quantification of the amount of critical habitat required to meet the population and distribution objective. 2017-2019
Survey areas surrounding the three Dromedary Jumping-slug locations where scientific information regarding natural habitat use is lacking. Scientific information available regarding natural habitat use; identification of critical habitat. 2017-2019
Conduct habitat modelling or mapping to allow for a range wide identification of suitable habitat for Dromedary Jumping-slug. Habitat modelling or mapping can be used to achieve a range wide critical habitat identification that will meet the population and distribution objective. 2020-2027
The “Socio-economic Considerations” section of the provincial document (Part 2) is not part of the federal recovery strategy for the Dromedary Jumping-slug (Hemphillia dromedarius) because socio-economic factors are not a consideration in the preparation of SARA recovery strategies (see section 41(1) of SARA).
This section modifies information in the Province of British Columbia’s Recovery Strategy for Dromedary Jumping-slug (Hemphillia dromedarius) in British Columbia (Part 2).
One or more action plans for the Dromedary Jumping-slug will be completed and posted on the Species at Risk Public Registry five years following the final posting of this recovery strategy.
A strategic environmental assessment (SEA) is conducted on all SARA recovery planning documents, in accordance with the Cabinet Directive on the Environmental Assessment of Policy, Plan and Program ProposalsFootnote6. The purpose of a SEA is to incorporate environmental considerations into the development of public policies, plans, and program proposals to support environmentally sound decision-making and to evaluate whether the outcomes of a recovery planning document could affect any component of the environment or any of the Federal Sustainable Development Strategy’sFootnote 7 (FSDS) goals and targets.
The recovery strategy identifies current threats to the Dromedary Jumping-slug and its habitat as well as current knowledge gaps. Recovery objectives clearly focus on resolving these threats and filling information gaps. Recommended activities may also benefit non-target species and the environment.
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COSEWIC. 2006. COSEWIC assessment and status report on the Blue-grey Taildropper, Prophysaon coeruleum in Canada. Committee on the Status of Endangered Wildlife in Canada. Ottawa. Vi + 27 pp. (http://www.registrelep-sararegistry.gc.ca/document/default_e.cfm?documentID=1023). [accessed September2016].
COSEWIC. 2014. COSEWIC assessment and status report on the Dromedary Jumping-slug Hemphillia dromedarius in Canada. Committee on the Status of Endangered Wildlife in Canada. Ottawa. xi + 59 pp. (www.registrelep-sararegistry.gc.ca/document/default_e.cfm?documentID=190). [accessed September2016].
Cowling, R.M., and W.J. Bond. 1991. How small can reserves be? An empirical approach in Cape Fynbos, South Africa. Biological Conservation 58:243-256.
Darnell, R.M., P.C. Lemon, J.M. Neuhold, and G.C. Ray. 1974. Natural areas and their role in land and water resource preservation. American Institute of Biological Sciences, Arlington, VA.
Dunk, J.R., Zielinski, W.J., and H.K. Preisler. 2004. Predicting the occurrence of rare mollusks in northern California forests. Ecological Applications, 14(3):713-729.
Edworthy, A.B., Steensma, K.M.M., Zandberg, H.M., and P.L. Lilley. 2012. Dispersal, home-range size, and habitat use of an endangered land snail, the Oregon forestsnail (Allogona townsendiana). Canadian Journal of Zoology, 90(7):875-884.
Environment and Climate Change Canada. 2016. Recovery Strategy for the Blue-grey Taildropper (Prophysaon coeruleum) in Canada.[Proposed]. Species at Risk Act Recovery Strategy Series. Environment and Climate Change Canada, Ottawa. 2 parts, 20 pp + 36 pp.
Grimm,B., and W. Paill. 2001. Spatial distribution and home-range of the pest slug Arion lusitanicus. Acta Oecologica, 22(4):219-227.
Harrison, S., and J. Voller. 1998. Connectivity. Pp. 76-97, in J. Voller and S. Harrison (eds). Conservation biology principles for forested landscapes. UBC Press, Vancouver.
Kappes, H., K. Jordaens, F. Hendrickx, J. Maelfait, L. Lens and T. Backeljau. 2009. Response of snails and slugs to fragmentation of lowland forests in NW Germany. Landscape Ecology 24:685-697.
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NatureServe. 2011. Population/occurrence delineation and viability criteria. www.natureserve.org/explorer/popviability.htm[accessed January2011].
RIC. 1998. Standards for Terrestrial Ecosystem Mapping in British Columbia.B.C. Ministry of Environment, Lands and Parks, Victoria. ISBN: 0-7726-3552-8.
