Information identified as archived on the Web is for reference, research or recordkeeping purposes. It has not been altered or updated after the date of archiving. Web pages that are archived on the Web are not subject to the Government of Canada Web Standards, as per the Policy on Communications and Federal Identity.
Recovery Strategy for the Colicroot (Aletris farinosa) in Canada [Proposed] - 2014
Table of Contents
- 1 COSEWIC Species Assessment Information
- 2. Species Status Information
- 3. Species Information
- 4. Threats
- 5. Population and Distribution Objectives
- 6. Broad Strategies and General Approaches to Meet Objectives
- 7. Critical Habitat
- 8. Measuring Progress
- 9. Statement on Action Plans
- 10. References
- Appendix A: Effects on the Environment and Other Species
- Appendix B: Extirpated Populations of Colicroot
- Appendix C: Associates Found in Colicroot Habitat
- Appendix D: Subnational Conservation Ranks for Colicroot in the United States
- Appendix E: Grids identified as containing critical habitat for Colicroot (Aletris farinosa) in Canada
Environment Canada. 2014. Recovery Strategy for the Colicroot (Aletris farinosa) in Canada [Proposed]. Species at Risk Act Recovery Strategy Series. Environment Canada, Ottawa. v + 29 p.
For copies of the recovery strategy, or for additional information on species at risk, including COSEWIC Status Reports, residence descriptions, action plans, and other related recovery documents, please visit the Species at Risk (SAR) Public Registry.
Cover illustration: © Gary Allen
Également disponible en français sous le titre
« Programme de rétablissement de l’alétris farineux (Aletris farinosa) au Canada [Proposition] »
© Her Majesty the Queen in Right of Canada, represented by the Minister of the Environment, 2014. All rights reserved.
Content(excluding the illustrations) may be used without permission, with appropriate credit to the source.
The federal, provincial, and territorial government signatories under the Accord for the Protection of Species at Risk (1996) agreed 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, ch. 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 five years after the publication of the final document on the SAR Public Registry.
The Minister of the Environment is the competent minister under SARA for the Colicroot and has prepared this strategy, as per section 37 of SARA. To the extent possible, it has been prepared in cooperation with the Province of Ontario.
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 Canada or any other jurisdiction alone. All Canadians are invited to join in supporting and implementing this strategy for the benefit of the Colicroot and Canadian society as a whole.
This recovery strategy will be followed by one or more action plans that will provide information on recovery measures to be taken by Environment Canada and other jurisdictions and/or organizations involved in the conservation of the species. Implementation of this strategy is subject to appropriations, priorities, and budgetary constraints of the participating jurisdictions and organizations.
This version of the recovery strategy was prepared by Judith Jones, Winter Spider Eco-Consulting. The Natural Heritage Information Centre (NHIC) and Ontario Ministry of Natural Resources (OMNR) Aylmer District provided records of Colicroot. Thanks are extended to Allen Woodliffe (formerly with -Aylmer) and Don Kirk (OMNR-Guelph) for assistance with the draft recovery strategy. The original draft of this recovery strategy was developed by the Tallgrass Communities of Southern Ontario Recovery Team, Al Harris (Northern Bioscience), Gerry Waldron (consulting ecologist), and Carl Rothfels (Duke University) with input from John Ambrose (Cercis Consulting), Jane Bowles (University of Western Ontario), Allen Woodliffe (formerly with OMNR), Peter Carson (Pterophylla), Graham Buck (Brant Resource Stewardship Network), Paul Pratt (Ojibway Nature Centre), and Ken Tuininga (Environment Canada, Canadian Wildlife Service - Ontario). Ken Tuininga, Angela Darwin, Krista Holmes, Janet Lapierre and Christina Rohe (Environment Canada, Canadian Wildlife Service – Ontario) provided further revisions to the recovery strategy. Contributions from Susan Humphrey, Lesley Dunn, Elizabeth Rezek and Madeline Austen (Environment Canada, Canadian Wildlife Service – Ontario) are also gratefully acknowledged.
Colicroot (Aletris farinosa) is an herbaceous perennial in the lily family reaching up to 1 m in height with white, tubular flowers which arise from a basal rosette of pale green, lance-shaped leaves. Flowering occurs between late June and late July.
Colicroot distribution ranges from New England west to Wisconsin and Illinois, and from Ontario south to eastern Texas and Florida (NatureServe 2012). In Canada, Colicroot is only confirmed as extant in the Windsor area (three populations) and on the Walpole Island First Nation in the St. Clair River delta, southwestern Ontario (two populations). The species is listed as Threatened on Schedule 1 of the federal Species at Risk Act (SARA). It is also listed as Threatened in Ontario under the provincial Endangered Species Act, 2007.
Threats identified to the Canadian population of Colicroot include, but are not limited to: habitat loss or degradation, changes to ecological dynamics or natural processes, invasive species and disturbance from recreational activities.
Recovery of Colicroot in Canada is considered to be feasible. The population and distribution objectives are to maintain, or increase where biologically and technically feasible, the current abundance and distribution of extant Colicroot populations in Canada. The broad strategies to be taken to address the threats to the survival and recovery of the species are presented in the section on Strategic Direction for Recovery (Section 6.2).
Critical habitat for Colicroot is partially identified in this recovery strategy based on the best available data. Critical habitat for Colicroot is located entirely on non-federal lands, As more information becomes available, additional critical habitat may be identified and may be described within an area-based, multi-species at risk action plan developed in collaboration with the Walpole Island First Nation.
One or more such action plans for Colicroot will be posted on the Species at Risk Public Registry by December 2021.
Based on the following four criteria outlined in the draft SARA Policies (Government of Canada, 2009), the recovery of the Colicroot is considered to be feasible.
Individuals of the wildlife species that are capable of reproduction are available now or in the foreseeable future to sustain the population or improve its abundance.
Yes. There are individuals capable of reproduction within the Canadian range that are available to sustain the population or improve its abundance. For example, hundreds to thousands of plants exist in the Ojibway Prairie Complex in Windsor, Ontario.
Sufficient suitable habitat is available to support the species or could be made available through habitat management or restoration.
Yes. Although some sites may require minor changes in habitat quality, sufficient suitable habitat is currently available to support known populations of the species. Mitigation work was recently conducted for sites supporting Colicroot that were impacted by the construction of the Right Honourable Herb Gray Parkway, and involved the creation and management of restoration sites for transplanted Colicroot plants as well as newly germinated or vegetatively propagated plants. In addition, if agricultural lands in the Windsor area can be protected from urban development and restored to prairie habitat, they could provide an opportunity to expand Colicroot habitat by many hectares. There may also be several areas that historically supported the species that could be restored, however, further investigation is required.
The primary threats to the species or its habitat (including threats outside Canada) can be avoided or mitigated.
Yes. Most primary threats can be avoided or mitigated through recovery actions. For example, in some cases succession can be mitigated using prescribed burns, a proven technique for managing tallgrass prairies. Other mitigation activities recently implemented for the Right Honourable Herb Gray Parkway construction such as fall sod transplants, sod propagation in greenhouses and seed germination with cold stratification have also been successful (LGL Ltd. 2013; PIC 2013). Other primary threats, such as development and agricultural expansion in suitable Colicroot habitat can be avoided.
Recovery techniques exist to achieve the population and distribution objectives or can be expected to be developed within a reasonable timeframe.
Yes. There is little information on the cultivation of Colicroot, but it appears to readily invade bare sand created through disturbance (Kirk 1988). This capacity suggests that suitable habitat could be created or restored nearby existing populations by manipulation of soil and topography. Propagation by seed is possible, and plants also reproduce vegetatively by budding from the rhizomes, however, Colicroot has not been known to transplant well (Harris 2009). Research to address these issues was carried out between 2009 and 2012 to fulfil the Endangered Species Act, 2007 permit requirements for the Right Honourable Herb Gray Parkway. Trials have shown fall sod transplantation to be quite successful and germination and propagation trials have demonstrated promising results (LGL Ltd. 2013; PIC 2013).
1. COSEWIC * Species Assessment Information
Date of Assessment: November 2000
Common Name: Colicroot
Scientific Name: Aletris farinosa
COSEWIC Status: Threatened
Reason for Designation: This perennial herb has few populations remaining which are highly localized in two remnant prairie habitats in southwestern Ontario. Habitat conversion is a continued threat.
Canadian Occurrence: Ontario
COSEWIC Status History: Designated Threatened in April 1988. Status re-examined and confirmed in November 2000.
Globally, Colicroot (Aletris farinosa) is regarded as Secure (G5) (NatureServe 2012). In the United States, it is ranked nationally as Secure (N5) (NatureServe 2012). It is ranked Presumed Extirpated(SX) in Maine and Possibly Extirpated(SH) in New Hampshire; Critically Imperiled (S1) in Pennsylvania and Critically Imperiled to Imperiled(S1S2) in Oklahoma; Imperiled in Rhode Island, Wisconsin and New York; Vulnerable (S3) in Delaware, West Virginia, and Illinois (S3?); and Apparently Secure , Secure, or Unranked (S4, S5, SNR) in 19 additional states (NatureServe 2012; Appendix D).
In Canada, Colicroot is ranked Imperiled both nationally (N2) and provincially (S2) in Ontario (NatureServe 2012).
The percentage of the global range found in Canada is estimated to be less than 5%. The distribution of Colicroot is very restricted in Canada, where it occurs near the northern extent of its North American range.
Colicroot is an herbaceous perennial in the lily family (Liliaceae) and is the only member of its genus in Canada. A basal rosette of pale green, lance-shaped leaves (8 cm to 20 cm long) emerge from a short, thick underground stem (rhizome). Between late June and late July, a slender scape/stalk arises, terminating in a spike-like raceme of small (8 mm to 10 mm), white, tubular shaped flowers. Growing erect, Colicroot generally reaches between 45 cm and 90 cm tall (NatureServe 2012). The fruit is a round, three-parted capsule, containing many small seeds (Cronquist 1991). The fruit capsules along with the basal rosette and dried flower stalk will persist through the winter (Kirk 1988). The capsules will often still contain many seeds the following spring (Kirk 1988), which are readily dispersed by wind (Kirk 1988).
Globally, Colicroot is endemic to North America. In the United States, its range extends across much of the eastern part of the country, from New England west to Wisconsin and Illinois, and south from Virginia to Texas (Figure 1; Appendix D). Colicroot is now considered extirpated and probably extirpated in Maine and New Hampshire respectively (NatureServe 2012). In Canada, Colicroot is only found in southwestern Ontario, where it is considered to be at the northern edge of its range (Figure 2). It occurs in local populations and throughout its range it is largely absent from extensive areas (Kirk 1988).
Groups of plants separated from each other by more than 1 km are generally recognized as separate populations/occurrences in the COSEWIC, NatureServe and Natural Heritage Information Centre (NHIC) records for vascular plants. Groups of plants that are closer to each other than 1 km are considered subpopulations of a single population (NHIC2011). Using this definition, there are five populations with several associated subpopulations considered to be extant and three additional populations of unknown status in Ontario (Figure 2; Table 1).
Two of the five extant populations are found in the Walpole Island First Nation and the other three are in the Windsor area in Essex County. The three populations in the Windsor area are described as follows: the Ojibway Prairie Complex, LaSalle Woodlot Environmentally Significant Area (ESA) and the Reaume Prairie ESA(Table 1). Aside from surveys in the Windsor area associated with the construction of the Detroit River International Crossing and the Right Honourable Herb Gray Parkway (HGP), there have been few Colicroot surveys in the last two decades. Further investigation is required in Essex, Elgin and Norfolk counties to determine the abundance of the three populations of unknown status.
Portions of several Colicroot subpopulations were formerly located in the corridor being developed for the HGP. Within the Ojibway Prairie Complex and the LaSalle Woodlot ESA populations the portions of the Colicroot subpopulations that extended into the HGPfootprint were removed and transplanted to restoration sites adjacent to the HGP under a permit issued under the provincial Endangered Species Act, 2007.The permit also required the proponent to carry out trials of different restoration techniques between 2009 and 2012 which have been largely successful (LGL Ltd. 2013; PIC 2013) (described in Section 6.1). With this in mind, the abundance information in Table 1 is quickly dated and subject to change. Restoration sites will be added once the transplanted plants have had time to establish and their success determined.
Ten extirpated populations (NHIC 2011) are listed in Appendix B.
Figure 1. The Global distribution of Colicroot (modified from Argus et. al.1982 – 1987).
Figure 2. The Canadian range of Colicroot (Environment Canada 2012). Due to lack of spatial reference, two extirpated populations have not been included. For a full list of populations and subpopulations, including those with extant and unknown status, see Table 1. For a list of extirpated populations see Appendix B.
|Last Observed||Abundance at last observation||Status|
|1. Walpole Island First Nation - Population #1||2009[c]||~100 flowering stems [f]||Extant|
|2. Walpole Island First Nation - Population #2||2009||~100 flowering stems [f]||Extant|
|3. Ojibway Prairie Complex|
|Ojibway Prairie Provincial Nature Reserve||2005||Hundreds to thousands of plants (1987) [a],[f]||Extant|
|Spring Garden Natural Area||1994||190 flowering stems (1987) [a],[f]||Extant|
|HGP2 #1 (near Matchette/Malden)||2008||1 526 flowering stems[f],[d]||Extant|
|HGP #2 (near Spring Garden/Lamont )||2008||1 flowering stem[f]||Extant|
|"Ball Diamond"||2008||Approximately 600 - 700 plants[e]||Extant|
|Tallgrass Prairie Heritage Park, Kirk (1987) #5||1987||No information||Unknown|
|North of Windsor Raceway. Kirk (1987) #9||1986||Single rosette[f]||Unknown|
|4. LaSalle Woodlot ESA|
(near Huron Church/Todd)
|2008||3 531 flowering stems[f],||Extant|
(near Huron Church)
|2008||18 flowering stems [f]||Extant|
|HGP #5 (near Huron Church/St Clair)||2008||30 flowering stems[f],||Unknown|
|Kirk (1987) Essex #3||1987||No information||Unknown|
|Near Oakwood Park, Windsor, Kirk (1987) Essex #10||1984||No information||Unknown|
|Near Brunet Park||1993||~1000 flowering stems[f]||Unknown|
|5. Reaume Prairie ESA||2012||30- 40 flowering stems, additional rosettes present[b], [g]||Extant|
|Ruscom Shores Conservation Area||1983||No information||Unknown|
|Eagle (southeast of West Lorne)||1993||~60 plants[f]||Unknown|
(Not found in 2002)
Sources: ( aKirk 1987; bBowles pers. comm. 2010; cJacobs pers. comm. 2010; dWaldron pers. comm. 2010; eWoodliffe pers. comm. 2010; fNHIC data available as of 2011, gOldham pers. comm. 2013).
xTable 1 does not include any of the sites to which Colicroot plants were transplanted as part of the Right Honourable Herb Gray Parkway mitigation.
- 1Subject to change
- 2HGP(Right Honourable Herb Gray Parkway)
- 3ESA (Environmentally Significant Area)
- 4Portions of these local populations were within the Endangered Species Act, 2007 permit boundary and transplanted to restoration sites. Estimated abundance and extent of occurrence may be subject to change.