Shafer, C. L. 1995. Values and shortcomings of small reserves. BioScience 45:80-88.
Steensma, K.M., Lilley, P.L., and H.M. Zandberg. 2009. Life history and habitat requirements of the Oregon forestsnail, Allogona townsendiana, in a British Columbia population. Invertebrate Biology, 128(3):232-242.
Taylor, P.D., L. Fahrig, K. Henein, and G. Merriam. 1993. Connectivity is a vital element of landscape structure. Oikos 68:571-573.
Three conservation principles guided the critical habitat identification and are described below:
1. The habitat included should be representative of habitat in which Dromedary Jumping-slug is known to occur.
The forest ecotypes and their ages at each Dromedary Jumping-slug location were recorded (Churchill et al. 2010). Dromedary Jumping-slugs have been discovered at sites composed of nine different forest ecotypes (Table 3), most commonly in mature or old forests (about 40 to &gt; 250 years old, most commonly &gt; 80 years old). When defining critical habitat polygons, only habitats composed of primary forest ecotypes and forest ages known to be suitable (across all locations) for Dromedary Jumping-slug were included.
2. Habitat areas should be large enough to maintain a Dromedary Jumping-slug sub-population at each location.
Although some terrestrial gastropods have home ranges varying from about 12m2 to 404m2, no literature is available that quantifies the size of habitat areas required to maintain viable Dromedary Jumping-slug locations (Grimm and Paill 2001; Edworthy et al. 2012). Oregon Forestsnails (Allogona townsendiana) in British Columbia had a mean home range size of 117m2 and existed at high densities – a mean of 1.0 snail per m2 (Steensma et al. 2009; Edworthy et al. 2012). Blue-grey Taildroppers (Prophysaon coeruleum)in British Columbia appear to typically exist at densities from 0.01 to 0.15 slugs per m2 (COSEWIC 2006). In California, Dunk et al. (2004) concluded that entire gastropod populations may be found in a 1 ha area. Dromedary Jumping-slugs, however, appear to occur at much lower densities than the species studied by the above authors and they may have larger home ranges than other local gastropods (COSEWIC 2014).
Some useful context for the size of reserves can be drawn from studies on other ecosystems and species. Twenty hectares has been recommended as a minimum size to maintain a specific habitat type (Darnell et al 1974; as cited in Shafer 1995). Other studies regarding the habitat areas required to ensure the persistence of small organisms have been for plants: bryophytes in British Columbia have been found to persist in as little as 3.5 ha of forest (Baldwin and Bradfield 2005), while herb species in South Africa required between 4 and 15 ha to persist (Cowling and Bond 1991).
Although few studies have quantified the area required for the persistence of small organisms, many studies have concluded that larger reserves increase the probability of persistence for organisms in general and for small organisms in particular (e.g., reviewed by Saunders et al. 1991; Shafer 1995). Some insect species were lost from experimental reserves in Brazil that were up to 10 ha in size and it was suspected that insect species may even be lost from reserves as large as 100 ha (Bierregaard et al. 1992). Similarly, in British Columbia, habitat reserves &gt; 100 ha were found to contain a greater abundance and diversity of gastropods (though no Dromedary Jumping-slugs were found) after logging, than reserves &lt; 2 ha (Ovaska and Sopuck, unpubl. manuscript).
To summarize, some terrestrial gastropods have small home ranges (e.g. Grimm and Paill 2001), or exist at high densities (e.g., Steensma et al. 2009), but these species appear to occur at much higher densities than Dromedary Jumping-slugs (COSEWIC 2014). Given that the Dromedary Jumping-slug is a mobile animal that occurs at low densities (and thus low population sizes), and has been observed dispersing away from occupied areas (COSEWIC 2014), it likely requires significantly larger areas than bryophyte and herb species that are not mobile, disperse primarily using seeds or spores and occur at relatively high densities. With this information in consideration, reserves of 15 ha or less may not provide for a strong probability of long term persistence for terrestrial gastropod populations.
To ensure that the critical habitat polygons in this recovery strategy provide a reasonable probability of persistence for known Dromedary Jumping-slug locations, a target size of 20 ha was chosen for critical habitat polygons.