In Canada, Colicroot primarily inhabits moist tallgrass prairie and oak savanna communities, although some plants occur in old field, roadside and woodland edge habitats (Kirk 1988; COSEWIC 2000). It occurs on soil characterized as coarse-textured, sand or sandy loam with a neutral to somewhat acidic pH (4.7 to 7.0) (Kirk 1988). The species may also be found in forest openings and sand pits given suitable habitat conditions (Kirk 1988; Kirk pers. comm. 2011).
Colicroot is intolerant of shading from woody plants and dense herbaceous growth (Kirk 1988). In the absence of fire, the species is dependent on disturbance, provided that the soil is not disturbed to a depth of more than a few centimetres, to maintain the open habitat from competing vegetation and thatch built up on the ground. When the habitat becomes too shady, Colicroot growth and vigour may be compromised and flowering may not occur at all, however, individual Colicroot plants may persist for years in a non-flowering state until the light conditions become more favourable (Woodliffe pers. comm. 2010). Colicroot appears to readily colonize scarified or bare sandy substrate created through disturbance, as significant population increases have been noted in areas where such conditions occur (Kirk 1988).
Colicroot occurs in the Carolinian region of southwestern Ontario. Although the species’ habitat is subject to seasonal extremes in moisture conditions (e.g., spring flooding and summer drought) (Lee et al. 1998; Kost et al. 2007), this region has one of the warmest climates and longest growing seasons in Canada (White and Oldham 2000). Kirk (1988) notes, the drought conditions, high humidity and high summer temperatures of this region, characterize a climate typical of the northern Midwest United States (e.g. Minnesota, Wisconsin).
Colicroot does not appear to transplant well (Harris 2009), suggesting it may have an obligate symbiotic relationship with mycorrhizal fungi (Kirk 1988; Harris 2009). Trials have been conducted to identify factors that increase Colicroot transplant success as a requirement of the permit issued under the Endangered Species Act, 2007 for the HGP (LGL Ltd. 2013).
Currently, there is little information on Colicroot pollinators, although other species of Aletris are pollinated by bumblebees (Bombus spp.) and beeflies (Bombyliusspp.) (Kirk 1988).
|Threat||Level of Concern ||Extent||Occurrence||Frequency||Severity||Causal Certainty |
|Habitat Loss or Degradation|
|Development (e.g. housing, commercial, infrastructure)||High||Widespread||Historic / Current / Anticipated||Recurrent||High||High|
|Dumping (e.g. fill, garbage)||Medium||Localized||Historic/ Current||Continuous||Unknown||Medium|
|Changes in Ecological Dynamics or Natural Processes|
|Alteration of natural fire regime||High||Widespread||Current||Continuous||High||Medium|
|Disturbance or Harm|
|Incidental harm (e.g. from mowing, off-road vehicles and trail use)||Medium||Localized||Current||Continuous||Moderate||Medium|
|Introduced and Invasive Species|
|Invasive species (e.g. Scots Pine, Common Reed, Autumn Olive, Multiflora Rose etc.)||Low-Medium||Localized||Current||Continuous||Unknown||Medium|
Sources: (COSEWIC 2000; Woodliffe pers. comm.2010; Pratt pers. comm.2010; and Jacobs pers. comm. 2010).
- Level of Concern: signifies that managing the threat is of (high, medium or low) concern for the recovery of the species, consistent with the population and distribution objectives. This criterion considers the assessment of all the information in the table.
- Severity: reflects the population-level effect (High: very large population-level effect, Moderate, Low, Unknown).
- Causal certainty: reflects the degree of evidence that is known for the threat (High: available evidence strongly links the threat to stresses on population viability; Medium: there is a correlation between the threat and population viability e.g. expert opinion; Low: the threat is assumed or plausible).
- Threat categories are listed in order of decreasing significance.
In Ontario, only about 2 100 ha or 0.5% of the prairie and savanna present in the 19th century remains, with the majority of tallgrass prairie lost to agricultural and residential development (Bakowsky and Riley 1994). Most populations of Colicroot in Canada are on open ground that is vulnerable to residential, commercial and infrastructure development. Expansion of several agricultural fields has destroyed multiple populations in Lambton and Essex counties (NHIC 2011).
Alteration of the natural fire regime or other limited disturbance can alter suitable habitat by allowing trees and shrubs to grow and eventually shade out the species. Periodic prescribed burning is conducted on the Ojibway Prairie Complex and on parts of the Walpole Island First Nation. It is also required at other sites to prevent prairie habitats from converting to woodlots. Succession was the likely cause of the disappearance of the Elgin County population as well as one of the Walpole Island First Nation subpopulations (White and Oldham 2000).
Dumping of fill and garbage has probably extirpated the population at Turkey Point and may threaten some of the other subpopulations in the Windsor area (White and Oldham 2000).
Off-road or all-terrain vehicle (ATV) and off-trail use can result in direct damage to an individual plant through trampling and compaction of the soil, thus making habitat unsuitable. The effects of off-road vehicles and other recreational activities were noted by Oldham (2000) on unfenced public and private sites in Windsor and LaSalle.
Mowing of prairie habitat that may contain Colicroot also occurs at some sites around Windsor that are outside of protected areas (Woodliffe pers. comm. 2010). Although Colicroot does not grow well with competing vegetation, mowing does not normally result in suitable habitat conditions for Colicroot and may potentially harm Colicroot plants.
Invasive species may out-compete Colicroot for resources and contribute to the loss of suitable habitat. Competition is particularly evident at Reaume Prairie, where Scots Pine (Pinus sylvestris) is invading. Additionally, invasive species such as Common Reed (Phragmites australisssp. australis), Autumn Olive (Elaeagnus umbellata) and Multiflora Rose (Rosa multiflora) have been identified at some HGPrestorations sites in which Colicroot was either found naturally or to which it was transplanted. Black Locust (Robinia pseudoacacia) and Sweet Clover (Melilotus alba) are the most significant invasives threatening Colicroot on Walpole Island First Nation (Jacobs pers. comm. 2013). These two species along with others such as Common Buckthorn (Rhamnus cathartica) may also be found in areas supporting Colicroot and typically invade disturbed areas with full sunlight (Ambrose and Waldron 2005; Tallgrass Ontario 2005), outcompeting native shade-intolerant species.
The population and distribution objectives are to maintain, or increase where biologically and technically feasible, the current abundance and distribution of extant Colicroot populations in Canada (including the abundance within each population where biologically and technically feasible).
The priority for increasing the current abundance and distribution of Colicroot populations is through management of habitat of extant populations, including those created under permit for the HGP, i.e. a more natural increase as opposed to reintroductions to sites from which Colicroot has been extirpated. Where possible, however, introduction at historical sites that have suitable habitat should be considered for biological and technical feasibility.
Several subpopulations are in provincially and municipally protected areas within the Ojibway Prairie Complex and are managed to conserve Colicroot and other tallgrass prairie plants and habitat. As well, the Reaume Prairie and LaSalle Woodlot sites are designated Environmentally Significant Areas (ESAs) in the official plan of the Town of LaSalle, thereby receiving additional consideration for protection in the planning process.
On the Walpole Island First Nation tallgrass prairie and savanna communities undergo periodic prescribed burns. The Ojibway Prairie Provincial Nature Reserve, Tallgrass Prairie Heritage Park, and Spring Garden Natural Area have active prescribed burn programs as well.
Recovery actions described in the Draft Walpole Island Ecosystem Recovery Strategy (Bowles, 2005) include raising awareness in the community about species at risk, including Colicroot. Pamphlets, calendars, newsletter articles, posters and other promotional material have been used to raise awareness of species at risk in the Walpole Island First Nation community.