A recently published recovery strategy for the Blue-grey Taildropper (another British Columbia gastropod; Environment and Climate Change Canada 2016) applied a slightly different approach to the identification of critical habitat than for the approach used here for Dromedary Jumping-slug. These approaches differ based on biological differences between the species (the Blue-grey Taildropper appears to have less dispersal capabilities and exists at higher densities than Dromedary Jumping-slug; COSEWIC 2006, COSEWIC 2014). However, both critical habitat approaches affect a similar amount of land base and protect a similar number of individuals (Parks Canada, unpubl. data). The Blue-grey Taildropper identification uses a smaller core area and a larger buffer (1.9 ha core and 240m buffer, versus 20 ha core and 120m buffer for Dromedary Jumping-slug), but the overall area affected is similar (estimated at 221 ha and 435 ha, respectively). Additionally, considering the different densities estimated for the two species (COSEWIC 2006, COSEWIC 2014), the core reserves (1.9 ha and 20 ha, respectively) will protect a similar number of individuals (protection estimated for 157 Blue-grey Taildroppers and 229 Dromedary Jumping-slugs; Parks Canada, unpubl. data).
For sites where 20 ha of suitable habitat is not currently available to be identified as critical habitat, adjacent areas should be restored so that sufficient suitable habitat will be available at a future date.
3. If multiple records of Dromedary Jumping-slug have been documented within the same location, they should be connected with corridors to facilitate potential movement of individuals within the location area.
Habitat connecting individuals in a location is important to increase the probability of persistence (Taylor et al. 1993; Harrison and Voller 1998). Due to the wide geographic separation of many of the Dromedary Jumping-slug locations on Vancouver Island, connectivity between locations is beyond the scope of this critical habitat identification. However, individuals within locations also require continuous habitat to allow for movement and to ensure gene flow (Harrison and Voller 1998). NatureServe (2011) considers terrestrial gastropod observations to be distinct locations if separated by at least 1km. Therefore critical habitat includes connecting habitat for Dromedary Jumping-slug records separated by &lt; 1km (i.e., those within a single location).
Using the three principles, the critical habitat identification protocol was applied to identify specific critical habitat areas for Dromedary Jumping-slug as follows:
The forest ecotypes surrounding Dromedary Jumping-slug locations were mapped using Terrestrial Ecosystem Mapping (TEM) methodology (RIC1998). The preferred method to define critical habitat polygons was to use mapping of habitat ecotypes on 1:10,000 to 1:20,000 scale orthophotos, supplemented with detailed ecological data collected during a site visit (Churchill et al. 2010). The TEM mapping protocol identified the forest ecotypes, areas of similar habitat based on forest structure and landform type, around each Dromedary Jumping-slug location (Churchill et al. 2010). Polygons were delineated on orthophotos and then digitized using ArcGIS software. During site visits, data were collected on forest conditions and changes in habitat within 250m of the Dromedary Jumping-slug location. Potential barriers to slug movement, such as the presence of a recent clear-cut, highway or water, as well as changes in forest structure or landform were used to identify polygon edges. Where site access was not possible critical habitat was mapped based only on habitat types visible on 1:10,000 to 1:20,000 scale orthophotos as described above, and focused on identifying areas of similar forest structure. Potential barriers to Dromedary Jumping-slug movement and changes in forest structure visible on the orthophotos were used to identify polygon edges.
The forest polygon in which a Dromedary Jumping-slug was found was identified as critical habitat, and the size and attributes of the area calculated. Age-specific forest ecotypes that comprised at least 25% of forest polygons with Dromedary Jumping-slug records were defined as primary ecotypes for the purposes of this critical habitat identification and assumed to represent suitable habitat for Dromedary Jumping-slug across all locations. The forest ecotypes and structural stages of surrounding polygons up to 500m away from the location were examined to identify other habitat polygons that contained primary ecotypes (500m radius was selected as a methodological consideration to ensure adequate mapping to reach 20 ha at each site).
Where available within 500m, contiguous polygons that contained primary ecotypes for the Dromedary Jumping-slug and addressed any outstanding deficits in the critical habitat polygon size were added one at a time until the critical habitat polygon reached or exceeded the target of 20 ha (or until there was no suitable ecologically relevant contiguous habitat in the surrounding area available for inclusion).
Due to the age of much of the imagery used in producing polygon boundaries (1984 to 2005), Google Earth imagery (dated from 2005 to 2010) was used where available to help ensure that suitable habitat was still present within the critical habitat polygon boundaries. Although the most recent ortho imagery available was used to verify the status of the habitat within critical habitat polygons, further forest harvesting or natural disturbance may have occurred in the area since the last date of imagery available or since field visits occurred.
Geographic Location details
This section describes the geographic location of each Dromedary Jumping-slug location and the corresponding critical habitat polygon.
Shawnigan Lake: The site is in a high-elevation (~700m) coniferous forest in the CWHmm2 subzone (Table 3). There is one observation record for this location, from 1999 (B.C. Conservation Data Centre 2010). The Shawnigan Lake critical habitat (Figure 1) occurs northwest of Shawnigan Lake. The critical habitat polygon is bounded to the north by forest of a younger structural stage, and to the northeast by a moist, rich ecotype not considered suitable for Dromedary Jumping-slug. Critical habitat for this location was mapped through interpretation of 1:15,0001988 colour orthophotos and in lieu of a site visit Google Earth imagery (18 August 2016) was used to verify critical habitat was still present within the polygon.
Mount Cokely, Mt. Arrowsmith: The site is in a mature Mountain Hemlock-Amabalis Fir high elevation (~1200m) forest in the MHmm1 subzone (Table 3). There is one observation record for this location, from 2006 (B.C. Conservation Data Centre 2010). The Mount Cokely critical habitat (Figure 2) is near Mount Arrowsmith Regional Park near a former ski area. Critical habitat for this location was mapped through interpretation of 1:16,0001990 black and white orthophotos and in lieu of a site visit Google Earth imagery (04August2012) was used to verify critical habitat was still present within the polygon. No additional habitat can be included in the critical habitat polygon because no contiguous suitable and representative habitat is currently available: the critical habitat polygon is bounded to the west by highly disturbed habitat and the rest of the surrounding habitat is too dry.
McBey Creek, Mt. Arrowsmith: The site is in a mature Western Hemlock-Amabalis Fir high elevation (&gt; 950m) forest in the CWHmm1 subzone (Table 3). There is one observation record for this location, from 2009 (B.C. Conservation Data Centre 2010). Critical habitat (Figure 3) for this location was mapped through interpretation of 1:16,0001990 black and white orthophotos and a detailed ecological assessment on a site visit on 01July2010.
Mount Brenton: The site is in a mature Western Hemlock-Amabalis Fir high elevation (&gt; 1000m) forest in the MHmm1 subzone (Table 3). There is one observation record for this location, from 2001 (B.C.Conservation Data Centre 2010). The Mount Brenton critical habitat (Figure 4) is near Holyoak Lake. Critical habitat for this location was mapped through interpretation of 1:15,0001998 colour orthophotos and in lieu of a site visit Google Earth imagery (18 August 2016) was used to verify critical habitat was still present within the polygon. At Mount Brenton no other suitable habitat is currently available for inclusion in the identification. Although the ecotype of some of the surrounding forest is considered suitable for Dromedary Jumping-slug (MB ecotype; Table 3), the forest is currently too young to be considered suitable for Dromedary Jumping-slug.
Mount Hooper: The site is in high-elevation (~850m) coniferous forest in the MHmm1 subzone (Table 3). There is one observation record for this location, from 2001 (B.C. Conservation Data Centre 2010). The Mount Hooper critical habitat (Figure 5) is 2.7km southeast of the summit of Mount Hooper, approximately 20km northwest of Youbou. Critical habitat for this location was mapped through photo interpretation of 1:20,0001984 black and white orthophotos and in lieu of a site visit Google Earth imagery (18 August 2016) was used to verify critical habitat was still present within the polygon.
Juan de Fuca Park, Loss Creek: The site is in low elevation (&lt; 150 m), mature Western Redcedar-Sitka Spruce forest in the CWHvm1 subzone (Table 3). There are two records for this location, from 2000 and 2001 (B.C. Conservation Data Centre 2010). The Juan de Fuca Provincial Park critical habitat (Figure 6) occurs southeast of Port Renfrew. The critical habitat polygon is bounded by riverine habitat to the north. Critical habitat was mapped at this location through interpretation of 1:10,000 2005 colour orthophotos and a detailed ecological assessment on a site visit on 25 August 2010..
Thrasher Cove: The site is in old-growth Western Redcedar-Western Hemlock low elevation (&lt; 100 m) forest in the CWHvm1 subzone (Table 3). There are eight records for this location, from 2004 (B.C.Conservation Data Centre 2010). The Thrasher Cove critical habitat (Figure 7) occurs on the West Coast Trail northwest of Port Renfrew in Pacific Rim National Park Reserve. Critical habitat was mapped at this location through interpretation of 1:20,000 1992 colour orthophotos and a detailed ecological assessment on a site visit on 24 August 2010..