The Walpole Island First Nation is currently developing an ecosystem protection plan based on the community’s traditional ecological knowledge (TEK).
Efforts by the Walpole Island Heritage Centre to lease lands for conservation have resulted in a reduction in the rate of conversion of prairie and savannah habitat to agriculture (COSEWIC 2009) during the tenure of the 5-year leases. The Walpole Island Land Trust was established in 2008 to conserve land on the Walpole Island First Nation (Jones 2013). Over 300 acres of land with tallgrass prairie, oak savannah and forest habitats have been acquired since 2001 for conservation (Jacobs 2011), benefitting species at risk such as Colicroot.
In the Windsor area, the construction of a divided multi-lane highway (the Herb Gray Parkway, or HGP) resulted in impacts to a portion of the Colicroot subpopulations in the Ojibway Prairie Complex and LaSalle Woodlot Environmentally Significant Area. In 2010, the Minister of Natural Resources issued a permit under the Endangered Species Act, 2007 to the Ministry of Transportation for the construction of the HGP. The permit identified several conditions to mitigate impacts to Colicroot, including creating restoration sites, developing a restoration and management plan, and completing several transplanting and propagation trials. The management plan identifies measures for habitat enhancement, including invasive species management and adaptive management strategies.
The purpose of the transplanting and propagation trials was to identify techniques for transplanting and propagating Colicroot, because the species was not known to transplant well, or grow successfully from seed. Trials conducted included timing of transplanting (spring, summer, or fall), seed dispersal into appropriate habitat, rhizome cutting, and growing Colicroot lifted from impact sites in a greenhouse to promote growth and reproduction. Many of the trials resulted in successful transplantation of Colicroot, with the notable exception of rhizome cutting. Trials revealed that Colicroot rhizomes were too small to cut. With respect to propagation trials, direct seeding into appropriate habitat was not successful, however, trials showed that cold moist stratification resulted in successful germination and growth of Colicroot seed. The most successful transplanting trial was lifting sods in fall and transplanting the sods into appropriate habitat prepared ahead of time by scraping away existing vegetation at the receptor site. This technique was employed in the fall of 2012 to transplant the impacted population. Large sods (approximately 1 m2), were lifted with soil intact, and planted into restoration sites. All planted and transplanted individuals are being monitored from the time of planting until five years after construction is completed. (LGL Ltd. 2013; PIC 2013).
|Threat or Limitation||Priority||Broad Strategy to Recovery||General Description of Research and Management Approaches|
|All threats||High||Assess / monitor populations|
|All threats||High||Protect, conserve and manage habitat|
|Knowledge gaps relating to recruitment and biological needs and impacts of threats||High||Conduct research|
|All threats||Medium||Outreach and education|
|Habitat loss or degradation||Medium||Habitat restoration|
Critical habitat is defined in the Species at Risk Act(S.C. 2002, c29) section 2(1) as “the habitat that is necessary for the survival or recovery of a listed wildlife species and that is identified as the species’ critical habitat in the recovery strategy or in an action plan for the species”.
Critical habitat for Colicroot is partially identified in this recovery strategy, to the extent possible, based on best available information. It is recognized that the critical habitat identified below is insufficient to achieve the population and distribution objectives for the species, because it has only been identified for three of five known extant populations. Available information on the species at a number of locations is outdated or lacking detailed spatial references. The Schedule of Studies (Section 7.2; Table 4) outlines the activities required for identification of additional critical habitat necessary to support the population and distribution objectives. More precise critical habitat boundaries may be identified, and additional critical habitat may be added in the future, as new information becomes available.
The identification of critical habitat for Colicroot is based on two criteria: suitable habitat and site occupancy.
Colicroot is found on damp sand or sandy loam in tallgrass prairie and oak savanna communities, old fields and woodland edges where the pH of the soil ranges from neutral to slightly acidic (4.7 to 7.0) (Kirk 1988). Scarified or bare sandy substrate from human disturbance may provide suitable open ground in the absence of fire. Colicroot may be found in large open areas or in smaller openings within another vegetation type (e.g. forest) given suitable soil type, moisture and pH conditions. Within these suitable habitat areas, the vegetation immediately adjacent to Colicroot typically consists predominantly of herbaceous plants, especially grasses (Appendix C). Both natural and human disturbances create and maintain the openness of habitat (prevent shading by competing vegetation), contributing to the suitability of habitat for Colicroot. Therefore, suitable habitat for Colicroot is described as natural or semi-naturalized habitat.
Natural habitat suitable for Colicroot includes tallgrass prairie and savanna. The Ecological Land Classification (ELC) framework for Ontario (from Lee et al. 1998) can be used to describe this habitat. Colicroot is documented to occur within the following ELC ecosite designations:
- - Fresh-Moist Tallgrass Prairie (TPO2)
- - Fresh-Moist Tallgrass Savanna (TPS2)
The ELC framework provides a standardized approach to the interpretation and delineation of dynamic ecosystem boundaries. The ELC approach classifies habitats not only by vegetation community but also considers hydrology and topography, and as such provides a basis for describing the ecosystem requirements of the natural habitat for Colicroot.
Semi-naturalized habitats such as old field, roadsides, railway embankments, wet meadows, utility corridors, and cultural woodland edges are also suitable for Colicroot but are not well characterized by ELC vegetation types. Suitable habitat in semi-naturalized habitat occurs where:
- the habitat is open (< 25% tree or shrub cover) and not shaded;
- the underlying ground is sand or sandy soil;
- the area immediately surrounding the plants is bare ground or predominantly covered with herbaceous plants, especially grasses, with some tallgrass prairie associates.
Suitable habitat in semi-naturalized areas ends where any of the following occur:
- the ground is entirely shaded by trees or shrubs (boundary is the forest edge);
- the soil is no longer sandy;
- there is active agricultural use (for crops or pasture) or manicured vegetation (lawns, gardens, etc.).
Although only a small portion of the suitable habitat area may be occupied, unoccupied area is required for wind dispersal, establishment, and expansion of the species to ensure long-term viability of the population at that site. Since Colicroot readily colonizes on disturbed (e.g. blowing or shifting) sandy soil (Kirk 1988) inclusion of additional areas surrounding the plants may accommodate the natural movement of sandy substrates and Colicroot colonies over time. In addition, suitable habitat requires periodic disturbance, so the extent of the suitable vegetation community is required to provide space for ecological processes that maintain habitat (such as fire, periodic flooding, etc.) to take place. As well, suitable natural habitat is extremely limited, so where the species occurs, it is important to protect all of the existing habitat.
Site Occupancy Criterion: The site occupancy criterion defines an occupied site as a location where Colicroot has been observed for any single year since 1993 AND where suitable habitat is present.
A site is defined by a boundary drawn at a distance of 50 m around a known observation of Colicroot. An observation may be represented by a point (representing a single plant or a location where there are multiple plants) or a polygon (collected as boundary points around the outer edge of a larger population). The 50 m distance is applied to each observation, with spatially overlapping areas merged together to form larger sites. In cases where observations are represented by a polygon, the 50 m distance is applied to the outer edge of the polygon.
Where Colicroot resides in natural habitat, the site boundary is extended beyond the 50 m to include the extent of continuous suitable habitat (ELC vegetation type, as described in Section 7.1.1), which is associated with, and is integral to, the production and maintenance of suitable habitat conditions and which provides the ecological context for occupied microhabitats. The entire suitable habitat patch is required to allow dispersal and establishment of the species. As well, suitable natural habitat is extremely limited, so where the species occurs, it is important to protect the entire existing habitat.
For populations in semi-naturalized habitats, the entire open area which may extend beyond the site boundary is not assumed to be suitable as some parts may not contain suitable habitat for Colicroot. Therefore, in semi-naturalized habitat only the area within the 50 m distance around a Colicroot plant is identified as an occupied site.
The 50 m distance is considered a minimum ‘critical function zone’, or the threshold habitat fragment size required for maintaining constituent microhabitat properties for a species (e.g. critical light, moisture, humidity levels necessary for survival). At present, it is not clear at what distance physical and/or biological processes begin to negatively affect Colicroot. Studies on micro-environmental gradients at habitat edges, i.e., light, temperature, litter moisture (Matlack 1993), and of edge effects on plants in mixed hardwood forests, as evidenced by changes in plant community structure and composition (Fraver 1994), have shown that edge effects could be detected up to 50 m into habitat fragments. Forman and Alexander (1998) and Forman et al. (2003) found that most roadside edge effects on plants resulting from construction and repeated traffic have their greatest impact within the first 30 to 50 m. Therefore, a 50 m distance from any Colicroot plant is appropriate to ensure microhabitat properties for rare plant species occurrences are incorporated in the identification of critical habitat. The area within the site boundary may include both suitable and unsuitable habitat as Colicroot may be found near the transition area/zone between suitable and unsuitable habitat (e.g. within small forest openings, or along woodland edges).
Occupancy is determined using occurrence reports collected between 1993 and 2012. The 20-year timeframe is consistent with NatureServe’s (2002) and Ontario’s Natural Heritage Information Centre’s (NHIC) threshold for considering populations to be extant versus historic, and allows for inclusion of a number of native populations that likely persist but which have not been recently surveyed. Given the known historic and current threats to the species, the assumption is that the species is extant until more information becomes available. Colicroot is a perennial species that may remain present in overgrown habitats for years without flowering. It can also seem to disappear for a few years until competing vegetation is removed, opening up the habitat (Woodliffe pers. comm. 2012). More detailed information on the location of critical habitat, to support protection of the species and its habitat, may be requested on a need-to-know basis by contacting Environment Canada – Canadian Wildlife Service.
Including suitable habitat (determined using high resolution aerial photography to confirm its presence) in the occupancy criteria aims to protect sites where the plants are likely to still remain.
Critical habitat for Colicroot in Canada is identified as the sites containing suitable habitat (Section 7.1.1) and currently known to be occupied by Colicroot according to the site occupancy criteria (Section 7.1.2). For clarity, critical habitat includes all the habitat within a radial distance of up to 50 m from a Colicroot plant, where suitable habitat exists. In natural habitats, critical habitat also includes the entire ELC ecosite polygon described as suitable in Section 7.1.1.
Major roadways or built-up features such as buildings do not assist in the maintenance of natural processes and are therefore not identified as critical habitat. If a hard edge (e.g., major road, building) occurs within a site (e.g., prior to the 50 m distance), critical habitat ends at the hard edge.
In addition, some sites within the Ojibway Prairie Complex and LaSalle Woodlot ESA populations were partially within the Endangered Species Act, 2007 permit boundary of the HGP development and are not currently identified as critical habitat. All plants previously occurring inside the HGP footprint have been transplanted into existing or restored suitable habitat. The majority of these restoration sites occur within the Ojibway Prairie Complex, LaSalle Woodlot ESA and surrounding areas. Additional plants were propagated and planted in the restoration sites. Once the transplanted populations occurring in suitable habitat have established the restoration sites will be reviewed and additional critical habitat may be identified.
For some Colicroot populations, little or no mapping and/or documentation of plant locations or habitat features exists, while for others, available data are more than 15 years old. For certain locations where Colicroot is confirmed to be extant (i.e. via pers. comm.) but no mapping exists, a generalized boundary is used to identify the area in which critical habitat is likely to occur. The generalized boundary is determined based on details provided in the observation (including historical references) and the extent of suitable habitat using air photo interpretation and recent imagery. Generalized boundaries of critical habitat were created at four sites (Ojibway Prairie Provincial Nature Reserve, Spring Garden Natural Area, “Ball Diamond” and Reaume Prairie ESA). Critical habitat at these sites reflects the best available information and may be refined as additional information becomes available.
Application of the critical habitat criteria to available information as of December 2012 identifies 15 sites (3 populations) as critical habitat for Colicroot in Canada (Appendix E). It is important to note that the coordinates provided are a cartographic representation of where the critical habitat sites can be found presented at the level of a 1 km x 1km grid and does not represent the extent or boundaries of the critical habitat itself. More detailed information on the location of critical habitat, to support protection of the species and its habitat, may be requested on a need-to-know basis by contacting Environment Canada – Canadian Wildlife Service at firstname.lastname@example.org.
The identification of critical habitat in this recovery strategy is based on the information currently available to Environment Canada for the 20-year time period of 1993-2012 and is insufficient to meet the population and distribution objectives, therefore a Schedule of Studies is included. As additional information becomes available, critical habitat identification may be refined or more sites meeting critical habitat criteria may be added.
Critical habitat is not identified for the two extant populations of Colicroot at Walpole Island First Nation. The information required to satisfy the critical habitat criteria (i.e., location and extent of populations, biophysical habitat attributes) is not available for use by Environment Canada. Although the continued presence of Colicroot has been confirmed (Jacobs pers. comm. 2010), confirming the extent of locations and biophysical habitat attributes (i.e., extent and amount of the ELC ecosite of suitable habitat (as listed in Section 7.1.1)) is also required for these populations. Once adequate information is available for use, additional critical habitat may be identified and may be described within an area-based multi-species at risk action plan developed in collaboration with the Walpole Island First Nation.
Critical habitat is not identified for two populations (Turkey Point and Eagle (SE of West Lorne)) and one subpopulation (West of Brunet Park) where the persistence of suitable habitat is not evident from recent imagery (high resolution orthophotography, circa. 2010). Confirmation of both species and suitable habitat persistence are required at these locations; this activity is described in the Schedule of Studies (Section 7.2).
In addition, the schedule of studies aims to confirm the location and extent of Colicroot population reports for five other locations of Colicroot considered to be of ‘unknown’ status (Table 1). The NHIC currently lists these locations as historic because they have not been visited since the 1980s, however, in this recovery strategy these sites are considered ‘unknown’. Further information on these locations is required to satisfy the population and distribution objectives for Colicroot in Canada. New information will be assessed to identify additional critical habitat or to refine existing critical habitat, as appropriate.
The restoration sites for the HGP created under the Endangered Species Act, 2007 permit, are not currently identified as critical habitat. All plants previously occurring inside the HGP footprint have been transplanted into existing suitable habitat or restored habitat. The majority of these restoration sites occur within the Ojibway Prairie Complex, LaSalle Woodlot ESA and surrounding areas. Additional plants were propagated and planted in the restoration sites. Once the restoration plantings have established the HGPrestoration sites will be reviewed and additional critical habitat may be identified.