Clo-oose Bay: The site is in mature Western Redcedar-Western Hemlock low elevation (&lt; 100m) forest in the CWHvh1 subzone (Table 3). There is one observation record for this location, from 2004 (B.C.Conservation Data Centre 2010). The Clo-oose critical habitat (Figure 8) occurs along the West Coast Trail near Clo-oose Bay. Critical habitat for this location was mapped through interpretation of 1:20,0001992 colour orthophotos and a detailed ecological assessment on a site visit on 12August2010.
Keeha Beach Trail, PRNPR: The site is in mature Western Redcedar-Western Hemlock low elevation (&lt; 100m) forest in the CWHvh1 subzone (Table 3). There is one observation record for this location, from 2006 (B.C. Conservation Data Centre 2010). The Keeha Beach Trail critical habitat (Figure 9) is near Cape Beale. Critical habitat for this location was mapped through interpretation of 1:10,0001989 colour orthophotos and a detailed ecological assessment on a site visit on 06August2010.
Bamfield: The site is in a low-elevation (&lt; 30m) old-growth/second-growth Western Redcedar-Western Hemlock forest in the CWHvm1 subzone (Table 3). There is one observation record for this location from 2000 (B.C. Conservation Data Centre 2010). The Bamfield critical habitat (Figure 10) is within the Village of Bamfield. Critical habitat for this location was mapped through interpretation of 1:10,0001989 colour orthophotos and in lieu of a site visit Google Earth imagery (17June2004) was used to verify critical habitat was still present within the polygon.
Willowbrae: The site is in an old-growth Western Redcedar-Western Hemlock low elevation (&lt; 100m) forest in the CWH vh1 subzone (Table 3). There is one observation record for this location, from 2006 (B.C. Conservation Data Centre 2010). The Willowbrae critical habitat (Figure 11) occurs along the Willowbrae trail in Pacific Rim National Park Reserve. Critical habitat for this location was mapped through interpretation of 1:20,0001992 colour orthophotos and a detailed ecological assessment on a site visit on 24August2010.
Indian Creek:The site is in mature Western Redcedar-Western Hemlock low elevation (&lt; 100m) forest in the CWHvh1 subzone (Table 3). There is one observation record for this location, from 2001 (B.C.Conservation Data Centre 2010). The Indian Creek critical habitat (Figure 12) is at Kennedy Flats, near Ucluelet. Critical habitat for this location was mapped through interpretation of 1:15,0001996 colour orthophotos and a detailed ecological assessment on a site visit on 24June2010. Google Earth imagery (13August2010) showed substantial forest harvesting after the 2010 field visit to the site. To avoid as much impacted habitat as possible, the critical habitat delineation was modified to better represent the extent/distribution of remaining suitable habitat.
Goldmine Trail, PRNPR:The site is in an old-growth Western Redcedar-Western Hemlock low elevation (&lt; 100m) forest in the CWHvh1 subzone (Table 3). There are two observation records for this location, from 2003 and 2004 (B.C. Conservation Data Centre 2010). The Goldmine critical habitat (Figure 13) occurs south of Goldmine trail and across the highway in Pacific Rim National Park Reserve. Critical habitat for this location was mapped through interpretation of 1:15,0001996 colour orthophotos and a detailed ecological assessment on a site visit on 23June2010.
Rainforest A Trail, PRNPR: The Rainforest A (Site ID No. 15) and Rainforest B (Site IDNo.16) observations are within 1km of each other and considered one location. As the location is split by the highway that may pose a barrier (i.e., drier conditions of roads may pose as barriers to movements of slugs; COSEWIC 2014), the critical habitat has been mapped separately for each side of the highway as if they were separate locations. It has also been mapped to connect as much as possible with habitat at Rainforest B Trail, as per Principle No. 3 (see above). The site is in an old-growth Western Redcedar-Western Hemlock low elevation (&lt; 100m) forest in the CWHvh1 subzone (Table 3). There are five observation records for the Rainforest A Trail portion of this location (B.C. Conservation Data Centre 2010) recorded in 2003 and 2004 at an elevation of 40m. The Rainforest A Trail critical habitat (Figure 14) is along the Rainforest Trail in Pacific Rim National Park Reserve. Critical habitat was mapped through interpretation of 1:15,0001996 colour orthophotos and a detailed ecological assessment on a site visit on 22June2010. At Rainforest A Trail, no suitable representative habitat is available for inclusion to the north (the habitat is riparian and likely too wet), but across the highway suitable connecting habitat to Rainforest B Trail has been included.
Rainforest B Trail, PRNPR: The Rainforest A (Site ID No.15) and Rainforest B (Site IDNo.16) observations are within 1km of each other and considered one location. As the location is split by the highway that may pose a barrier (i.e., drier conditions of roads may pose as barriers to movements of slugs; COSEWIC 2014), the critical habitat has been mapped separately for each side of the highway as if they were separate locations. It has also been mapped to connect as much as possible with habitat at Rainforest A Trail, as per Principle No. 3 (see above). The site is in an old-growth Western Redcedar-Western Hemlock low elevation (&lt; 100m) forest in the CWHvh1 subzone (Table 3). There is one observation record for this portion of the location, from 2006 (B.C.Conservation Data Centre 2010). The Rainforest B Trail critical habitat (Figure 14) occurs along the Rainforest Trail in Pacific Rim National Park Reserve. Critical habitat for this location was mapped through interpretation of 1:15,0001996 colour orthophotos and a detailed ecological assessment on a site visit on 22June2010. The critical habitat polygon is delineated to include connecting habitat between both sides of the highway.
Ty-histanis: To be determined.
Location: “a geographically distinct area where a group of individuals of a species is (or has been) found. The total population of a species may comprise a number of locations. Dispersal between sites is impossible or very rare. A single threatening event can rapidly affect all individuals in a location. Where a taxon is affected by more than one threatening event, location should be defined by considering the most serious plausible threat. (Source: adapted from IUCN 2001)” (COSEWIC 2008).
Primary forest ecotypes were defined as forest ecotypes (as per RIC 1998) that comprised at least 25% of the habitat composition surrounding known Dromedary Jumping-slug locations.
Part 2 – Recovery Strategy for Dromedary Jumping-Slug (Hemphillia Dromedarius) in British Columbia, prepared by the British Columbia Ministry of Environment
&lt;&lt;a href="http://www.env.gov.bc.ca/wld/recoveryplans/rcvry1.htm"&gt;http://www.env.gov.bc.ca/wld/recoveryplans/rcvry1.htm&gt;
ISBN:978-0-7726-6104-3
Catalogue Number: Pending
William Woodhouse,B.C.Parks, Black Creek, BC
Jennifer Heron,B.C.Ministry of Environment, Vancouver, BC
Dromedary Jumping-slug, Hemphillia dromedarius, is an old-growth coniferous forest-dwelling slug endemic to southern British Columbia (B.C.) and western Washington, with unconfirmed records in northern Oregon. The species exists at the northernmost limits of its range in south western B.C. with a known Canadian range extent of approximately 4000 km2 confined to southern Vancouver Island. The species was located and confirmed in Canada in 1999. As of 2008, 15 locationsFootnote 1have been defined for Dromedary Jumping-slug, with eight of these locations in protected areas. Additional undocumented localities likely exist, although the range extent is not likely to expand significantly. The Committee on the Status of Endangered Wildlife in Canada (COSEWIC) designated Dromedary Jumping-slug as Threatened in 2003, due to the fragmentation of its coniferous forest habitats and threats to the remaining habitats, mainly from forestry activities.
The recovery goal is to ensure the long-term survival of Dromedary Jumping-slug by maintaining a connected networkFootnote 2 of protectedFootnote 3 locations and habitats at the current distribution, area of occupancy, and population sizes, throughout the species' historical range in Canada.
Critical habitat cannot be identified at this time due to incomplete information on life history requirements, population sizes, distribution, area of occupancy, and specific habitat requirements at both the stand and microhabitat scale. Dromedary Jumping-slug is known to occur in older-growth coniferous forests, although the sparse records and number of observed specimens make it difficult to specifically describe critical habitat. Range wide habitat suitability modeling will likely not be possible due to a lack of knowledge of micro-habitat requirements. Soil moisture, relative humidity, coarse woody debris requirements, food requirements, soil mineral requirements, understory vegetation components, and limiting factors within a given location and habitat are not clear, and all these components are necessary to describe critical habitat. Furthermore, the small home ranges Dromedary Jumping-slug occupies are difficult to incorporate with existing GISmapping.
An action plan will be completed by March2013. This action plan will likely be a multi-species document, as recovery actions are similar among multiple gastropod species at risk.
Needs of Dromedary Jumping-Slug
Existing Recommended Approaches to Habitat Protection
Recommended Approaches for Recovery Implementation
Statement of Action Plans
Date of Assessment: April2003
COSEWIC Status History: Designated Threatened in April2003. Assessment based on a new status report.
The Canadian range of Dromedary Jumping-slug is restricted to southern Vancouver Island,B.C. with an approximate range extent of 4000 km2. There is no historic data for this species, as it was recently described (Branson 1972) and the first confirmed record in B.C. was from 1999 (K. Ovaska, pers. comm., 2008). An old record of a large jumping-slug exists from Vancouver Island (Hanham 1926) and most likely represents this species (COSEWIC 2003).
As of 2008, 15 locationsFootnote 4 of Dromedary Jumping-slug are known in B.C. (Figure 2). Survey coverage and locality information for this species is incomplete. Much of the potential habitat within the species’ range has not been surveyed although it is unlikely the range extent will extend beyond existing localities due to existing available habitat (See Habitat and biological needs section).
Area (ha)Table 1 note **
Location OneTable 1 note* 1999 Private forestlandTable 1 note* 700 N/A Remnant high elevation coniferous forest 1
Loss Creek 2000 B.C. Parks; Juan de Fuca Provincial Park 140 N/A Old-growth coniferous forest at Loss Creek near Highway 14 (SEof Port Renfrew) in Juan de Fuca Provincial Park 2
Location ThreeTable 1 note* 2000 UnknownTable 1 note* 30 N/A Mixed old- and second-growth cedar–hemlock coastal forest 2
Location FourTable 1 note* 2001 Private forestlandTable 1 note* 1060 N/A Remnant high elevation coniferous forest 5
Indian Creek 2001 Provincial Crown land 45 1 (COSEWIC 2003) Old-growth cedar–hemlock coastal forest about 9km N of Ucluelet on Kennedy Flats 20
Location SixTable 1 note* 2001 Private forestlandTable 1 note* 850 N/A Remnant high elevation coniferous forest 50+
Pacific Rim National Park Reserve 2003 Parks Canada Agency; Federal 40 15 (Ovaska and Sopuck 2005) Old-growth cedar–hemlock coastal forest along Rainforest A Trail 15
Pacific Rim National Park Reserve 2003 Parks Canada Agency; Federal 25 6 (Ovaska and Sopuck 2005) Old-growth cedar–hemlock coastal forest SE of Goldmine Trail 10
Pacific Rim National Park Reserve 2004 Parks Canada Agency; Federal 80 36 (Ovaska and Sopuck 2005) Old-growth cedar–hemlock coastal forest near Thrasher Cove NW of Port Renfrew on West Coast Trail 50+
Pacific Rim National Park Reserve 2004 Parks Canada Agency; Federal 10 1 (Ovaska and Sopuck 2005) Older second-growth cedar–hemlock coastal forest near Clo-oose on West Coast Trail 50+
Location ElevenTable 1 note* 2006 Mixture of provincial Crown land and privateTable 1 note* land 1200 N/A Remnant high elevation old-growth coniferous forest 50+
Pacific Rim National Park Reserve 2006 Parks Canada Agency; Federal 30 N/A Old-growth cedar–hemlock coastal forest along Rainforest B Trail 20
Pacific Rim National Park Reserve 2006 Parks Canada Agency; Federal 20 N/A Old-growth cedar–hemlock coastal forest along Keeha Beach Trail near Cape Beale 50+
Pacific Rim National Park Reserve 2006 Parks Canada Agency; Federal 30 N/A Old-growth cedar–hemlock coastal forest along Willowbrae Trail 5
Location 15Table 1 note* 2008 Private forestlandTable 1 note* approx1200 1 Old-growth, remnant high elevation hemlock-mixed coniferous forest
Private land is unnamed to respect landowner privacy.
Area refers to the approximate area of the habitat polygon where Dromedary Jumping-slug was observed, where the forest type and ecosystem attributes are similar.
Dromedary Jumping-slug is associated with rich mesic mature and old growth coniferous temperate forests dominated by western hemlock (Tsuga heterophylla) and western redcedar (Thuja plicata). On Vancouver Island, the elevation of known locations is from near sea level to 1200m. The low-elevation locations are within the wet, west coast of Vancouver Island; the remaining localities are from elevations above 700m, in the foggy high areas within the southern interior of the island. Five of the known localities are in remnant patches of old-growth coniferous forest dominated by western hemlock and western redcedar (Figure 3). All localities appear to have high relative humidity and constant moisture.
Slugs are known to initiate ‘water seeking’ responses to dehydration after a short-term reduction in locomotor activity (Prior 1985). Some species exhibit group aggregations, or huddles – groups of slugs aggregate together to prevent water loss (Cook 1981a,b; Prior 1981; Prior et al., 1983, as cited in Prior 1985). Huddles create a high humidity microenvironment and reduce dehydration, yet appear to be non-social aggregations (Cook 1981a as cited in Prior 1985). When a slug becomes dehydrated, the animal will also assume a flattened body position over a wet surface, in order to maximize the surface area of water absorption through the foot (Prior 1985). It is likely Dromedary Jumping-slug exhibits similar huddling and flattening behaviour when dehydrated.
Habitat conversion; fragmentation; isolation; recreational use
Isolation of populations; decreased resources; dispersal sinks; mortality
Competition from exotic species
Exotic gastropod and plant species
Resource competition; alteration of habitat characteristics and plant communities; changes in plant species and community structure of forest ecosystems
Decreased microhabitat humidity from changes in forest floor vegetation; isolation of populations; dispersal sinks; reduced food availability and increased egg and larval mortality (from dehydration); increased predation and competition by exotic gastropods
Roadside vegetation management and maintenance
Errant application of roadside herbicides; chemicals that contain high concentrations of salt; vegetation removal (reducing humidity)
Increased dehydration; direct mortality from vegetation removal
Recovery of Dromedary Jumping-slug is biologically and technically feasible in B.C.The recovery criteria used to assess the technical and biological feasibility of recovery of Dromedary Jumping-slug are discussed below.
Within the species’ range, less than 6% of the landbase remains in old-growth forests and remaining habitats are highly fragmented (MacKinnon and Eng 1995). Dromedary Jumping-slug likely has small home ranges, and thus small (&lt; 20hectares) fragmented patches of habitat throughout the southern portion of Vancouver Island will likely provide suitable habitat.
The recovery goal is to ensure the long-term survival of Dromedary Jumping-slug by maintaining a connected networkFootnote 5 of protectedFootnote 6 locations and habitats at the current distribution, area of occupancy, and population sizes, throughout the species' historical range in Canada.
ProtectFootnote 5 known locations by 2013.
1) Protect known locations by 2013
Knowledge gaps preventing the identification of critical habitat will be addressed according to the schedule of studies, and critical habitat will be proposed within a draft action plan that will be completed by March2013. This action plan will likely be a multi-species document, as threats and proposed recovery actions are similar among multiple gastropod species at risk.
Determine microhabitat requirements for egg laying and nesting, feeding, shelter (aestivation and hibernation sites), and cover (protection from predators) 2008 – 2013
Recovery of Dromedary Jumping-slug is not expected to have extensive socioeconomic implications. A detailed review of the socioeconomic considerations will be completed in the action plan for this species. Localized economic considerations involve forest harvesting within older-growth forests within the species’ range, although small patches of habitat (&lt; 50hectares) may be all that is necessary to conserve Dromedary Jumping-slug locations. Potential long-term conflicts involve habitat conservation within areas where there have been extensive logging and historic land use activities that are incompatible with protection or recovery recommendations. Yet multiple species at risk occur within similar habitats to Dromedary Jumping-slug, and this gastropod can be incorporated into existing management for species that require larger scale habitats.
An action plan will be completed by March2013. The action plan will likely be a multi-species document, as recovery actions are similar among multiple gastropod species at risk.
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Committee on the Status of Endangered Wildlife in Canada (COSEWIC). 2008. Website consulted May2008. www.cosewic.gc.ca
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_______. 2002b. Terrestrial gastropods and salamanders as indicators for monitoring ecological effects of variable-retention logging practices. A pilot study, May–October2001. Report prepared by Biolinx Environmental Research Ltd for Weyerhaeuser Company Ltd., Nanaimo, BC. Unpublished.
_______. 2003c. Terrestrial gastropods as indicators for monitoring ecological effects of variable-retention logging practices. Pre-disturbance surveys at experimental sites May–November2003. Report prepared by Biolinx Environmental Research Ltd. for Weyerhaeuser Canada, Nanaimo, BC. Unpublished.
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Location: a geographically distinct area where a group of individuals of a species is (or has been) found. The total population of a species may comprise a number of locations. Dispersal between locations is impossible or very rare. A single threatening event can rapidly affect all individuals at a location. Where a taxon is affected by more than one threatening event, location should be defined by considering the most serious plausible threat. (Source: adapted from IUCN 2001) (COSEWIC 2008).
Dromedary Jumping-slug has a metapopulation structure within habitat patches, and unoccupied habitats need to be protected to link metapopulations. This network of patches includes known locations and potential habitats, and will link with other conservation initiatives within the species’ range.
Protection can be achieved through a variety of mechanisms including: regulatory changes, voluntary stewardship agreements, conservation covenants, sale by willing vendors of private lands, land use designations, and protected areas.