|Description of Activity||Rationale||Timeline|
|Confirm/obtain population information and conduct Ecological Land Classification for any outstanding natural populations/subpopulations.||Location of population becomes known and habitat associations, biophysical habitat attributes and extent of suitable habitat are confirmed.||2014-2019|
|Confirm/obtain population information and conduct habitat assessments (using ELC or other method to determine the boundaries of suitable habitat) for those populations/subpopulations with records older than 5 years (<2008) and identify additional critical habitat.||Location of population becomes known and habitat associations, biophysical habitat attributes and extent of suitable habitat are confirmed and critical habitat is fully identified.||2014-2019|
|Confirm/obtain population and ELC information for HGP restoration sites and any other restoration planting sites and determine success of plantings and identify additional critical habitat.||Locations of successful new or re-established populations becomes known and habitat associations, biophysical habitat attributes and extent of suitable habitat are confirmed, thereby allowing identification of critical habitat at these sites and fully identifying critical habitat.||2014-2019|
Understanding what constitutes destruction of critical habitat is necessary for the protection and management of critical habitat. Destruction of critical habitat is determined on a case by case basis. Destruction would result if part of the critical habitat was degraded, either permanently or temporarily, such that it would not serve its function when needed by the species. Destruction may result from a single activity or multiple activities at one point in time or from the cumulative effects of one or more activities over time (Government of Canada, 2009). Activities described in Table 5 include those likely to cause destruction of critical habitat for the species; however; destructive activities are not limited to those listed.
|Description of Activity||Description of Effect||Details of Effect|
|Development and conversion of lands (e.g. agricultural expansion, residential and commercial development, road construction)|
Results in loss of suitable substrate conditions, habitat fragmentation/increased edge effects and/or direct covering up of suitable ground
Can reduce quality of germinating sites and/or prevent growth of Colicroot
|Direct effect, applicable at all times|
|Operation of off road vehicles or removal of top soil (greater than a few centimetres)|
Results in ruts or trampled vegetation and loss of substrate or suitable substrate conditions
These activities can reduce the quality of germinating sites and prevent establishment
|Repeated off road traffic will cause soil compaction, except when ground is frozen. Removal of topsoil is a direct effect at all times|
Results in expansion of woody vegetation in Colicroot habitat
Creates unsuitable habitat conditions
|Long term fire suppression will result in shading or crowding out of the species|
|Alteration of moisture levels (e.g. ditching, berm construction or tiling)|
Results in sites that are no longer moist but too wet or too dry
Soil conditions are no longer suitable for Colicroot germination or growth
|A single event of this kind is very likely to result in destruction of critical habitat|
|Introduction of invasive species (e.g. direct seeding or planting or through vectors such as ATVs)|
Results in increased resource competition through crowding or shading
Can make habitat unsuitable for Colicroot
|A single event of this kind is likely to result in destruction of critical habitat|
|Use of herbicides, constant mowing, livestock grazing, tree planting, depositing fill|
Results in alteration of soil conditions and/or light intensity rendering habitat unsuitable for growth of Colicroot
Can result in loss of native species and degradation of critical habitat
|Even localized impacts by these activities can change soil and light conditions affecting the species|
The performance indicators presented below provide a way to define and measure progress toward achieving the population and distribution objectives.
Every five years, success of recovery strategy implementation will be measured against the following performance indicators:
- the abundance of each extant population of Colicroot in Canada has been maintained at its current level or has increased;
- there are at least five extant populations of Colicroot across its native range in Canada.
One or more action plans for Colicroot will be completed by December 2021.
Ambrose, J. D., and G. E. Waldron. 2005. Draft National Recovery Strategy for Tallgrass Communities of southern Ontario and their associated species at risk. Draft recovery plan prepared for the Tallgrass Communities of Southern Ontario Recovery Team. National Recovery Plan, Recovery of Nationally Endangered Wildlife (RENEW), Ottawa, Ontario.
Argus, G.W., K.M. Pryer, D.J. White, and C.J. Keddy. 1982-87. Atlas of the Rare Vascular Plants of Ontario. 4 parts. National Museum of Natural Sciences, Ottawa, Ontario.
Bakowsky, W.D. and J.L. Riley. 1994. A survey of the prairies and savannas of southern Ontario. Proceedings of the Thirteenth North America Prairie Conference: 7-16. Edited by R.G. Wickett, P.D. Lewis, A. Woodliffe, and P. Pratt.
Bowles, Jane, personal communication 2010. Curator of herbarium, University of Western Ontario, London; and consulting ecologist.
Bowles, J.M., 2005. Draft Walpole Island Ecosystem Recovery Strategy. Walpole Island Heritage Centre, Environment Canada, and the Walpole Island Recovery Team.
COSEWIC 2000. COSEWIC assessment and update status report on the colicroot Aletris farinosa in Canada. Committee on the Status of Endangered Wildlife in Canada. Ottawa. vi + 10pp.
COSEWIC 2009. COSEWIC assessment and status report on the pink milkwort Polygala incarnata in Canada. Committee on the Status of Endangered Wildlife in Canada. Ottawa. 24 pp.
COSEWIC 2011. COSEWIC Species Assessment Information. COSEWIC's Assessment Process and Criteria accessed December 6, 2011.
Cronquist, A. 1991. Manual of Vascular Plants of Northeastern United States and Adjacent Canada, 2nd ed. New York Botanical Garden, 910 pp.
Environment Canada, 2010. Species at Risk Public Registry. Species Profile: Colicroot. Web site:Species at Risk Public Registry - Species Profile (Colicroot) [accessed June 09, 2011].
Forman, R.T.T. and L. E. Alexander. 1998. Roads and their major ecological effects. Annual Review of Ecology and Systematics 29:207-231.
Forman, R. T. T., D. Sperling, J. A. Bissonette, A. P Clevenger, C. D. Cutshall, V. H. Dale, L. Fahrig, R. France, C. R. Goldman, K. Heanue, J. A. Jones, F. J. Swanson, T. Turrentine, and T. C. Winter. 2003. Road ecology: science and solutions. Island Press, Washington, D.C., USA.
Fraver, S. 1994. Vegetation Responses along Edge‐to‐Interior Gradients in the Mixed Hardwood Forests of the Roanoke River Basin, North Carolina. Conservation Biology 8(3): 822-832.
Government of Canada. 2009. Species at Risk ActPolicies, Overarching Policy Framework [Draft]. Species at Risk Act Policy and Guidelines Series. Environment Canada. Ottawa. 38 pp.
Harris, A. 2009. Mitigation Methods for Vascular Plant Species at Risk in Ontario. Northern Bioscience, unpublished report.
Jacobs, C. 2011. Bkejwanong's Conservation Approaches: Completing the Circle. Walpole Island Heritage Centre, Accessed January 11, 2013.
Jacobs, Clint, personal communications 2010 and 2013. Natural Heritage Coordinator, Walpole Island Heritage Centre.
Jones, J. 2013. DRAFT Recovery strategy for the Willowleaf Aster (Symphyotrichum praealtum) in Ontario. Ontario Recovery Strategy Series. Prepared for the Ontario Ministry of Natural Resources, Peterborough, Ontario. v + 23 pp.
Kirk, D.A. 1987. Conservation Recommendations for Colicroot, Aletris farinosa L., a Threatened Species in Canada. Committee on the Status of Endangered Wildlife in Canada (COSEWIC), Ontario. 5 pp.
Kirk, D.A. 1988. Status Report on the Colicroot, Aletris farinosa, in Canada. Committee on the Status of Endangered Wildlife in Canada. 39 pp.
Kirk, Donald, personal communication 2011. Natural Heritage Ecologist, Ontario Ministry of Natural Resources, Guelph District.
Kost, M.A., D.A. Albert, J.G. Cohen, B.S. Slaughter, R.K. Schillo, C.R. Weber, and K.A. Chapman. 2007. "Mesic Sand Prairie" in Natural Communities of Michigan: Classification and Description. Michigan Natural Features Inventory, Report No. 2007-21, Lansing, MI. accessed January 13, 2011.
Lee, H.T., W.D. Bakowsky, J. Riley, J. Bowles, M. Puddister, P. Uhlig and S. McMurray, 1998. Ecological Land Classification for Southern Ontario: First Approximation and Its Application. OMNR, Southcentral Science Section, Science Development and Transfer Branch. SCSS Field Guide FG-02. 225 pp.
Lee, Harold, personal communication 2012. Ecologist, Ontario Ministry of Natural Resources, London, Ontario.
LGL Limited. 2013. Draft Colicroot (Aletris farinosa) Trials 2012 Annual Monitoring Report The Windsor-Essex Parkway Created To Meet Conditions of Permit No. AY-D-001-09 Issued Under the Authority of Clause 17(2)(d) of the Endangered Species Act, 2007. Prepared for the Ontario Ministry of Transportation, London, Ontario. 61 pp.
NatureServe 2012. NatureServe Explorer: An online encyclopaedia of life [web application]. Version 7.1. NatureServe, Arlington, Virginia. (Accessed: December 20, 2012).
Matlack, G. R. 1993. Microenvironment variation within and among forest edge sites in the eastern United States. Biological conservation 66(3), 185-194.
NHIC2011. Electronic and element occurrence databases. (accessed December, 2011).
Oldham, M.J. 2000. Element Occurrence records of White-tubed Colicroot (Aletris farinosa) from the database of the Natural Heritage Information Centre, Ontario Ministry of Natural Resources, Peterborough. 30 pp.
Oldham, Mike, personal communication. 2013. Botanist/Herpetologist, Ontario Ministry of Natural Resources, Natural Heritage Information Centre.
Parkway Infrastructure Contractors (PIC) 2013. 2012 Annual Monitoring Report for Plant Species at Risk The Rt. Hon. Herb Gray Parkway Volume 1 Mitigation and Monitoring Created To Meet the Conditions of Endangered Species Act (2007) Permits AY-B-009-04; AY-C-009-01; AY-D-001-09; and AY-C-004-11. 147 pp.
Tallgrass Ontario. 2005. A Landowner’s Guide to Tallgrass Prairie and Savanna Management in Ontario, Tallgrass Ontario. i + 48 pp.
Pratt, Paul, personal communication 2010. Naturalist, Ojibway Park Nature Centre, City of Windsor.
Waldron, Gerry, personal communication 2010. Consulting Ecologist, Amherstberg, Ontario.
White, D.J., and M.J. Oldham. 2000. Update COSEWIC status report on the Colicroot Aletris farinosa in Canada. Committee on the Status of Endangered Wildlife in Canada. Ottawa. 8 pp.
Woodliffe, Allen, personal communication 2010. District Ecologist, Ontario Ministry of Natural Resources, Aylmer District, Chatham, Ontario.
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 Proposals. 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’s (FSDG) goals and targets.
Recovery planning is intended to benefit species at risk and biodiversity in general. However, it is recognized that strategies may also inadvertently lead to environmental effects beyond the intended benefits. The planning process based on national guidelines directly incorporates consideration of all environmental effects, with a particular focus on possible impacts upon non-target species or habitats. The results of the SEA are incorporated directly into the strategy itself, but are also summarized below in this statement.
Many at-risk and rare species occur in tallgrass prairie habitats. Therefore, it is expected that recovery efforts for Colicroot will also benefit many other species that occur in these habitats and could be conducted in combination with recovery activities for other species such as Dense Blazing Star, Willowleaf Aster and many others (Table 6). Habitat securement, policy, and stewardship approaches are not expected to have adverse effects on the habitat.
Prescribed burning can improve habitat for many rare and at-risk tallgrass prairie species, but burning may also harm some species sensitive to fire. However, fire is recognized as an integral part of this ecosystem and has been used by First Nations people as a management tool for millennia. Therefore, it is intended that any reduction of species sensitive to fire should still result in population levels that fall within the natural range of fluctuations. Monitoring to determine the effects of fire on some species may be necessary. Fire may reduce the presence of woody species to the benefit of tallgrass prairie species. This is not expected to have a significant impact since the encroaching woody species are often common in other habitat types.
|Common Name||Scientific (Latin) Name||SARA Status|
|Climbing Prairie Rose||Rosa setigera||Special Concern|
|Monarch||Danaus plexippus||Special Concern|
|Riddell’s Goldenrod||Solidago riddellii||Special Concern|
|Butler’s Gartersnake||Thamnophis butleri||Threatened|
|Dense Blazing Star||Liatris spicata||Threatened|
|Willowleaf Aster||Symphyotrichum praealtum||Threatened|
|Eastern Foxsnake||Pantherophis gloydi||Endangered|
|Eastern Prairie Fringed-Orchid||Platanthera leucophaea||Endangered|
|Gattinger’s Agalinis||Agalinis gattingeri||Endangered|
|Henslow’s Sparrow||Ammodramus henslowii||Endangered|
|Northern Bobwhite||Colinus virginianus||Endangered|
|Pink Milkwort||Polygala incarnata||Endangered|
|Purple Twayblade||Liparis liliifolia||Endangered|
|Showy Goldenrod||Solidago speciosa||Endangered|
|Skinner’s Agalinis||Agalinis skinneriana||Endangered|
|Slender Bush-clover||Lespedeza virginica||Endangered|
|Small White Lady’s-slipper||Cypripedium candidium||Endangered|
|White Prairie Gentian||Gentiana alba||Endangered|
|Elgin||West Lorne Woods||1986||Extirpated||Extirpation most likely due to natural succession of poplar (Populus sp.), raspberry (Rubus sp.), and sassafras (Sassafras albidum).|
|Essex||Kirk (1987) Essex #2||1987||Extirpated||Extirpated by subdivision development.|
|Essex||Mic Mac Park||1976||Extirpated||Industrial area|
|Lambton||Walpole Island First Nation - Population #3||1984||Extirpated||Part of site converted to agriculture in 1985|
|Lambton||Walpole Island First Nation - Population #4||1958||Extirpated||Not relocated in field work in the 1980s|
|Lambton||Near Sarnia||1896||Extirpated||Not relocated since initial collection.|
|Lambton||NE of Edys Mills||1896||Extirpated||Not relocated since initial collection.|
|Norfolk||Charlotteville Twp, Lot 21 Conc. 6||1954||Extirpated||Area now cultivated.|
|Middlesex||Caradox Twp.||1891||Extirpated||Not relocated since initial collection.|
Colicroot occurs in tallgrass prairie as well as oak savanna vegetation, but other habitats where the species occurs are not easily classified by the Ontario ELC (Lee et al. 1998). These semi-naturalized habitats (Section 7.1.1) do however exhibit a prairie aspect in their type, number and distribution of plant species; therefore, it is useful to know what other plant species frequently occur in conjunction with Colicroot in order to further refine the identification of critical habitat. The information that follows is from Kirk (1988).
In Haldimand-Norfolk County, the known site (population status unknown) is in an old field complex surrounded by Silver Maple (Acer saccharinum) woodland succeeding to Trembling Aspen (Populus tremuloides), White Birch (Betula papyrifera), and Silver Maple. Common associates include goldenrods (Euthamia graminifolia, Solidago juncea, S. hispida), Sensitive Fern (Onoclea sensibilis), Bush Clover (Lespedeza capitata), Spiraea (Spiraea alba), Pale-spiked Lobelia (Lobelia spicata), rushes (Juncus dudleyi, J. greenei, J. effusus), Purple Milkwort (Polygala sanguinea) and Cinquefoil (Potentilla simplex). A dense carpet of Hair Cap Moss (Polytrichum juniperinum) is present.
In Essex County, some sites are in tallgrass prairie with Big Bluestem (Andropogon gerardii), Little Bluestem (Schizachyrium scoparium), Switchgrass (Panicum virgatum), Indiangrass (Sorghastrum nutans), goldenrods (Solidago rigida, S. altissima, S. rugosa), asters (Aster azureus, A. ericoides, A. laevis), Bush Clover, Black-eyed Susan (Rudbeckia hirta), and Dense Blazing Star (Liatris spicata) as well as other less common species.
Other Essex County sites, although not in tallgrass prairie, none the less have a prairie affinity. These sites may have any of the above species as well as:
|English Species name||Latin Species name|
|Culver's root||Veronicastrum virginicum|
|Flowering Spurge||Euphorbia corollata|
|Prairie Loosestrife||Lysimachia quadriflora|
|Purple Milkwort||Polygala sanguinea|
|Prairie Willow||Salix humilis|
|Swamp Thistle||Cirsium muticum|
|Tall Coreopsis||Coreopsis tripteris|
|Tall Ironweed||Vernonia gigantea|
|Tall Nutrush||Scleria triglomerata|
|Two-flowered Cynthia||Krigia biflora|
|Virginia Mountain Mint||Pycnanthemum virginianum|
|Wild Indigo||Baptisia tinctoria|
One Essex site in a moist meadow also has rushes (Juncus brachycarpus, J. greenei), Pinweeds (Lechea villosa, L. leggettii), Hair-like Bulbostylis (Bulbostylis capillaris), Slimspike Threeawn (Aristida longespica), and Orange-grass (Hypericum gentianoides) in addition to the species listed above.
|Global (G) Rank||National (N) Rank|
|Sub-national (S) Rank|
|G5 (Secure – common; widespread and abundant)||N5 (Secure - common; widespread and abundant)||Alabama (SNR)|
District of Columbia(SNR)
New Hampshire (SH)
New Jersey (S4)
New York (S2)
North Carolina (S5)
Rhode Island (S2)
South Carolina (SNR)
West Virginia (S3)
S1: Critically Imperiled; S2: Imperiled; S3: Vulnerable; S4: Apparently Secure; S5: Secure; SNR: Unranked; SH: Possibly Extirpated; SX: Presumed Extirpated; S3?: Inexact Numeric Rank
APPENDIX E: Grids Identified as Containing Critical Habitat for Colicroot (Aletris farinosa) in Canada
|Grid ID||Site Name||UTM Zone||Easting||Northing||Number of Critical Habitat Site Centroids within Grid||Total Site Area(ha) within the Grid that contains Critical Habitat||Land Tenure|
|17LG28_92||HGP #1-1 (Matchette/Malden), HGP #1-2 (Matchette/Malden), HGP #1-4 (Matchette/Malden)||17||329000||4682000||1||2||Non-federal|
|17LG28_91||HGP #1-1 (Matchette/Malden), HGP #1-3 (Matchette/Malden), HGP #1-4 (Matchette/Malden), HGP #1-5 (Matchette/Malden), HGP #1-6 (Matchette/Malden), Ojibway Prairie Provinical Nature Reserve||17||329000||4681000||5||9||Non-federal|
|17LG38_11||HGP #2 (Spring Garden/Lamont)||17||331000||4681000||0||1||Non-federal|
|17LG38_01||HGP #2 (Spring Garden/Lamont),|
Spring Garden Natural Area
|17LG38_10||HGP #3-1 (Huron Church/Todd), HGP #3-2 (Huron Church/Todd), Spring Garden Natural Area||17||331000||4680000||1||13||Non-federal|
|17LG37_19||HGP #3-2 (Huron Church/Todd), HGP #3-3 (Huron Church/Todd)||17||331000||4679000||2||2||Non-federal|
|17LG37_28||HGP #4 (Huron Church Line)||17||332000||4678000||1||1||Non-federal|
|17LG37_29||HGP #4 (Huron Church Line)||17||332000||4679000||0||<1||Non-federal|
|17LG27_89||Ojibway Prairie Provinical Nature Reserve||17||328000||4679000||0||4||Non-federal|
|17LG27_99||Ojibway Prairie Provinical Nature Reserve||17||329000||4679000||0||5||Non-federal|
|17LG28_80||Ojibway Prairie Provinical Nature Reserve||17||328000||4680000||0||17||Non-federal|
|17LG28_81||Ojibway Prairie Provinical Nature Reserve||17||328000||4681000||0||1||Non-federal|
|17LG28_90||Ojibway Prairie Provinical Nature Reserve, 'Ball Diamond'||17||329000||4680000||2||70||Non-federal|
|17LG27_87||Reaume Prairie ESA||17||328000||4677000||0||3||Non-federal|
|17LG27_88||Reaume Prairie ESA||17||328000||4678000||1||12||Non-federal|
|17LG37_09||Spring Garden Natural Area||17||330000||4679000||0||5||Non-federal|
|17LG38_00||Spring Garden Natural Area, 'Ball Diamond'||17||330000||4680000||1||57||Non-federal|
- Based on the standard UTM Military Grid Reference System (Finding UTM References ) and the Ontario Breeding Bird Atlas, where the first 2 digits represents the UTM Zone, the 2 letter code indicates the 100km block, followed by 2 digits to represent the 10km square. The last 2 digits represent the 1km grid containing all or a portion of the critical habitat site.
- The listed coordinates are a cartographic representation of where critical habitat can be found, presented as the southwest corner of the 1km grid containing all or a portion of the critical habitat site. The coordinates may not fall within critical habitat and are provided as a general location only.
- A value of "0" means the grid square contains a portion of (a) critical habitat site(s) but not the site centroid.
- The area presented is that contained within the critical habitat site boundary (rounded up to the nearest 1 ha); therefore, the actual area of critical habitat within this boundary may be significantly less. Field verification is required to determine the precise area of critical habitat. Refer to Refer to Section 7.1 for a description of how critical habitat within these areas is defined.
- Land tenure is provided as an approximation of the types of land ownership that exist at the sites containing critical habitat and should be used for guidance purposes only. Accurate land tenure will require cross referencing critical habitat boundaries with surveyed land parcel information.
- 1common; widespread and abundant
- 2species or community is believed to be extirpated from the jurisdiction
- 3species or community occurred historically in the state/province, and there is some possibility that it may be rediscovered
- 4extremely rare (often 5 or fewer occurrences) or especially vulnerable to extirpation from the jurisdiction because of some factor(s) such as very steep declines
- 5imperiled in the state/province because of rarity due to very restricted range, very few populations (often 20 or fewer), steep declines, or other factors making it very vulnerable to extirpation from the nation or state/province
- 6restricted range, relatively few populations, recent and widespread declines, or other factors make it vulnerable to extirpation
- 7uncommon but not rare; some cause for long-term concern due to declines or other factors
- 8national or subnational conservation status not yet assessed
- 9a wildlife species that is likely to become endangered if nothing is done to reverse the factors leading to its extirpation or extinction
- 10a species that is at risk of becoming endangered in Ontario if limiting factors are not reversed
- 11the flower-bearing stalk of a plant containing a cluster of flowers arranged along a common axis with oldest flowers at the base
- 12a thick layer of dead organic material, including grass, leaves, stems and roots, that builds up at the base of living grass
- 13a relationship in which one or both organisms cannot exist apart from the other
- 14Five populations are currently known to be extant. The status of three others is unknown and requires field verification.
- 15The ELC framework in Ontario is currently being revised to further distinguish between different types of cultural habitats in addition to various native open habitat ecotypes (Lee pers. comm. 2012) and may be useful to define habitat suitability for Colicroot in the future. In addition, identification of associate plant species found in Colicroot habitat (Appendix C) may help further refine suitable Colicroot habitat.
- 16The NHIC maintains records of populations as extant unless new information is received proving/indicating that apopulation no longer exists. However, if no new information is obtained in 20 years, a population is presumed to be historic.
- 17Planning for a Sustainable Future: A Federal Sustainable Development Strategy for Canada
- Date Modified: