Pugnose Shiner (Notropis anogenus): recovery strategy

Official title: Recovery Strategy for the Pugnose Shiner (Notropis anogenus) in Canada

Preface

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 the 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 a recovery strategy for species listed as extirpated, endangered, or threatened and are required to report on progress 5 years after the publication of the final document on the Species at Risk Public Registry, until its objectives have been met or recovery is no longer deemed feasible.

The Minister of Fisheries and Oceans and the Minister responsible for Parks Canada (PC) are the competent ministers under SARA for the Pugnose Shiner and have prepared this amended recovery strategy, as per section 37 of SARA. In preparing this amended recovery strategy, the competent ministers have considered, as per section 38 of SARA, the commitment of the Government of Canada to conserving biological diversity; and to the principle that, if there are threats of serious or irreversible damage to the listed species, cost-effective measures to prevent the reduction or loss of the species should not be postponed for a lack of full scientific certainty. To the extent possible, this amended recovery strategy has been prepared in cooperation with the Ontario Freshwater Fish Recovery Team, Ministry of Northern Development, Mines, Natural Resources and Forestry, Ontario Parks, Ausable Bayfield Conservation Authority, Essex Region Conservation Authority, Trent University, University of Western Ontario, St. Clair Region Conservation Authority, Cataraqui Region Conservation Authority, Quinte Region Conservation Authority, the Saugeen Valley Conservation Authority, the St. Lawrence River Institute, and the Mohawk Council of Akwesasne, as per section 39(1) of SARA.

As stated in the preamble to SARA, 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 amended recovery strategy and will not be achieved by Fisheries and Oceans Canada (DFO), PC, or any other jurisdiction, alone. The cost of conserving species at risk is shared amongst different constituencies. All Canadians are invited to join in supporting and implementing this amended recovery strategy for the benefit of the Pugnose Shiner and Canadian society as a whole.

Action plans provide information on recovery measures to be taken by DFO, PC and other jurisdictions and/or organizations involved in the conservation of the species. Action plans that implement activities that benefit Pugnose Shiner have already been posted for the Ausable River watershed (including the Old Ausable Channel) by DFO (2020), and the Thousand Islands National Park by PC (2016). Implementation of this amended recovery strategy is subject to appropriations, priorities, and budgetary constraints of the participating jurisdictions and organizations.

Acknowledgments

Amendments to the “Recovery Strategy for the Pugnose Shiner (Notropis anogenus) in Canada” (2012) were undertaken by Peter Jarvis (DFO contractor) and Joshua Stacey (DFO, Species at Risk Biologist) on behalf of DFO. The original recovery strategy (2012) was prepared by Andrea Doherty (DFO), Amy L. Boyko (DFO), Sarah P. Matchett (DFO) and Shawn K. Staton (DFO). DFO would like to thank the following organizations for their support in the development of the amended Pugnose Shiner recovery strategy: Ontario Freshwater Fish Recovery Team, Ontario Ministry of Natural Resources and Forestry, Ontario Parks, Ausable Bayfield Conservation Authority, Essex Region Conservation Authority, Trent University, Environment and Climate Change Canada (Canadian Wildlife Service), University of Western Ontario, Parks Canada Agency, St. Clair Region Conservation Authority, Cataraqui Region Conservation Authority, Quinte Region Conservation Authority, the Saugeen Valley Conservation Authority, the St. Lawrence River Institute, and the Mohawk Council of Akwesasne. Mapping provided by Andrew Geraghty (DFO).

Executive summary

The Pugnose Shiner (Notropis anogenus) was listed as endangered under the Species at Risk Act (SARA) in 2003. In 2013, the Committee on the Status of Endangered Wildlife in Canada (COSEWIC) re-assessed the species and reclassified it as threatened, principally due to the discovery of new sub-populations. The Pugnose Shiner was down-listed to threatened under SARA in 2019. This amended recovery strategy is part of a series of documents for this species that are linked and should be taken into consideration together; these documents include the COSEWIC status reports (COSEWIC 2002, 2013), a recovery potential assessment (RPA) (DFO 2010), the original recovery strategy (DFO 2013), the report on the progress of recovery strategy implementation (DFO 2022), the Ausable River Action Plan (DFO 2020), and the “Multi-Species Action Plan for Thousand Islands National Park” (PCA 2016). Recovery has been determined to be biologically and technically feasible.

The Pugnose Shiner is a small minnow (typically 4 to 5 cm) distinguished from similar species by its tiny, near vertically upturned mouth. A dark lateral stripe extends the length of the body and scales on the back are darkly outlined, while the underside is mostly silver in colour. The Pugnose Shiner is mostly associated with shallow areas of lakes or slow-moving rivers with abundant submerged aquatic vegetation. In Canada, its distribution is limited to 4 main regions of Ontario: the southern drainage of Lake Huron; Lake St. Clair; Lake Erie; and Lake Ontario/St. Lawrence River. The species was known historically from Point Pelee National Park and Rondeau Bay (Lake Erie), and the Gananoque River (St. Lawrence River tributary).

The main threats facing the species are described in section 5 and include: habitat modifications, aquatic vegetation removal, sediment loading and turbidity, nutrient loading, and invasive species.

The population and distribution objectives (section 6) for the Pugnose Shiner are:

Population objective: To ensure that populations at 15 locations demonstrate signs of reproduction and recruitment, and are stable or increasing, with low risk of known threats.

Distribution objective: To ensure the survival of self-sustaining sub-populations at the following currently occupied locations:

Teeswater River, Old Ausable Channel, Mouth Lake, Maxwell Creek, Little Bear Creek, St. Clair Unit of the St. Clair National Wildlife Area (NWA), Long Point Bay (Including Long Point Bay NWA) /Big Creek (including Big Creek NWA), Trent River, Wellers Bay (including Wellers Bay NWA), West Lake, East Lake, Waupoos Bay, St. Lawrence River and Gananoque River in the Thousand Islands National Park - Gananoque area, St. Lawrence River in the Thousand Islands National Park in the Grenadier Island/Mallorytown Landing area, and Lake St. Lawrence in the St. Lawrence River.

A description of the broad strategies to be taken to address threats to the species’ survival and recovery, as well as research and management approaches needed to meet the population and distribution objectives, are included in section 7. These will help inform the development of specific recovery measures in 1 or more action plans.

For the Pugnose Shiner, critical habitat (section 8) is identified to the extent possible, using the best available information, and provides the functions and features necessary to support the species’ lifecycle processes and to achieve the species’ population and distribution objectives. This amended recovery strategy identifies critical habitat for the Pugnose Shiner in the Teeswater River, Old Ausable Channel, Mouth Lake, Maxwell Creek, Little Bear Creek, St. Clair Unit of the St. Clair NWA, Long Point Bay (including Long Point Bay NWA)/Big Creek (including Big Creek NWA), the Trent River, Wellers Bay (including Wellers Bay NWA), West Lake, East Lake, Waupoos Bay, and 3 areas within the St. Lawrence River.

Recovery feasibility summary

Recovery of the Pugnose Shiner is believed to be both biologically and technically feasible.

1. Are individuals of the wildlife species that are capable of reproduction available now or in the foreseeable future to sustain the population or improve its abundance?

Yes. Reproducing populations of Pugnose Shiner currently exist in the Old Ausable Channel, Long Point Bay (Lake Erie, Lake St. Clair, Trent River, Wellers Bay, East Lake, West Lake, Waupoos Bay, and the St. Lawrence River, and could provide a basis for natural expansions and potential translocations or artificial propagation, if necessary.

2. Is sufficient suitable habitat available to support the species or could it be made available through habitat management or restoration?

Yes. Suitable habitat is present at several locations where extant populations exist, particularly the Old Ausable Channel, the area around Walpole Island (Lake St. Clair), within bays of Prince Edward County, and the Upper St. Lawrence River (from Eastview to Lancaster). Improved water quality and habitat management (through stewardship and Best Management Practices [BMPs]) could restore suitable habitat in locations where Pugnose Shiner populations have been extirpated or are in decline.

3. Can significant threats to the species or its habitats be avoided or mitigated?

Yes. Threats believed to pose a serious risk to Pugnose Shiner, such as siltation/turbidity and the removal of aquatic vegetation, can be addressed through recovery actions. Identifying and remediating sources of nutrients and suspended sediments affecting the health of occupied coastal wetlands will be critical to ensuring that these habitats can continue to support the Pugnose Shiner (EERT 2008).

4. Do recovery techniques exist to achieve the population and distribution objectives or can they be expected to be developed within a reasonable timeframe?

Yes. Techniques to reduce identified threats (for example, BMPs) and restore habitats are well known and have proven to be effective for the fish community in general. Projects conducted through the Habitat Stewardship Fund may lead to habitat improvements in areas where Pugnose Shiner occurs.

1 Introduction

The Pugnose Shiner (Notropis anogenus) was originally listed as endangered under the Species at Risk Act (SARA) in 2003; however, in 2013 the Committee on the Status of Endangered Wildlife in Canada (COSEWIC) re-assessed the species and reclassified it as threatened. It was subsequently down-listed under SARA in 2019. This amended recovery strategy is part of a series of documents regarding Pugnose Shiner that should be taken into consideration together, including the COSEWIC status reports (COSEWIC 2002, 2013) and the science advisory report from the recovery potential assessment (RPA) (DFO 2010), the original recovery strategy (DFO 2013), the “Report on the Progress of Recovery Strategy Implementation for the Pugnose Shiner (Notropis anogenus) in Canada for the Period 2012-2017” (DFO 2022), the “Action Plan for the Ausable River: An Ecosystem Approach” (DFO 2020), and the “Multi-Species Action Plan for Thousand Islands National Park”(PCA 2016). A recovery strategy is a planning document that identifies what needs to be done to arrest or reverse the decline of a species. It sets objectives and identifies the main areas of activities to be undertaken. Further detailed planning is done at the subsequent action plan stage.

The RPA is a process undertaken by Fisheries and Oceans Canada (DFO) Science to provide the information and scientific advice required to implement SARA, relying on the best available scientific information, data analyses and modelling, and expert opinions. The outcome of this process informs many sections of the amended recovery strategy. For more detailed information beyond what is presented in this amended recovery strategy, refer to the COSEWIC status report and the RPA science advisory report for this species.

2 COSEWIC species assessment information

Date of assessment: May 2013

Species’ common name: Pugnose Shiner

Scientific name: Notropis anogenus

Status: Threatened

Reasons for designation: The species has a small area of occupancy and consists of numerous small populations, many of which may not be viable. At least 2 populations have been extirpated. Habitat degradation and loss continues to threaten populations, particularly in the western part of their distribution in the Lake Huron, Lake St. Clair and Lake Erie watersheds.

Canadian occurrence: Ontario

Status history: Designated special concern in April 1985. Status re-examined and designated endangered in November 2002. Status re-examined and designated threatened in May 2013.

3 Species status information

a. Only the Species at Risk Act and the Ontario Endangered Species Act provide protection. All other entries are provincial, national or international status assessments.

b. NatureServe (2018): G = global status; N = national status; S = subnational status; 1 = critically imperiled; 2 = imperiled ; 3 = vulnerable.

c. NatureServe (2018): G = global status; N = national status; S = subnational status; 1 = critically imperiled; 2 = imperiled ; 3 = vulnerable.

d. Refer to NatureServe (2018) for state-specific designations.

Upon listing as a threatened species, the Pugnose Shiner became protected wherever it is found in Canada by section 32 of SARA:

“No person shall kill, harm, harass, capture or take an individual of a wildlife species that is listed as an extirpated species, an endangered species or a threatened species.” [subsection 32(1)]

“No person shall possess, collect, buy, sell or trade an individual of a wildlife species that is listed as an extirpated species, an endangered species or a threatened species, or any part or derivative of such an individual.” [subsection 32(2)]

Under section 73 of SARA, the competent ministers may enter into an agreement or issue a permit authorizing a person to engage in an activity affecting a listed wildlife species, any part of its critical habitat, or its residences.

4 Species information

4.1 Description

The Pugnose Shiner (figure 1) is a slender, moderately compressed, silvery minnow with a lateral black stripe, and a blunt snout ending in a small, upturned, mouth (Becker 1983; Leslie and Timmins 2002; Holm et al. 2010; Page and Burr 2011). Total length averages 38 to 51 mm, while the largest recorded individual was 72 mm (Becker 1983; Scott and Crossman 1998). Overall, colouration is silvery with pale yellow tints on the back. This species is sexually dimorphic during the breeding season when the males take on a bright golden colouration (Smith 1985). The dark lateral band extends from the snout through the eye to the end of the caudal peduncle, terminating in a small, dark, wedge-shaped caudal spot. All fins are transparent and, unlike other Notropis species, the peritoneum (lining of abdominal cavity) is black (Page and Burr 2011). The mouth is positioned almost vertical to the body axis (Becker 1983) and is the distinguishing feature that separates the Pugnose Shiner from other species in the black-lined shiner group, especially when they are age 0 juveniles (Leslie and Timmins 2002). This species is most similar in appearance to the Blackchin Shiner (N. heterodon), which is distinguished from the Pugnose Shiner by its larger mouth (Holm et al. 2010). The Pugnose Shiner is also similar in appearance to the Pugnose Minnow (Opsopoeodus emiliae) and Bridle Shiner (N. bifrenatus). The Pugnose Minnow can be distinguished from the Pugnose Shiner by dark areas on the dorsal fin, crosshatched areas on the upper surface, and 9 dorsal rays (the Pugnose Shiner typically has 8 dorsal rays) (Page and Burr 2011; Scott and Crossman 1998). The Bridle Shiner is distinguished from the Pugnose Shiner by its larger, upturned mouth, 7 anal rays, and incomplete lateral line (Scott and Crossman 1998; Page and Burr 2011).

4.2 Population abundance and distribution

4.2.1 Global distribution and population abundance

The Pugnose Shiner has a limited and fragmented distribution in North America (figure 2). It is predominantly found in the Mississippi River and Great Lakes basins, but also in tributaries of the Hudson Bay basin (Page and Burr 2011). It is found in several tributaries of the upper Mississippi River in Illinois, Minnesota and Wisconsin, and in the upper Red River drainage in Minnesota and North Dakota (Hudson Bay basin). Within the Great Lakes basin, the Pugnose Shiner is known from tributaries of lakes Huron, Michigan, St. Clair, Erie, eastern Lake Ontario, and the upper St. Lawrence River. A global population estimate is unavailable, but ongoing declines seem likely as a result of threats including increased turbidity, loss of aquatic vegetation, and invasive species (McCusker et al. 2014a).

4.2.2 Canadian distribution

In Canada, the Pugnose Shiner has been recorded in 4 main areas of Ontario (figure 3a, 3d): southern Lake Huron, Lake St. Clair, Lake Erie, and eastern Lake Ontario/upper St. Lawrence River. The locations where Pugnose Shiner has been detected within Canada are summarized in table 2 and shown in figures 3a to 3e. Temporal changes in distribution of the species are difficult to assess due to a lack of data, which can be partly attributed to the species’ small size and difficulties with field identification. Scott and Crossman (1998) described the Canadian range of Pugnose Shiner as diminishing and surmised that it probably occurred historically between the 2 widely separated areas where it is now found, along the northern shores of lakes Erie and Ontario. Pugnose Shiner was last captured from the Gananoque River in 1935, Point Pelee National Park in 1941, and Rondeau Bay in 1963; hence, it is thought to be extirpated from these locations, as all subsequent sampling has failed to detect the species (Holm and Mandrak 2002; DFO 2010). Recent discoveries of the species (detected since the publication of the original recovery strategy in 2012) have occurred in a variety of new locations across its Canadian range, including the St. Clair River, coastal wetlands of Lake St. Clair, West Otter Creek, Sydenham River, Detroit River, Trent River (emptying into the Bay of Quinte), South Bay (Bay of Quinte), and further locations within the St. Lawrence River (table 2), suggesting the species may be more widely distributed than was previously reported. For further information on survey efforts, refer to COSEWIC (2013) and DFO (2018a).

a. Ausable Bayfield Conservation Authority

b. Ministry of Natural resources and Forestry

4.2.3 Canadian population abundance and status

Abundance estimates are lacking for the majority of Pugnose Shiner populations in Canada, making temporal trends difficult to evaluate (COSEWIC 2014). The status of Pugnose Shiner populations in Canada was assessed by Bouvier et al. (2010) (table 3). Since 2010, new information, including new locations, has been added to table 3. Populations were ranked with respect to abundance and trajectory estimates based on best available information. Population abundance and trajectory estimates were then combined to determine the population status. A certainty level was also assigned to the population status, which reflected the lowest level of certainty associated with either population abundance or trajectory. Refer to Bouvier et al. (2010) for further details on the methodology.

a. Certainty: 1=quantitative analysis; 2=Catch Per Unit of Effort or standardized sampling; 3=best guess.

b. Population was not included in Bouvier et al. (2010).

c. Note that, for lack of supporting data, the location was assumed to have a single population when population status was assessed by Bouvier et al. (2010).

Since the assessment of Pugnose Shiner populations by Bouvier et al. (2010), there has been substantial sampling which, in some cases, may further inform understanding of the status of these populations. Furthermore, Pugnose Shiner has been detected at new locations that were not included in the original assessment. New information, including new locations where Pugnose Shiner has been detected is discussed below. A new assessment of Pugnose Shiner populations is warranted, should an updated RPA be conducted in the future.

Lake Huron drainage

Teeswater River: The first record of Pugnose Shiner from the Teeswater River, located in the Saugeen River watershed, was in 2005 when 3 specimens were captured at locations below the Cargill Mill Dam as well as above the dam in Cargill Mill Pond (D’Amelio pers. comm. 2005; Marson et al. 2009; DFO 2010). Pugnose Shiner was subsequently detected in 2009 (1 specimen), 2010 (25 specimens) and 2013 (1 specimen), all of which were detected in Cargill Mill Pond. No sampling has been conducted for Pugnose Shiner at this location since 2013.

Limited sampling had been conducted at the time of the original population assessment, which contributed to a status of “Unknown” (table 3), and very little sampling has been conducted since that time. Furthermore, all of the sampling that has occurred has been conducted within a small area of the river at Cargill Mill Pond. Currently the area of occupied critical habitat identified is less than the minimum area for population viability (MAPV) (table 8), which may suggest that this population is vulnerable to habitat perturbations.

Old Ausable Channel (OAC): Pugnose Shiner was first collected from the OAC in the early 1980s (ARRT 2006). Between 1982 and 2010, the OAC was sampled extensively, with a variety of gear types, relative to some other Canadian Pugnose Shiner populations. The population in the OAC is believed to have declined in recent years, as only 21 specimens were captured during a survey in 1997 compared to 110 in 1982, despite an increase in effort (Holm and Boehm 1998; ARRT 2006). In 2002, DFO sampled a 5 km reach of the OAC using various gear types and caught 43 Pugnose Shiner, only 7 of which were caught in the 1 km reach sampled in 1982 and 1997, suggesting a further decline. However, DFO did not use a beach seine, as was the sampling method employed by Holm and Boehm (1998), making inter-annual comparisons difficult. In 2004 and 2005, the species was detected more frequently, with a total of 291 Pugnose Shiner captured throughout the OAC (DFO, unpublished data). In 2010, the Pugnose Shiner was captured for the first time outside of the Pinery Provincial Park. Since 2010,7 specimens (in 2012) and 1 specimen (in 2015) have been detected as the result of limited sampling efforts. Bouvier et al. (2010) originally assessed this population as fair in status (table 3) and subsequent sampling has been too limited to indicate otherwise.

L Lake: L Lake is a small lake that is located near the OAC and contains similar habitat. This location was sampled in 2007 and 2010 by DFO but Pugnose Shiner was not captured, despite the fact that Lake Chubsucker (Erimyzon sucetta) (a species often found in association with Pugnose Shiner) and other black-lined shiners were detected (DFO, unpublished data). Further sampling at this location and other oxbow lakes near the OAC may detect the presence of the species in the future.

Mouth Lake: Mouth Lake, which is also located near the OAC and L Lake, and contains similar habitat, was sampled in 2010 by DFO at 4 sites and a total of 30 Pugnose Shiner were captured (DFO, unpublished data). The population status is unknown for Mouth Lake and it is uncertain if enough suitable habitat exists to support the minimum area for population viability (MAPV), suggesting that this population may be vulnerable to habitat perturbations.

Lake St. Clair drainage

St. Clair River: A total of 2 specimens were captured for the first time in 2012 (DFO 2022). More sampling is required before population status can be inferred.

Lake St. Clair: A total of 223 Pugnose Shiner have been captured in Mitchell’s Bay as a result of sampling conducted in 1983, 1996, 2003, 2006, and 2007 (Holm and Mandrak 2002; DFO, unpublished data; ROM, unpublished data; Soper pers. comm. 2010). Pugnose Shiner continued to be detected in Mitchell’s Bay in 2011, 2012, 2017, 2018, and 2019 during surveys conducted by DFO and the Ontario Ministry of Natural Resources and Forestry (MNRF). Sampling conducted in 1983 led to the detection of Pugnose Shiner in St. Luke’s Bay, and sampling conducted by DFO in 2006 yielded 10 specimens (Holm and Mandrak 2002; DFO, unpublished data; ROM, unpublished data). Further sampling conducted by the MNRF in 2012, 2013, 2014, 2015, 2016, and 2017 led to the detection of 160 specimens throughout St. Luke’s Bay and 1 specimen was captured by DFO in 2018 (DFO 2022).

The delta channels and freshwater coastal marshes of Walpole Island, located at the north end of Lake St. Clair, yielded 281 individuals during a survey in 1999 (Holm and Mandrak 2002) and 3 specimens were captured in 2002 (ROM, unpublished data). Pugnose Shiner has subsequently been captured in the Walpole Island/St. Clair Delta at locations including Chematogen Channel, Snook’s Lake, Swan Lake, Mallard Drain, Goose Lake, Johnston Bay and Channel, as well as other unnamed bays in surveys conducted in 2001, 2002, 2016, and 2018 leading to the capture of 588 individuals. Similarly, 330 Pugnose Shiner have been detected throughout Chenail Ecarté/The Snye in surveys conducted 1999, 2010, 2012, 2015, 2017, 2018, and 2019 (table 2, figure 3c), indicating that there is likely a fair population at this location.

Additional sites in Lake St. Clair (31 sites) were sampled in 2007 by the Essex Region Conservation Authority; however, no Pugnose Shiner were captured (Nelson and Staton 2007). Since that time, Pugnose Shiner was captured through non-target surveys at 2 locations along the south shore of Lake St. Clair for the first time in 2011 (table 2, figure 3c).

The species was detected for the first time from the western diked marsh in the St. Clair Unit of the St. Clair National Wildlife Area (NWA) in 2003 and was caught again in 2004 (Bouvier et al. 2010). DFO conducted extensive sampling in the east cell of St. Clair Unit of the St. Clair NWA in 2017 and 2018; however, Pugnose Shiner was not detected.

The populations within Lake St. Clair were originally assessed as fair in Bouvier et al. (2010). Since then, the species has continued to be detected, and has been detected more frequently and over a broader distribution than previously understood; therefore, there is no reason to believe the population status has worsened since the 2010 assessment was conducted.

Lake St. Clair tributaries were not included in the original population assessment (Bouvier et al. 2010); however, the recovery strategy (DFO 2013) grouped Whitebread Drain/Grape Run and Little Bear Creek with Lake St. Clair under an assessment of “f” status. Since that time Pugnose Shiner has been detected in several other tributaries such as the Sydenham River, West Otter Creek, and Maxwell Creek. The potential status of populations within these aforementioned tributaries is discussed below.

Whitebread Drain/Grape Run: A total of 3 Pugnose Shiner were captured in this tributary to Lake St. Clair in 2003. Since that time, no sampling has been conducted; therefore, the distribution and abundance of Pugnose Shiner at this location is currently unknown.

Sydenham River and West Otter Creek: Pugnose Shiner was detected near the confluence of the Sydenham River and Chenail Ecarté (The Snye) in 2015 and 2017. The species was captured further upstream in the Sydenham River in 2016 at a location between Wallaceburg and Chenail Ecarté (The Snye), as well as West Otter Creek in 2013, which is within the Sydenham River watershed (table 2, figure 3c). Extensive sampling was conducted in 2019 using a mamou trawl to target another species, Pugnose Minnow, at 4 sites in the Lower Sydenham River near where Pugnose Shiner was detected, as well as at 16 sites in the East Sydenham River and 18 sites in the North Sydenham River (Barnucz and Drake 2021); however, no Pugnose Shiner were captured despite the suitability of the gear type. No follow-up sampling has been conducted in Otter Creek to further investigate the presence and distribution of Pugnose Shiner. Given the limited detections of Pugnose Shiner within the Sydenham River watershed, its status and distribution is currently unknown.

Maxwell Creek: Pugnose Shiner was detected in Maxwell Creek for the first time in 2010. Since that time, no targeted surveys have been conducted for the species. Non-target surveys were conducted in 2013, which did not yield any new detections (DFO 2022); however, sampling conducted at 2 sites in 2019 for another species at risk, Pugnose Minnow, led to the detection of 53 Pugnose Shiner. Pugnose Shiner populations within Maxwell Creek were not assessed in Bouvier et al. (2010); however, it seems likely its status is “fair” at this location.

Little Bear Creek: In 2003, DFO completed targeted, wadeable, surveys for fish species at risk in tributaries of Lake St. Clair and captured 2 Pugnose Shiner in Little Bear Creek (Mandrak et al. 2006b). In 2006,9 specimens were captured from MacLeod Creek, a drain that flows into Little Bear Creek (ROM, unpublished data). Since that time, the species has been frequently captured in surveys conducted in 2010, 2013, 2014, 2015, and 2019 (263 individuals) (DFO unpublished data; Reid et al. 2016) at new sites that fill in gaps between older records and extend further upstream of them (table 2). These new detections support an assessment of “f” status for populations at this location, which is consistent with the status assigned to Lake St. Clair and tributaries in the 2013 recovery strategy (DFO 2013). The status of populations found in Little Bear Creek was not assessed in Bouvier et al. (2010) and there is no information to indicate if the population size is equal to, or exceeds, the minimum viable population size for Pugnose Shiner described by Venturelli et al. (2010); however, habitat modelling conducted by Montgomery et al. (2018) suggests that there is enough suitable habitat at this location to meet the minimum area for population viability in riverine habitats that was reported by Venturelli et al. (2010)^{Footnote 1}.

Lake Erie drainage

Detroit River: Pugnose Shiner was detected for the first time in the Detroit River in 2011 where Lake St. Clair outlets into the Detroit River; however, other non-target surveys conducted in 2011 and between 2013 to 2017 did not detect the species (DFO 2022). Pugnose Shiner is also thought to be present in the Canard River, suggesting that the species may occur in other locations within the Detroit River. At this point, there is not enough information regarding the distribution and abundance of the species at this location; therefore, the status of populations is unknown.

Canard River: Pugnose Shiner was first detected in in the Canard River in 1994, relatively close to the confluence with the Detroit River, where 4 specimens were captured (ROM, unpublished data). Another specimen was captured in 2003 further downstream; however, there is uncertainty associated with the identification of this individual. Currently, the status and distribution of populations at this location is unknown. Significant non-target sampling for another species at risk, the Pugnose Minnow, has occurred throughout the Canard River where Pugnose Shiner has been historically detected (Gáspárdy et al. 2020); however, no Pugnose Shiner were captured during these surveys. This suggests that the abundance of Pugnose Shiner is likely low at this location, if it still occurs there at all.

Point Pelee National Park: Pugnose Shiner was first detected in Point Pelee National Park in 1940, and has not been captured at this location since 1941 despite repeated sampling over the years. The species is considered to be extirpated from this location (Bouvier et al. 2010).

Rondeau Bay: Pugnose Shiner was first captured in Rondeau Bay in 1940 and subsequently in 1963; however, it has not been captured in Rondeau Bay since, and is considered to be extirpated (Bouvier et al. 2010).

Long Point Bay: The species was first recorded within Inner Long Point Bay in 1947 and was subsequently detected in 1985 and 1986. Between 2002 and 2009, 100 specimens were captured in the Inner Long Point Bay, and, in the last decade Pugnose Shiner has been consistently captured (2,397 specimens) by DFO and other partner organizations around the inner bay, including in the Crown Marsh, the Old Cut, Long Point Provincial Park, and the Thoroughfare Unit of Long Point NWA (Long Point NWA), composed of 2 units. For more details regarding detections refer to table 2.

Pugnose Shiner was also captured within Big Creek NWA in 2007 and 2008 (15 specimens) and again in 2010, 2014 and 2017 (3 specimens). The species was first detected within the Long Point Unit of Long Point NWA (outer bay/point) in surveys conducted from 2007 to 2009 (19 specimens); and subsequent sampling in this area that was conducted in 2016 and 2017 has led to substantial detections (398 specimens).

Pugnose Shiner was first captured in Turkey Point in 2004 (3 specimens), and was detected in surveys conducted in 2007 (44 specimens). In 2011, the species was detected further into the marshes of Turkey Point in the Cannon Ball Marsh (2 specimens).

Populations found at Long Point Bay were originally assessed as “p” in Bouvier et al. (2010), despite the fact that the species was detected in higher density, at that time, than in Lake St. Clair, which was assessed as “f”. Since this assessment was conducted, Pugnose Shiner has been consistently detected in relatively high numbers at occupied locations and likely is present at historical locations that have been inadequately sampled (that is, Thoroughfare Unit up to Long Point NWA, Big Creek NWA). The frequent detections of this species over the last 10 years brings into question the status of “p” assessed by Bouvier et al. (2010), suggesting that the population status needs to be reassessed.

Lake Ontario drainage

Trent River: Pugnose Shiner was first captured in the Trent River by the MNRF in 2011 (52 specimens) and subsequently in 2012 (2 specimens). Further targeted sampling was conducted in 2020 using mamou trawls. A total of 66 sites were sampled, which included 5 reaches (Seymour Lake, Crowe Bay, Percy Boom, Glen Ross, and Trenton) between Rice Lake and the Bay of Quinte; however, Pugnose Shiner were only captured in the Glen Ross reach (66 specimens) at locations where the species was detected in 2011, as well as sites up to 2.5 km further upstream (Lebaron and Reid 2021). The status of populations is currently unknown.

Wellers Bay: Pugnose Shiner was captured in Wellers Bay (Prince Edward County, eastern Lake Ontario) for the first time in 2010 (65 specimens). No relevant sampling has been conducted at this location since 2010. Considering Pugnose Shiner had not been detected in Wellers Bay at the time that the RPA was being undertaken (Bouvier et al. 2010), this location was not included in the population status assessment. However, the status of this population was described as “u” in the original Pugnose Shiner recovery strategy (DFO 2013).

West Lake: Pugnose Shiner was detected for the first time in West Lake (Prince Edward County, eastern Lake Ontario) in 2009. There were 2 specimens were collected during an electrofishing study conducted by DFO in June 2009 (DFO, unpublished data), and another 32 specimens were captured in September 2009 as a result of targeted sampling for the species (DFO, unpublished data). Subsequent targeted sampling around the lake in 2010 yielded an additional 71 Pugnose Shiner (DFO, unpublished data). Non-target sampling was conducted by the MNRF in 2013 and DFO in 2015^{Footnote 2}, leading to the capture of 39 and 9 specimens, respectively. The population or populations found in West Lake were assessed as having an unknown status by Bouvier et al. (2010) and no further information has become available that would change this status.

East Lake: Pugnose Shiner was first detected in East Lake (Prince Edward County, eastern Lake Ontario) through sampling events conducted by DFO in 2010 (116 specimens). Subsequent sampling conducted by external agencies in 2013 also led to the capture of the species (9 specimens). East Lake was not included as a location in the population status assessment from Bouvier et al. (2010) and was given a status of “u” in the original recovery strategy (DFO 2013).

South Bay: Pugnose Shiner was detected for the first time through non-target sampling conducted by DFO in South Bay (Prince Edward County, eastern Lake Ontario, inlet of Prince Edward Bay) in 2014 (1 specimen). No subsequent sampling has taken place at this location and the status of populations at this location is currently unknown.

Waupoos Bay: The species was first detected by DFO in Waupoos Bay (Prince Edward County, eastern Lake Ontario, inlet of Prince Edward Bay) in 2010 (179 specimens). No subsequent sampling has been conducted at this location and the status of populations is currently unknown.

St. Lawrence River Drainage

Gananoque River: Pugnose Shiner was first collected in the Gananoque River in 1935, when it was captured near its confluence with the St. Lawrence River in 1937, just upstream of the Water Street bridge. The species was not detected at this location in subsequent years of sampling and was considered extirpated at the time the RPA was developed (Bouvier et al. 2010). However, the species was again captured in the Gananoque River in 2013 (2 specimens) during a non-target survey conducted by DFO approximately 350 m upstream of the mouth of the St. Lawrence River. The current status of populations within the Gananoque River is unknown and further sampling is required to get a better understanding of the species abundance and distribution.

St. Lawrence River: Pugnose Shiner was first detected within the Canadian waters of the St. Lawrence River in 1935 near MacDonald Island, which is in close proximity to Gananoque (Toner 1937, as cited in Holm and Mandrak 2002). The species was then detected east of this area near Mallorytown landing in 1989 and west of this area in 1994 near Eastview where it was captured again in 2009 (4 specimens). Non-targeted sampling was conducted by DFO at sites between Gananoque and Mallorytown Landing in 2005 (256 specimens) and 2009 (123 specimens). Targeted sampling was conducted by DFO throughout these areas in 2010, leading to the capture of 221 individuals. Furthermore, Parks Canada (PC) conducted sampling (both inside and outside of the Thousand Islands National Park boundaries) from east of Mallorytown Landing to Wolfe Island near Kingston in 2011 (Van Wieren pers. comm. 2011) (570 specimens), 2013 (95 specimens), 2014 (38 specimens), 2016 (123 specimens), 2017 (238 specimens), and 2018 (18 specimens). In addition, surveys targeting Pugnose Shiner were conducted along the shoreline of the mainland across from Grenadier Island by McGill University in 2018 (257 specimens). In 2019, PC, in partnership with Muskies Canada and the MNRF, captured a total of 34 Pugnose Shiner at locations including Botswick, Sugar, Ash, and Grenadier islands as part of their long-term monitoring program.

Since the original recovery strategy, which included records up to 2010, the Pugnose Shiner distribution has been discovered to be far more widespread, extending downstream past the Moses Saunders Dam in Cornwall to the Lancaster area. Moving from upstream to downstream, the species was detected: near Brockville in 2016 (94 specimens) during surveys conducted by the St. Lawrence River Institute; during targeted surveys conducted by DFO approximately 30 km upstream near Johnstown in 2011 (8 specimens); along the shores of Drummond Island in 2017 by the St. Lawrence River Institute (4 specimens); near the entrance to Flagg Bay/Flagg Creek in 2017 (1 specimen) and along the shore of Riverside-Cedar Park in 2016 (5 specimens) by the St. Lawrence River Institute; during targeted surveys conducted by DFO in 2011 that led to detections within a bay adjacent to Chrysler Park (10 specimens), in a bay adjacent to Farran Park (4 specimens), near Long Sault Parkway Park, West Woodlands Island (1 specimen), and on the shore of Mille Roches Island (1 specimen); and during surveys conducted by the St Lawrence River Institute along the shores of the Long Sault Parkway Park, including East Woodlands Island in 2015 (6 specimens) and 2017 (7 specimens), Macdonell Island in 2016 (9 specimens) and 2017 (3 specimens), as well as Sheek Island in 2015 (85 specimens), and just upstream along the shore of the mainland at Guindon Park (10 specimens).

Pugnose Shiner was detected for the first time below the Moses Saunders Dam in Cornwall by PC, in partnership with the Mohawks of Akwesasne, in 2014 along the Thompson Island shoreline. Similarly, the St. Lawrence River Institute captured Pugnose Shiner below the dam in 2015 at: 1 site at Cornwall Island (5 specimens); along the shore of the Rotary Eco Gardens across from Cornwall Island (72 specimens); at Ile Corn in 2015 (1 specimen); at Ile Christatie (5 specimens); and at a site along the shore approximately 1 km upstream of the mouth of the Raisin River (1 specimen). Pugnose Shiner was also captured in 2016 at 1 site in the Colquhoun Islands (9 specimens); and in 2017 along the shore of South Lancaster, approximately 500 m downstream of the mouth of the Raisin River. The detection made along Ile Corn and Ile Christatie represent the first detections of Pugnose Shiner within Quebec waters.

4.3 Needs of the Pugnose Shiner

Habitat and biological needs: Habitat and biological needs of Pugnose Shiner are summarized below. Refer to the COSEWIC status report (COSEWIC 2013) and/or the RPA (DFO 2010) for more detailed information on habitat and biological needs of the Pugnose Shiner. Considering that Pugnose Shiner is known to occur at locations with high water quality and abundant submerged vegetation, it has been suggested that the specific habitat requirements of the Pugnose Shiner may make it a potentially valuable environmental indicator of habitat quality (McCusker et al. 2014a).

Spawn to hatch: Spawning is believed to take place when water temperatures reach 21˚ to 29˚C (Becker 1983), which generally occurs in early to mid-June in Ontario (DFO 2010). The timing of spawning may also be related to the development of submersed plants (Leslie and Timmins 2002). Spawning areas have been characterized as shallow (< 2 m) zones with abundant submergent and emergent vegetation, sand and silt, and, to a lesser extent, gravel substrates (Lane et al. 1996a). Submergent vegetation appears to play an important role in the spawning process (COSEWIC 2013). Pugnose Shiner is a lithophile, meaning it spawns over open substrates; it does not guard a nest or provide parental care (Leslie and Timmins 2002).

Young-of-the-year (YOY) and juvenile: YOY Pugnose Shiner have been associated with shallow (< 2 m), heavily vegetated habitats with species such as Common Stonewort (Chara vulgaris), Eurasian watermilfoil (Myriophyllum spicatum), Wild Celery (Vallisneria americana), pondweeds (Potamogeton spp.), and Naiad (Najas flexilis) (Leslie and Timmins 2002). Furthermore, YOY Pugnose Shiner have been documented to use habitats with substrates of sand and silt and, to a lesser extent, clay (Lane et al. 1996b). Overall, Pugnose Shiner habitat requirements seem to be similar across life stages (DFO 2010).

Adult: Limited information is currently available regarding the size and age of Pugnose Shiner at maturity in Ontario; however, 1 study conducted on Lake St. Clair recorded that mature males and females ranged in size 30 to 38 mm, and 41 to 56 mm, respectively (ROM, unpublished data cited in COSEWIC 2013). Adult Pugnose Shiner are typically found in slow-moving, clear waters of streams, large lakes, and embayments with low gradients and abundant rooted vegetation (Becker 1983; Carlson 1997; Page and Burr 2011). Pugnose Shiner is generally collected in shallow water (< 3 m) but is believed to move to deeper waters in cooler months (Becker 1983). Records of Pugnose Shiner have also been obtained from sheltered inshore ponds, diked wetlands, stagnant channels, and protected bays adjacent to large waterbodies (Parker et al. 1987; DFO, unpublished data), primarily over sand and silt substrates with organic detritus (Lane et al.1996c; Scott and Crossman 1998). Environments relatively low in turbidity may be important for the species’ long-term survival (Bailey 1959; Trautman 1981; Becker 1983; Gray et al. 2014, 2016).

Pugnose Shiner presence appears to be strongly associated with emergent and submergent vegetation (for example, Becker 1983; Leslie and Timmins 2002; McCusker et al. 2014b), which appears to be a more important limiting factor than substrate type (MDNR 2018). Recent analysis of habitat data from Thousand Islands National Park found a correlation between the presence of greater than 83% submergent vegetation and Pugnose Shiner occurrence (J. Van Wieren, PCA, unpublished data). Similarly, modeling of habitat suitability in Little Bear Creek confirmed a positive relationship between the abundance of Pugnose Shiner and increased vegetation cover, with > 50% cover, which occurred at depths of < 1.425 m, considered suitable habitat (Montgomery et al. 2018). Specifically, adult Pugnose Shiner have been observed in association with: submergent species such as Common Stonewort, Wild Celery, Naiad, pondweeds, and waterweeds (Elodea spp.); emergent species such as cattail (Typha spp.), bulrush (Scirpus spp.), and sedge (Carex spp.); as well as filamentous algae (that is, Spirogyra spp.) (Becker 1983; Holm and Mandrak 2002; Leslie and Timmins 2002).

Recent studies modelling the habitat characteristics associated with the presence of Pugnose Shiner in the Canadian waters of Thompson’s Bay (St. Lawrence River) (Potts et al. 2020a; 2021) and the American waters of Sodus Bay (Lake Ontario), and Chippewa and Goose bays (St. Lawrence River) (Haynes et al. 2020) have identified Common Stonewort as an important macrophyte species. Common Stonewort has also been identified as a component of Pugnose Shiner diet along with filamentous green algae, in addition to other more common prey items such as cladocerans, small leeches, and caddisfly larvae (Leslie and Timmins 2002). Wild Celeryand Richardson’s Pondweed (Potamogeton richardsonii) were the dominant macrophyte species found at locations where Pugnose Shiner were captured during recent surveys conducted in the Trent River (LeBaron and Reid 2021).

Montgomery et al. (2018) estimated that Pugnose Shiner in Little Bear Creek have a limited home range size and dispersal capability (27.48 m in length), based on body size and stream width and flow, among other variables. These findings suggest that connectivity between habitat patches is important to maintain stable and increasing populations with adequate gene flow.

Key limiting factors:

• Genetic analysis suggests a low dispersal potential (McCusker et al. 2014a), as does the small body size of Pugnose Shiner (Montgomery et al. 2018)

5 Threats

5.1 Threat assessment

An assessment and prioritization of threats to survival and recovery of the Pugnose Shiner is undertaken during the RPA process (DFO 2010). Tables 4 a, b, and c provide a summary of threats to extant Pugnose Shiner populations in Canada. Known and suspected threats were ranked with respect to threat likelihood and threat impact for each population. The threat likelihood and threat impact were then combined to produce an overall threat status. A certainty level was also assigned to the overall threat status, which reflected the lowest level of certainty associated with either threat likelihood or threat impact. Further details on Pugnose Shiner threat assessment are described in DFO (2010). Pugnose Shiner populations detected shortly after the publication of the RPA have been included in table 3, while the most recently detected locations (that is, South Bay, West Otter Creek, St. Clair, Sydenham, Detroit, and Trent rivers) have yet to be assessed.

a. The list of threats was established during the recovery potential assessment (RPA) development (DFO 2010) and did not include climate change; however, the potential impacts of climate change are discussed in the narrative text.

b. Pugnose Shiner were detected in 4 new locations after the RPA was completed. Discussions with local conservation authorities, Ontario Ministry of Natural Resources and Forestry, Provincial Park staff, National Wildlife Area staff, and Fisheries and Oceans Canada staff, using the same criteria as Bouvier et al. (2010), determined threat status for these locations.

c. Threat status revised from Bouvier et al. (2010) based on the expert opinion of J. Robinson, Environment and Climate Change Canada (pers. comm. 2010).

a. Although non-target sampling conducted by Fisheries and Oceans Canada in 2015 used boat-electrofishing, which is a suitable gear-type, it is believed that many Pugnose Shiner specimens were not adequately captured during these surveys.

5.2 Description of threats

The primary threats to Pugnose Shiner populations in Canada include habitat modifications, aquatic vegetation removal, sediment loading and turbidity, and nutrient loading. Other threats that are expected to have a lower impact include invasive species, incidental harvest via the baitfish industry and potentially anglers who use minnow traps, as well as changes in trophic dynamics. Threat descriptions are detailed in the COSEWIC and RPA documents (Bouvier et al. 2010; DFO 2010; COSEWIC 2013) and summarized below.

Aquatic vegetation removal/control: The removal of aquatic plants from the shallow littoral areas of lakes and rivers is believed to be a serious threat to the Pugnose Shiner, given that it requires aquatic plants for cover at every life stage, and as a source of food (Parker et al.1987; COSEWIC 2013). The physical act of removing aquatic vegetation is harmful to the species, as mechanical removal of vegetation reduces the availability of suitable habitat, while other methods including dredging and herbicide use also disturb sediments and create turbid conditions, and introduce potentially harmful chemicals into the water, respectively. Some fishers and resource users from Walpole Island First Nation have noted a decrease in aquatic vegetation, which they attribute to scouring as a result of wakes from ships and lower water levels (Jacobs pers. comm. 2011).

Sediment loading/turbidity: Sediment loadings may affect Pugnose Shiner through the selective transport of pollutants, while increased siltation of substrates may degrade spawning habitat. Trautman (1981) observed that Pugnose Shiner disappeared from turbid areas of western Lake Erie, where it was historically present in bays and marshes, before Blackchin and Blacknose (Notropis heterolepis) shiners, suggesting that the Pugnose Shiner is less tolerant of turbidity. Laboratory-based investigations have demonstrated the Pugnose Shiner to be less tolerant of turbidity than other cyprinid species within its range, with impacts including: altered schooling behaviour, a reduced critical swimming speed, and respiratory impairment (Gray et al. 2014, 2016). Increased levels of turbidity may also impact the species’ vision, which can affect predator avoidance and foraging success, while elevated turbidity levels impede light penetration, which may compromise macrophyte growth, resulting in a loss of preferred habitat for the Pugnose Shiner. Bailey (1959) stated that areas once inhabited by Pugnose Shiner had suffered radical changes in habitat quality, particularly an increase in turbidity and loss of aquatic vegetation, as a result of human land and water use. Increased sediment loads may occur from dredging within lakes and channels, practices that result in stream bank erosion (for example, agricultural practices, construction activities, bank brushing), and channelization, all of which result in sediment transport and the associated increase in turbidity.

A recent study (Rodriguez et al. 2021) used a joint species distribution model (JSDM) populated with data (including the number of individuals of each species captured at locations, environmental variables, species traits, phylogenetic correlations, and other variables related to sampling methods and space and time), which allowed them to better project the responses of species at risk to threats by inferring comparability between these species for which limited data is available, to other appropriate members of the fish community, for which more robust data exists. The results of this study indicate that Pugnose Shiner had strong non-linear relationships with environmental stressors including turbidity, water velocity, and dissolved oxygen (Rodriguez et al. 2021). It is possible that the relationship with dissolved oxygen is a consequence of the temperature preferences of Pugnose Shiner, although the JSDM used by Rodriguez et al. (2021) did not show a detectable response to water temperature for Pugnose Shiner.

Nutrient loading: Excess nutrient (nitrates and phosphorus) inputs into waterbodies can negatively influence Pugnose Shiner habitat through the development of algal blooms and associated reductions in dissolved oxygen concentrations that occur when these blooms die off. Nutrient loading is particularly evident in Rondeau Bay where loadings from adjacent agriculture and residential areas are negatively impacting wetland habitats. Vegetation diversity tends to decline with increased nutrient inputs as some species, such as cattail and European Common Reed (Phragmites australis australis), are superior competitors for the excess nutrients (Gilbert et al. 2007). Although wetlands are highly valued for their water filtering capacity, these systems are negatively impacted when nutrient (and chemical) concentrations far exceed normally occurring background levels (Gilbert et al.2007).

The persistent elevated concentrations of total phosphorus and apparent trend of increasing nitrate ion concentrations in some watercourses suggest that this is an ongoing concern (EERT 2008). Elevated phosphorus concentrations have been recorded at several locations within the OAC (Jean et al. 2015), North and East Sydenham River branches, and Little Bear Creek (DFO 2022).

Invasive species: Invasive fish and plant species may be having an unfavourable effect on Pugnose Shiner populations, and the potential for further invasions remains. Round Goby (Neogobius melanostomus) may negatively affect Pugnose Shiner populations by predating on its eggs and competing for resources and/or spawning habitat; although little information is currently available regarding interactions between these 2 species. Common Carp (Cyprinus carpio) may potentially harm Pugnose Shiner by uprooting essential aquatic vegetation and increasing turbidity levels (for example, Lougheed et al. 2004). Similarly, Asian carps may pose a threat to Pugnose Shiner; for example, the Grass Carp (Ctenopharyngodon idella) would likely find coastal wetlands with abundant macrophytes, such as Long Point Bay, suitable for colonization, and consequently reduce macrophyte abundance through consumption, which would lead to indirect impacts on a number of fish species as well as other taxonomic groups (Wittmann et al. 2014). Predictive modelling of the potential effects of Grass Carp on coastal habitats within the Great Lakes, at both the biotic and abiotic levels, suggests that this invasive species will likely have low to moderate impacts on coastal wetlands of Lake Erie where Pugnose Shiner occurs, such as Long Point Bay, depending on the projected density of Grass Carp (Gertzen et al. 2016). In contrast, habitats within the upper St. Lawrence River are projected to be significantly impacted at both of the density scenarios used in the modelling (Gertzen et al. 2016). Based on this modelling, Pugnose Shiner is predicted to experience significant impacts if colonization of Grass Carp occurs within coastal wetlands where it is present, due to the potential reduction of aquatic macrophytes, which are a critical component of the species spawning, nursery, and adult habitat (Gertzen et al. 2016).

Since 2013, a total of 29 Grass Carp have been captured in Canadian waters of the Great Lakes (Colm pers. comm. 2020). Grass Carp has been detected within Lake Erie (Cudmore et al. 2016) and Lake Ontario, including Muscote Bay in the Bay of Quinte (DFO 2017), which is relatively close to areas where Pugnose Shiner occurs such as Prince Edward Bay and the Trent River. In addition, spawning has been observed in 2 United States tributaries to Lake Erie (Maumee and Sandusky Rivers) (Harris et al. 2020). Furthermore, spawning Grass Carp have been confirmed within a tributary of Lake Erie in Ohio (Chapman et al. 2013; Embke et al. 2016) and a diploid specimen capable of reproduction was detected within Jordan Harbour, a Canadian tributary of Lake Ontario (DFO 2017). DFO’s Aquatic Invasive Species Program conducts annual monitoring surveys to detect and address the potential establishment and spread of this species.

Invasive plant species can also pose a potential threat to Pugnose Shiner populations by significantly altering wetland vegetation communities (EERT 2008). There are 2 species of particular concern include European Common Reed and Eurasian Watermilfoil. Eurasian Watermilfoil is a fast-growing perennial that forms dense underwater mats that may shade other aquatic plants important to the Pugnose Shiner. The extirpation of Pugnose Shiner, as well as 7 other species in a Wisconsin lake, was linked to the proliferation of Eurasian Watermilfoil (Lyons 1989) and its establishment in Rondeau Bay in the 1960s may have contributed to the apparent loss of the Pugnose Shiner from that location. Unfortunately, the removal of Eurasian Watermilfoil may be detrimental to Pugnose Shiner, as the preferred methods of removal include use of the herbicide 2,4-Dichlorophenoxyacetic acid or mechanical harvesting, which may compromise remaining native plants (EERT 2008).

In addition, a reduction in wetland plant diversity has been attributed to the proliferation of the European Common Reed (Wilcox et al. 2003), an invasive plant species that forms dense stands that have been documented to transform habitats from wetland to terrestrial (Schummer et al. 2012). European Common Reed can be found in the majority of locations where Pugnose Shiner occurs, and is considered to have had profound ecological impacts in coastal habitats such as Long Point Bay (Badzinski et al. 2008) where Pugnose Shiner is present, and Point Pelee National Park (Vis et al. 2014) where Pugnose Shiner is now considered extirpated. Dense stands of European Common Reed have been implicated in the reduction of wetted habitat within coastal wetlands and reduction of macrophyte diversity (Gilbert and Locke 2007; Rook et al. 2016), which is important habitat for Pugnose Shiner at multiple life stages and an important food resource. Research has been conducted that models potential impact scenarios stemming from the combined effects of climate change and the increased expansion of European Common Reed within Long Point Bay on Pugnose Shiner habitat. This research has not yet been published; however, the preliminary results indicate that the extinction risk of Pugnose Shiner from climate change increased significantly after invasion from European Common Reed (Drake pers. comm. 2018). At other locations, European Common Reed may further affect Pugnose Shiner by contributing to anoxic conditions in locations where there is limited water flow.

The impacts and benefits of European Common Reed removal have been investigated in Long Point Bay (Rook et al. 2016), with results indicating that it may increase the potential spawning habitat for Pugnose Shiner in certain locations; however, there is also a concern that the creation of small shallow ponds amidst large stands of European Common Reed may lead to stranding during periods of the year when low water conditions occur, stranding fish in confined areas in unsuitable conditions. It is also possible that European Common Reed may be used by Pugnose Shiner at certain life stages or as refuge from predators. Specific efforts to gain a more robust understanding of the impacts of European Common Reed on Pugnose Shiner populations are currently ongoing.

Another invasive plant species that may impact Pugnose Shiner is Starry Stonewort (Nitellopsis obtusa). Starry Stonewort, a macro-algal species in the same family (Characeae) as the native Common Stonewort (Chara vulgaris), is native to Europe and Asia and was first discovered in the St. Lawrence River in 1978 (Geis et al. 1981). Since then it has spread to a number of areas in the Great Lakes watershed, including locations where Pugnose Shiner is known to occur such as the St. Clair River, Lake St. Clair, and the Detroit River in the Huron Erie Corridor (Schloesser et al.1986), Wellers Bay, East Lake, and South Bay in Lake Ontario (Prince Edward County) (Midwood et al. 2016), and throughout the u St. Lawrence River (Karol et al. 2017). In addition, Starry Stonewort is also found in a portion of the Kawartha Lakes including Lake Simcoe and Lake Scugog (Harrow-Lyle et al. 2020), which raises the possibility that this exotic species may be found in the Trent River where Pugnose Shiner occurs.

Starry Stonewort has been observed to form large monoculture mats that extend high in the water column, which may limit the amount of light available to other native macrophyte species (Larkin et al. 2018). Furthermore, Starry Stonewort is capable of altering water chemistry, as well as the cycling of nutrients, which could limit the availability of benthic nutrients to other native species (Larkin et al. 2018; Pullman and Crawford 2010). Brainard et al. (2017) investigated the potential impacts of Starry Stonewort invasions in 4 lakes located in Central New York and found that, where it was abundant, the species richness of other macrophytes was lower and their biomass was significantly reduced. These declines in biomass were observed at water depths including shallow (<1 m), intermediate (1 to 2 m), and deep areas (>2 m) (Brainard et al. 2017). Similarly, Pullman and Crawford (2010) observed that invasions were common in depths of 0.5 to 1.5 m in Michigan lakes, where Starry Stonewort out-competed common non-native and native species such Eurasian Watermilfoil, Fanwort, and Curly Leaf Pondweed. These findings suggest that Starry Stonewort could likely impact critical habitat identified for Pugnose Shiner, which includes depths of <2 m with dense submersed vegetation (for example, wild celery, pondweeds, and naiad) for the spawning to embryo and YOY life stages, and <3 m with rooted native Common Stonewort for the adults (table 7).

Although little research has been conducted regarding the impacts of this invasive species on the fish community, Pullman and Crawford (2010) have documented that Starry Stonewort affects, and in some cases eliminates, the availability of spawning habitat for many species. These authors note that Centrarchid species, such as bass and sunfish, which are capable of nesting and spawning in beds of the similar native Common Stonewort species, do not exhibit spawning activity in areas dominated by Starry Stonewort. It is currently unclear how, or if, this invasive species would affect Pugnose Shiner spawning success. However, it is likely that submerged vegetation plays an important role in the spawning process for Pugnose Shiner (COSEWIC 2013), and the timing of spawning, in early-mid June (DFO 2010), is believed to coincide with the development of these macrophytes (Leslie and Timmins 2002). Starry Stonewort decomposes in March within Great Lakes latitudes (Kipp et al. 2020), and only begins to regrow in July, and reach peak biomass in September in the St. Clair-Detroit River system (Schloesser et al. 1986; USGS 2020); and is considered uncommon in July, with increased biomass occurring from August to October in the St. Lawrence River (Kipp et al. 2020; Geis et al.,1981). Based on these observations, it could be hypothesized that the establishment and dominance of Starry Stonewort within Pugnose Shiner critical habitat could significantly impact the availability of suitable habitat features (submerged vegetation) during the seasonal spawning period. In addition, it is hypothesized that Starry Stonewort could impact critical nursery habitat for YOY considering that the dense floating mats that this exotic species forms have led to reductions in the density of stems, due to the loss of other plant species (for example, Eurasian Watermilfoil, Pondweeds, and Water Lilies) (Pullman and Crawford 2010). Such reductions in the complexity of nursery habitat could lead to increased exposure of YOY and even small bodied adults, including imperiled species such as Pugnose Shiner, to predators, leading to higher mortality rates (Pullman and Crawford 2010). The native Common Stonewort has been identified as a component of the diet of adult Pugnose Shiner (Leslie and Timmins 2002); however, it is currently unclear if Starry Stonewort could serve as supplementary food source, or whether its dominance over Common Stonewort would deprive Pugnose Shiner of an important source of energy.

Starry Stonewort is capable of reproducing both sexually and asexually (Larkin et al. 2018), and fragments of the plant can act as disseminules, or seeds, which can be dispersed by water currents, enhancing the spread and colonization of this species (Pullman and Crawford 2010). Boat Traffic has been implicated as a likely cause for the fragmentation and spread of Starry Stonewort (Pullman and Crawford 2010; Midwood et al. 2016). Modelling research, aimed at identifying physical and chemical environmental factors that could be used to predict the occurrence of Starry Stonewort in Presqu'ile Bay, Lake Ontario, found that 2 of the best predictors were the number of docks within a 1 km radius and the distance to the nearest marina (Midwood et al. 2016). These findings demonstrate that human activity, mainly recreational boating, is likely to be an important mechanism driving the spread of this invasive species. More research is needed to elucidate what implications the spread of Starry Stonewort may have for Pugnose Shiner populations.

Water Soldier (Stratiotes aloides) is another invasive plant species that may threaten Pugnose Shiner. This perennial aquatic plant, which originates in Europe and northwest Asia, has become established in the Trent River where it was first discovered in 2008 (Snyder et al. 2016), including areas where Pugnose Shiner is known to occur. More recently, Water Soldier has been observed in the Glen Ross reach of the Trent River in close proximity to habitats occupied by Pugnose Shiner (Lebaron and Reid 2021). This species was likely introduced into Ontario waters as an ornamental garden plant and has since spread downstream in areas with water depths up to 5 m (OFAH/MNRF 2012). Water Soldier has2 forms: an emergent form that floats near the surface with stiff sharp leaves; and a submersed form usually found on the bottom substrate or floating nearby (Snyder et al. 2016). The submersed form eventually rises to the surface during the summer months leading to the emergent form, then sinks below the surface again once the leaves become waterlogged (OFAH/MNRF 2012). Water Soldier can reproduce both sexually and asexually (vegetatively) (Cook and Urmi-König 1983) but currently only female plants have been found as of 2016, which has not negatively impacted the spread and proliferation of this species in any way (Snyder et al. 2016).

Water Soldier can affect the aquatic environment where Pugnose Shiner occurs by forming dense mats of floating vegetation, which can limit light penetration and nutrients available to other macrophyte species, and alter water chemistry leading to a decrease in plant biodiversity (OFAH/MNRF 2012; Snyder et al. 2016). As discussed earlier, with regard to Starry Stonewort, Pugnose Shiner may be directly impacted by such changes in the biodiversity and composition of macrophytes if specific species are outcompeted that are important for spawning, embryo and YOY development, and food resources for adults in depths up to 3 m. In addition, research suggests that Water Soldier has the potential to impact zooplankton availability by exuding allelopathic substances (Mulderij et al. 2006), which could have food web implications that could affect Pugnose Shiner. Similar to Starry Stonewort, the proliferation of this species may be exacerbated by boat traffic (OFAH/MNRF 2012). Efforts to control the invasion of this species have been unsuccessful (Snyder et al. 2016). If this species spreads, it could impact Pugnose Shiner at a number of locations throughout the species range. In its native range in Europe, Water Soldier is known to thrive in ditches (Snyder et al. 2016), impeding flow and consequently causing sedimentation, which might suggest that this species could threaten species at risk, such as Pugnose Shiner, within smaller drains of southwest Ontario. Evidently, more research is required to explore the potential impacts Water Soldier might have on Pugnose Shiner.

Incidental harvest (baitfishing): Pugnose Shiner is not a legal baitfish in Ontario (Cudmore and Mandrak 2018) but the potential for incidental bycatch of the species in commercial baitfish operations, and potentially by anglers who use minnow traps, exists. Due to the species’ relative rarity and sparse distribution, the likelihood of it being captured incidentally is low; however, it still is considered a potential threat.

Changes in trophic dynamics: Apparent shifts in fish communities, from a cyprinid-dominated (minnows) assemblage to one dominated by centrarchids (sunfishes), has been suggested to have negative impacts on Pugnose Shiner (Holm and Boehm 1998), particularly in the OAC (ARRT 2006). These shifts could result in both an increase in the number and diversity of predators present and an increase in interspecific competition for resources (for example, Finigan et al. 2018). Evidence suggests that minnow diversity and abundance decrease with an increase in the number and diversity of littoral predators, such as basses (Micropterus spp.) and pikes (Esox spp.) (Whittier et al.1997). It has been theorized that increased competition for resources with juveniles of species, such as Black Crappie (Pomoxis nigromaculatus), Bluegill (Lepomis macrochirus), and adult Brook Silverside (Labidesthes sicculus), may have also played a role in the decline of Pugnose Shiner in Point Pelee National Park (Bouvier et al. 2010). These species have a diet similar to Pugnose Shiner, feeding heavily on cladocerans and occasionally on plant material (Holm and Mandrak 2002). However, Brook Silverside, as well as juvenile Bluegill and Black Crappie, occurred together with Pugnose Shiner in 1999 collections at Walpole Island (Holm and Mandrak 2002), so it is uncertain to what extent competition for food is a threat.

Fish community data, collected in 1982, 1997, and 2004, has also been used to assess the potential effects of centrarchids and invasive species on the abundance of Pugnose Shiner in the OAC (Drake pers. comm. 2017). Through these surveys, a shift in the fish community has been observed, including an increase in the abundance of centrarchid species, such as Black Crappie , Smallmouth Bass (Micropterus dolomieu), Largemouth Bass (M. salmoides), and Rock Bass (Ambloplites rupestris), which appears to be correlated with declines in the abundance of Pugnose Shiner, at least at downstream sites where these aforementioned species are most prolific. Similarly, research modelling the impact of environmental variables, as well as species co-occurrences on the distribution of Pugnose Shiner in Thompson’s Bay in the upper St. Lawrence River indicates that there is a negative association with Largemouth Bass, Pumpkinseed, and other juvenile species of the Lepomis family (Potts et al. 2020a; 2021).

Climate change: The capacity for climate change to alter water levels, temperature regimes, and the frequency of extreme weather events is a further threat to Pugnose Shiner. Climate change may threaten Pugnose Shiner directly through environmental changes and indirectly through its effects on species interactions. Although warming may result in the potential for range expansion of the Pugnose Shiner (Chu et al. 2005), the species may be highly vulnerable to projected changes in the coastal wetlands where it often resides (Doka et al. 2006). It is anticipated that the effects of climate change will be widespread and should be considered a contributing impact to species at risk and to habitats, and may impact species such as Pugnose Shiner through interactive effects with other threats discussed here. Recent experimental research has demonstrated that elevated water temperatures impacted the metabolic rate of Pugnose Shiner and led to responses including changes in gill shape/size (Potts et al. 2020b). These findings have not yet been studied in wild populations; however, Potts et al. (2020b) suggest that climate change may already be impacting Pugnose Shiner populations considering that 28˚C, the temperature treatment, caused significant declines in standard metabolic rate. This temperature is representative of summer rearing conditions within some of the waterbodies of Ontario where the species occurs. In addition, they found that acute hypoxia (low oxygen levels), which may occur as a result of eutrophication caused by nutrient loading, limited the thermal tolerance of Pugnose Shiner; therefore, nutrient loading may further exacerbate the impact of climate change by limiting the ability of Pugnose Shiner to acclimate to higher water temperatures. McDonnell et al. (2021) also examined the interactive effects of elevated water temperature and hypoxia on the thermal tolerance of Pugnose Shiner. Similar to the findings of Potts et al. (2020b), McDonnell et al. (2021) observed that Pugnose Shiner that were acclimated to warmer water temperatures had increased thermal maximum (CTmax^{Footnote 3}) limits. Furthermore, Pugnose Shiner acclimated to lower levels of dissolved oxygen (40% air saturation) had increased CTmax limits compared to conspecifics reared in normally oxygenated conditions, demonstrating improved thermal tolerance and potential plasticity (McDonnell et al. 2021). These findings may provide important insights that could be used to inform rearing practices to ensure the best chance of survival in waterbodies that have been impacted by climate change if repatriation programs are ever undertaken for Pugnose Shiner.

A study conducted by the Michigan Department of Natural Resources regarding the projected effects of climate change on species at risk has categorized Pugnose Shiner as highly vulnerable (Hoving et al. 2013), which is consistent with the ranking of this species in a Canadian vulnerability assessment for Great Lakes coastal wetland communities (Mortsch et al. 2006). However, considering that the impact of climate change on Pugnose Shiner is highly speculative, it was not included in the population-specific threat analysis at the time of the RPA. Current and anticipated implications of climate change on Pugnose Shiner require further assessment throughout the Canadian range of the species.

Habitat modifications: It is likely that many of these aforementioned threats have, and will continue to impact Pugnose Shiner populations interactively. In many cases, it is difficult to parse these threats out since many of them may be related to one another in some way. Habitat modifications, a term that encompasses many of the threats previously discussed, are of particular concern with respect to the Pugnose Shiner when nutrients, sediment loading, and turbidity levels increase, and a loss of vegetation results. Parker et al. (1987) suggested that the amount of available habitat for Pugnose Shiner in Canada may have been diminished in quality and quantity due to a general decline in water quality and an increase in lakeshore development. Habitat loss can result from shoreline hardening and the construction of in-water and shoreline structures (for example, piers, groynes, docks) within Pugnose Shiner habitat. Furthermore, Montgomery et al. (2020) compared the species richness of the fish community between protected wetlands in Ontario and unprotected wetlands where available habitat has been significantly reduced due to the impacts of human activities, such as the draining of wetlands and increased turbidity from land use practices, as well as through the establishment and encroachment of invasive monocultures of Common Reed and Cattail (Typha spp.). These comparisons indicate that 13 wetlands where Pugnose Shiner occur are in extinction debt^{Footnote 4}, with local extirpation likely to occur in the future. Of these 13 wetlands, 55 located in the Crown Marsh of Long Point Bay had areas below the conservative MAPV^{Footnote 5} reported by Velez-Espino et al. (2010) of 0.05 km² (Montgomery pers. comm. 2020), an area that is currently applied to larger locations such as Long Point Bay in its entirety (table 8); but it is worth noting that it likely should be applied to the level of these sub-locations, given the lack of connectivity between these marshes and the limited dispersal capability of this species.

The preferred habitat of Pugnose Shiner in many areas has been relegated to isolated patches as a result of habitat modifications across its range, limiting connectivity among fragmented populations (Leslie and Timmins 2002), consequently impacting gene flow. Furthermore, large scale habitat alterations have created physical barriers to movement and altered hydrology in areas such as the OAC, Mouth Lake, and Trent River, which in turn appear to have had a strong effect on gene flow by isolating populations therein (McCusker et al. 2014a).

Drain maintenance has been identified as a threat to the habitat of Pugnose Shiner (DFO 2016, 2017; Montgomery et al. 2017, 2018). Montgomery et al. (2018) used a modelling approach to assess potential impacts to Pugnose Shiner habitat within Little Bear Creek that would result from a proposed drain maintenance project. These authors determined that the direct loss of habitat, through the removal of submerged vegetation and dredging in depths < 1.425 m, would lead to a reduction of suitable habitat for Pugnose Shiner that is below the MAPV reported by Velez-Espino et al. (2010). Furthermore, their modelling framework indicated that the proposed drain maintenance activities would have a significant impact on connectivity between habitat patches, which could inhibit gene flow and compromise the persistence of populations. Additionally, nearshore dredging within the St. Lawrence River has been identified as a threat to the species through the loss of aquatic vegetation and increased sedimentation (McCusker et al. 2017).

6 Population and distribution objectives

In 2002, COSEWIC assessed the Pugnose Shiner as endangered, in part because of its limited distribution. At the time of the report’s publication, Pugnose Shiner was considered extant at 4 locations in Canada and extirpated from 2 (Holm and Mandrak 2002). At the time that the original recovery strategy was drafted for Pugnose Shiner, an additional 8 locations were confirmed as extant and another location had been confirmed extirpated. The species was re-assessed by COSEWIC as threatened in 2013, with a total of 16 extant locations identified at that time, as well as 3 extirpated locations. The species is now known to occur at 21 locations including large areas of Lake St. Clair and almost the entire length of the upper St. Lawrence River from Eastview to Lancaster. Pugnose Shiner may potentially still occur at another location (Canard River), and is only considered to be extirpated from 2 locations (Point Pelee National Park and Rondeau Bay).

An important factor to consider when determining population and distribution objectives is the number of populations that may be at a given location, as it is possible that a location may contain more than one discrete population. In this context, location does not refer to the locality of the discrete population, but rather a geographically or ecologically distinct area in which a single threatening event can rapidly affect all individuals of this species present (COSEWIC 2011). To recover the species to a level lower than t under COSEWIC criteria, a minimum of 11 extant locations with at least one self-sustaining population are required. Where present, multiple populations at a single location should be maintained. Currently, the number of populations present at each Pugnose Shiner location in Canada is unknown and further research is required to investigate this. A total of 15 locations have been chosen to meet this aforementioned COSEWIC criteria.

Population and distribution objectives establish, to the extent possible, the number of individuals and/or populations, and their geographic distribution, that are necessary for the recovery of the species. Based on existing knowledge, the population and distribution objectives for the Pugnose Shiner are:

Population objective: To ensure that populations or sub-populations at 15 locations (consistent with the distribution objective listed below) demonstrate signs of reproduction and recruitment, and are stable or increasing, with low risk of known threats.

Distribution objective: To ensure the survival of self-sustaining populations or sub-populations at the following locations currently occupied by the species:

• Teeswater River
• OAC, Mouth Lake
• Maxwell Creek
• Little Bear Creek
• St. Clair Unit of the St. Clair NWA
• Long Point Bay /Big Creek
• Trent River
• Wellers Bay
• West Lake
• East Lake
• Waupoos Bay
• St. Lawrence River and Gananoque River in the Thousand Islands National Park – Gananoque area
• St. Lawrence River in the Thousand Islands National Park in the Grenadier Island/Mallorytown Landing area and
• Lake St. Lawrence in the St. Lawrence River

The populations or sub-populations at these locations could be considered recovered when they demonstrate signs of reproduction and recruitment throughout their distributions. More quantifiable objectives will be developed once necessary surveys and studies have been completed (refer to section 8.2). The objectives laid out in section 8.2 would serve to further inform population modelling, specifically with regard to quantifying the MAPV. Modelling conducted by Venturelli et al. (2010) estimated the minimum viable population (MVP) for Pugnose Shiner as well as the MAPV under 2 catastrophe scenarios in both lentic and lotic waterbodies (see section 8.1.3). However, these models were built with general life history parameters from the literature and are not population specific. The implementation of such a population and habitat targets is difficult without also having information on population(s) size, trends, spatial distribution, habitat quality, frequency of catastrophic declines, and a more complete understanding of the life history of the species. For example, basic information such as length- and mass-at-age, age- and size-at-maturity, fecundity, and clutch size are unknown for Canadian populations; these parameters were inferred from nearby U.S. populations when developing existing models. Therefore, more confident objectives relating to MVP can be developed, and further validation of model results can be obtained, once the understanding of the life history and demographics for this species is improved. Research actions designed to fill such knowledge gaps are outlined in table 4.

Genomic assessments have also been conducted for certain Pugnose Shiner populations (McCusker et al. 2014), which indicate the populations found within Mouth Lake and Weller Bay may be prone to the effects of inbreeding depression. For this reason, population enhancement may be warranted in the future to maintain these populations and to lower their extinction risk and fulfill the population and distribution objectives for these locations. However, it is important to determine if population densities are indeed low at these locations and if there is currently unutilized habitat that would support translocated individuals. Furthermore, the right donor populations would need to be chosen and the potential for outbreeding depression would also have to be considered. Translocations have led to successful recruitment and population growth in Chaumont Bay, an inlet of the U.S. coast of Lake Ontario in New York, using a broodstock captured from Sodus Bay, another inlet of Lake Ontario in New York (Carlson et al. 2019).

7 Broad strategies and general approaches to meet objectives

7.1 Actions already completed or currently underway

Reporting: The original recovery strategy was posted in 2013 (DFO 2013) and the “Report on the Progress of Recovery Strategy Implementation for the Pugnose Shiner (Notropis anogenus) in Canada for the Period 2012 to 2017” was completed in 2022 (DFO 2022). The progress report summarizes the collective efforts of the competent ministers, provincial organizations, and all other parties involved in conducting activities that contribute towards the species’ recovery. For example, a cataloguing of recent surveys (both targeted and non-targeted) along with completed and ongoing research activities is contained within the progress report.

Ecosystem-based action plans: The following aquatic ecosystem-based action plans include Pugnose Shiner and are currently being implemented by their respective recovery teams. Recovery activities prescribed for implementation in these action plans include active stewardship and outreach/awareness programs to reduce identified threats. Funding for these activities is supported by Ontario’s Species at Risk Stewardship Fund and the Government of Canada’s Habitat Stewardship Program (HSP) for species at risk. Additionally, research requirements for species at risk identified in these documents are funded, in part, by the Canadian Nature Fund for Species at Risk.

• Action Plan for the Ausable River in Canada: An Ecosystem Approach: An ecosystem-based action plan for at-risk fish and mussel species in the Ausable River basin, including Pugnose Shiner, has been developed. The goal of the action plan is to prescribe measures that sustain and enhance the native aquatic communities of the Ausable River through an ecosystem approach that focuses on species at risk (ARRT 2006). The action plan includes recovery measures for Pugnose Shiner in the OAC as well as in Mouth Lake (DFO 2020).
• Multi-species Action Plan for Thousand Islands National Park of Canada: The action planapplies to lands and waters occurring within the boundaries of Thousand Islands National Park of Canada (PCA 2016). Measures pertaining to Pugnose Shiner contained within the action plan include the installation of signage related to critical habitat, and the completion of targeted surveys for Pugnose Shiner at numerous locations within park boundaries.

Conservation authorities: Conservation authorities (for example, Saugeen Valley, Long Point, Ausable-Bayfield, Cataraqui, St. Clair Region, Essex Region, and the Quinte Region) continue to play a vital role in stewardship and public education programs that have resulted in increased awareness of species at risk and improvements to habitat and water quality throughout the Pugnose Shiner range in Ontario.

Invasive species programs: The Asian Carp Program was established by DFO in 2013 and focuses on the early detection of Asian carps, including the Grass Carp among others. Sampling efforts are focused in areas where Asian carps are most likely to become established within the Great Lakes and its watersheds; many of these locations are in or near watersheds occupied by Pugnose Shiner. Furthermore, the Federal Aquatic Invasive Species (AIS) Regulations came into effect in 2015 and prohibit the possession or transfer of species that have been listed as invasive.

The MNRF has developed an Invasive Species Strategic Plan (2012) with objectives that include preventing new invasions, slowing and/or reversing the spread of existing invasive species, and reducing the harmful impacts of existing invasive species (MNRF 2012). Rules to prevent and control the spread of invasive species are set out in Ontario’s Invasive Species Act, 2015. Furthermore, PC’s program for invasive species within the Thousand Islands National Park includes monitoring the progress/establishment of invasive species to provide early opportunities to mitigate their potential threat. The MNRF has been working in conjunction with PC and the Ontario Federation of Anglers and Hunters (OFAH) to monitor and control the spread of Water Soldier in the Trent River (Reid pers. Comm. 2021). The MNRF has also partnered with federal, provincial, and municipal governments, as well as environmental non-government organizations (ENGOs), since 2016 to conduct projects centred on the control of European Common Reed and related improvement projects at locations along the North Shore of Lake Erie including Rondeau Bay Provincial Park, the Long Point Big Creek NWAs, the Crown marsh in Long Point Bay (Reid et al. 2021), and Point Pelee National Park.

St. Lawrence River Institute and Mohawk Council of Akwesasne: The St. Lawrence River Institute (SLRI) and the Mohawk Council of Akwesasne (MCA) have partnered with a variety of Canadian and U.S. researchers to monitor the fish community and aquatic habitat in the u St. Lawrence River since 2015, which includes surveys for Pugnose Shiner. At its onset, these surveys were conducted over a 150 km stretch of the St. Lawrence River extending from Brockville downstream to the eastern extent of Lake St. Francis in Quebec (Windle pers. comm. 2018); however, this program recently expanded to include areas from the Bay of Quinte and Prince Edward County in Lake Ontario downstream to Montreal, Quebec (Windle 2019; Windle pers. comm. 2021). Within this study region, MCA and SLRI have worked closely to identify and prioritize monitoring locations distributed within traditional Mohawk territories of the St. Lawrence River. These surveys have led to the detection of Pugnose Shiner at many new locations, served to monitor the abundance of the species over time, and have monitored the abundance of invasive Round Goby (Windle 2018; 2019).

Parks Canada and partners:  Thousand Islands National Park have been working with the MNRF and Muskies Canada on a long-term monitoring program at 18 sites within the Thousand Islands, which has led to the detection of Pugnose Shiner at multiple locations and served to track the abundance of this species over time. Furthermore, PC has worked with the Mohawks of Akwesasne to conduct sampling in Lake St. Francis below the Moses Saunders Generating Station (J. Van Wieren, PC, unpublished data).

Baitfish regulations: Further to the rules on baitfish harvesting supplementing Ontario’s recreational fishing regulations, a baitfish primer (Cudmore and Mandrak 2018) has been developed that identifies the baitfish species of Ontario. The purpose of the baitfish primer is to reduce the chances of misidentification of baitfish, which would prevent or limit removal of non-target species, such as Pugnose Shiner, as bycatch. The baitfish primer has been made available to commercial bait harvesters, anglers, and the general public via MNRF offices, ServiceOntario offices. Furthermore, the baitfish primer has also been made into an app that can be downloaded to smartphones, which is available at Google Play Store.

7.2 Strategic direction for recovery

A description of the broad strategies to address identified threats, and of the research and management approaches needed to meet population and distribution objectives is presented in table 5. These will help inform the development of specific recovery measures in 1 or more action plans.

There are 4 broad strategies that were identified to address threats to the species and to meet the management objectives:

1. inventory and monitoring
2. research
3. management and coordination and
4. stewardship and outreach

Approaches are identified for each of the broad strategies that are further divided into numbered recovery measures, with a priority ranking (high, medium, and low), and identification of the threats addressed (table 4). If your organization is interested in participating in one of these measures, please contact the Species at Risk Ontario and Prairies office. A narrative (section 7.3) is included to provide further explanation of specific approaches.

Implementation of the following approaches will be accomplished in coordination with relevant ecosystem-based recovery teams already in place (as described in section 7.1) and associated implementation groups. Higher priority will be given to inventory and monitoring, and research measures, since these activities will provide data that will be used to inform measures for management and coordination, and stewardship and outreach strategies.

a. “Priority” reflects the degree to which the measure contributes directly to the recovery of the species or is an essential precursor to a measure that contributes to the recovery of the species:

• "high" priority measures are considered likely to have an immediate and/or direct influence on the recovery of the species
• "medium" priority measures are important but considered to have an indirect or less immediate influence on the recovery of the species
• "low" priority measures are considered important contributions to the knowledge base about the species and mitigation of threats

b. “Timeline” refers to the time period following publication of this amended recovery strategy.

c. Approaches currently being implemented by 1 or more ecosystem-based recovery programs (see section 7.1).

7.3 Narrative to support the recovery planning table

Broad strategy 1: inventory and monitoring

Recovery measures 1 to 5 (population monitoring): The establishment of a sampling program is required to monitor changes in the distribution and abundance of Pugnose Shiner. Standardized sampling programs also aid in the detection of invasive species and in the ability to confidently define habitat associations. Investigations to outline appropriate sampling protocols for Pugnose Shiner have been undertaken (for example, Portt et al. 2008; McKenna et al. 2013; Dextrase et al. 2014). Dextrase et al. (2014) recommend electrofishing or seine netting as the optimal gear types, which have been applied for monitoring Pugnose Shiner populations in specific areas with shallower habitats. Furthermore, mamou trawls have proven to be an effective means to capture Pugnose Shiner as well as other species at risk (for example, Pugnose Minnow) in deeper areas (Reid et al. 2016; LeBaron and Reid 2021: Barnucz and Drake 2021). For example, PC has conducted standardized monitoring surveys for Pugnose Shiner in the Thousand Islands National Park from 2008 to 2018, in partnership with the MNRF and Muskies Canada, using seine nets to track changes over time at specific locations (Van Wieren pers. comm. 2020). In addition, the SLRI and MCA have conducted sampling in the u St. Lawrence River, including traditional Mohawk territories, since 2015 and have detected Pugnose Shiner at many new locations. However, there is still a need to develop a standardized protocol that can be applied throughout the species’ Canadian range. With a refined understanding of Pugnose Shiner habitat requirements, further surveys may be warranted in locations with similar habitat characteristics.

Targeted surveys need to be conducted at historical locations, including Point Pelee National Park and Rondeau Bay, to confirm that Pugnose Shiner is truly extirpated from these locations. If the species is truly extirpated from these locations, then an assessment of water quality parameters, habitat conditions, and the fish community present might be compared to occupied locations to provide insight into what drove the declines of Pugnose Shiner at these 2 locations. Further sampling is also needed throughout extant locations to provide a better understanding of population trends and distribution patterns throughout the species’ Canadian range. Currently, the assessment of populations conducted by Bouvier et al. (2010) is outdated and does not include multiple new populations, which had not been discovered at the time the RPA was undertaken. Locations that have not been sampled since 2010, or those where targeted sampling has not been conducted (for example, Mouth Lake, Waupoos Bay, Whitebread Drain/Grape Run), as well as locations where limited and/or unsuccessful non-target sampling has occurred (for example, Chenail Ecarté, interior marshes of Turkey Point) should be given priority. Similarly, targeted sampling should be conducted in the Canard River to confirm that Pugnose Shiner does indeed still occur at that location, considering that voucher specimens more recently sampled at this location were re-identified as Pugnose Minnow, a species of similar resemblance.

In addition, new locations where Pugnose Shiner has been detected need to be sampled to verify recent records. New locations, within which limited sampling has been conducted, such as the Sydenham River, West Otter Creek, south shore of Lake St. Clair, Detroit River, Maxwell Creek, Prince Edward Bay (areas between Smith and South bays), the Gananoque River, as well as areas within the St. Lawrence River near Brockville and Johnstown, should be sampled again. In addition, sampling should be conducted in Lake St. Francis in the St. Lawrence River below the Moses Saunders Dam where Pugnose Shiner has only recently been captured. This location would represent an expansion of the species’ known range that includes habitat found within Quebec waters.

There are also a number of suspected locations where Pugnose Shiner may potentially occur that should be sampled. These include locations such as Otter Creek, East Otter Creek, the North Sydenham River, the St. Clair NWA (east cell), areas with suitable habitat between Prince Edward Bay and Eastview, areas within the St. Lawrence River between the Thousand Islands and Brockville, between Brockville and Morrisburg, and throughout Lake St. Francis.

Recovery measures 6 to 8 (habitat monitoring): Many existing monitoring programs that undertake activities such as water quality monitoring (for example, Ausable River recovery strategy implementation project, the Provincial Water Quality Monitoring Network, and the Surface Water Monitoring Program), which are conducted by other partner organizations, are expected to be valuable in the recovery of the Pugnose Shiner. In addition, PC, in partnership with Muskies Canada and the MNRF, have been conducting long-term monitoring at 18 index sites within the Thousand Islands, which has included habitat monitoring (Van Wieren pers. comm. 2020). Furthermore, PC has established a long-term population and habitat monitoring program for populations within the Thousand Islands National Park. Similarly, surveys conducted by SLRI and MCA have monitored aquatic habitat conditions in the u St. Lawrence River, including traditional Mohawk territories, since 2015.

These pre-existing programs may serve to address monitoring activities prescribed within this document that are centered on measuring sediment and nutrient loads emitted from streams, and monitoring other general water quality parameters. In contrast, more specific monitoring programs are needed to identify where stormwater management structures and wastewater treatment facilities occur within the range of Pugnose Shiner, and to measure nutrient levels and other potential parameters that may impact the species, such as pharmaceutical pollutants. These studies will help to determine what impact, if any, wastewater and/or stormwater have on Pugnose Shiner.

There are also existing programs that are centered on monitoring for invasive species, including DFO’s program for Asian carps and PC program for invasive species within the Thousand Islands National Park. These programs monitor the progress/establishment of invasive species and provide early opportunities to mitigate potential threats. DFO’s Asian Carps Monitoring Program has been ongoing since 2013 and includes sampling of areas where Pugnose Shiner is known to occur (for example, Long Point Bay). Furthermore, multi-jurisdictional projects have been underway since 2016 to control the spread and establishment of European Common Reed in Rondeau Bay, Long Point Bay, and Big Creek (Reid et al. 2021), as well as Point Pelee National Park, that involve monitoring for the occurrence of this invasive plant species. In addition, the MNRF, PC, and OFAH have been monitoring the spread of Water Soldier in the Trent River (Reid pers. comm. 2021).

Broad strategy 2: research

Recovery measures 9 to 14 (threat evaluation): There are a number of threats that are currently impacting Pugnose Shiner populations as well as others that may potentially impact them in the future. For example, the establishment of invasive species may be having adverse consequences for Pugnose Shiner populations. The proliferation of European Common Reed within coastal wetlands of Lake St. Clair and Long Point Bay may impact Pugnose Shiner at multiple life-stages by reducing the availability and quality of habitat for all life stages, as well as the availability of suitable vegetation for feeding. At this point, further research is needed to elucidate what effects this invasive plant species may be having on Pugnose Shiner populations. In addition, Eurasian Water Milfoil has been implicated as a possible cause of the extirpation of Pugnose Shiner within Rondeau Bay. Although it has been observed that Pugnose Shiner is associated with this macrophyte species at multiple life stages, it is believed that high densities, occurring in monoculture stands, may adversely impact populations. Research is needed to explore these potential impacts and examine the role, potentially both positive and negative, that Eurasian Water Milfoil plays as a component of Pugnose Shiner habitat. More research is needed to examine the impact that other invasive plant species such as Starry Stonewort and Water Soldier may have on Pugnose Shiner populations, and to develop monitoring protocols to aid in their detection. In the case of Water Soldier, research has been conducted that examined the feasibility of monitoring the spread of this species using aerial drones, resulting in overall detection accuracy of 78% (Chabot et al. 2016). Similarly, research is underway that examines the potential use of eDNA to detect Water Soldier (Marinich et al. 2015), which may help to detect this invasive species at new locations early enough to control or eradicate it. Lastly, invasive fish species such as Round Goby and Common Carp may also affect Pugnose Shiner; therefore, further investigation is required to link the presence of these species to impacts on Pugnose Shiner populations.

Investigations into fish community associations may also highlight additional pressures that affect the population trajectory of Pugnose Shiner. For example, predation and/or interspecific competition with centrarchid species (for example, basses, Bluegill, Black Crappie), pikes (that is, Esox species), and other small-bodied species (for example, Brook Silverside) may have caused historical declines in Pugnose Shiner abundance at locations such as Point Pelee National Park, and may currently pose a threat in areas such as the OAC where they are expanding their range. Elucidating such interactions would likely lead to a better understanding of the interactive stressors that limit Pugnose Shiner productivity at locations where the species co-occur.

Studies that model the potential impacts of climate change on Pugnose Shiner would also greatly inform recovery planning for this species. For example, it is not clear whether increases in water temperature may lead to higher growth and range expansion for Pugnose Shiner, a species at the northern edge of its continental range; or conversely, will lead to reductions in the availability of critical habitat through the dewatering of suitable nearshore areas, or in concert with the spread of invasive species such as European Common Reed, as has been projected by modelling studies conducted by DFO (DFO 2018a).

In addition, vegetation removal is a known threat to the species, and permit applications are commonly submitted such activities in areas such as Long Point Bay. There is a need to understand the degree to which vegetation removal projects can be carried out before significant impacts to the population, which jeopardize recovery objectives, begin to occur. Furthermore, the majority of projects involving work in water along vegetated shoreline areas are conducted in the winter to avoid adverse impacts to Pugnose Shiner. It is important to investigate whether this timing window mitigation approach is effective in alleviating impacts to Pugnose Shiner by assessing whether this species is still present along shoreline areas during the winter months, and examining what impact these projects have on the regeneration of important macrophytes the following spring.

Research is still required to examine nutrient and sediment point sources within watersheds containing Pugnose Shiner, as well as their impacts on this species. For example, land use practices in the surrounding watershed of Long Point Bay, originating from upstream sections of Big Creek, contribute high turbidity levels and sedimentation and impact the suitability of areas downstream. This measure represents an opportunity for outside jurisdictions, such as conservation authorities and environmental non-government organizations, to examine threats from point sources and to inform future stewardship initiatives. It is also important to conduct experiments that can outline the threshold of tolerance for Pugnose Shiner with respect to water quality parameters (for example, dissolved oxygen, water temperature, nutrients), as well as contaminants such as heavy metals. In addition, further research should be dedicated to examining the impacts of pharmaceutical pollutants emitted from waste water treatment plants on Pugnose Shiner or a suitable surrogate of this species.

Recovery measure 15 (threat prevention): If feasible, it would be beneficial to prohibit the use of live bait within the OAC to prevent the establishment of invasive species. Currently, the use of baitfish is prohibited within the Pinery Provincial Park; however, use of baitfish is still legal within the northern portion of the OAC. Therefore, an evaluation is needed to investigate what the municipalities’ view is regarding such a prohibition, since it would likely come into effect as a municipal bylaw. In place of prohibitions, outreach materials (signs) might be used to encourage anglers not to use baitfish. Similar efforts could also focus on generating awareness of invasive plant species, prohibiting the disposal of aquarium plants.

Broad strategy 3: management and coordination

Recovery measures 16 to 18 (interagency cooperation): A coordinated, cohesive approach among relevant groups (for example, the Ontario Freshwater Fish Recovery Team, First Nations and ecosystem-based recovery teams, PC, the St. Lawrence Institute) that maximizes opportunities to share resources and information, and to combine efficiencies is recommended. Ongoing cooperative practices include the assessment of stressors to Pugnose Shiner critical habitat and the implementation of habitat improvement and restoration activities within tributaries of Lake St. Clair and the Detroit River with relevant partners (for example, Essex Region Conservation Authority). Furthermore, experts and representatives should be engaged from other jurisdictions, including the Ministry of the Environment, Conservation, and Parks (MECP), the MNRF, and Environment and Climate Change Canada (ECCC), to aid in undertaking research and monitoring measures that pertain to water quality parameters, wastewater treatment, and stormwater facilities, as well as the impacts of nutrients, heavy metals, pharmaceutical pollutants, and other contaminants on Pugnose Shiner. Additionally, cooperation and coordination is needed with U.S. agencies such as the U.S. Fish and Wildlife Service in New York State and researchers conducting projects through the Fish Enhancement, Mitigation, and Research Fund, to engage in monitoring and research activities focused on Pugnose Shiner in the St. Lawrence River.

The 2 major threats affecting Pugnose Shiner are habitat modifications and poor water quality (that is, sediment loading/turbidity, and nutrient loading), which can seriously impact its recovery potential. Communicating and coordinating with municipal planning boards and First Nations will increase their awareness of important Pugnose Shiner habitats and the likelihood that further negative impacts on preferred habitat are avoided. To date, the municipality of Chatham-Kent and the City of London have incorporated DFO species at risk guidance into their planning processes.

Recovery measure 19 (threat mitigation): Stewardship-related activities should be conducted as a collaborative effort among organizations and jurisdictions to address stressors to Pugnose Shiner populations at the watershed scale. Many of the threats facing Pugnose Shiner are related to habitat loss and degradation, which affect many aquatic and wetland-dependent species. Ecosystem-based recovery strategies, such as those for the Ausable River and the Essex-Erie region, have incorporated the requirements of Pugnose Shiner in their basin-wide strategies. As well as species-specific considerations, these ecosystem-based recovery strategies employ basin-wide strategies to improve environmental conditions such as water quality, benefiting Pugnose Shiner and other species. Wetland restoration projects may also be a suitable avenue towards restoring and enhancing Pugnose Shiner populations at certain locations. For example, the Crown Marsh project has been ongoing in Long Point Bay to restore ponds and hemi-marsh habitat within areas where dense stands of European Common Reed have reduced wetted area and macrophyte diversity (Rook et al. 2016). This project includes the control and removal of European Common Reed. Currently, research regarding the efficacy of these restoration projects is ongoing, and it remains to be determined what sort of lasting impact can be expected. Wetland restoration projects have been identified by Montgomery et al. (2020) as the best means of offsetting extinction debt in a number of wetlands in Ontario, including 13 where Pugnose Shiner occurs. Specifically, such projects could ensure that the habitat available within5 areas of the Crown Marsh, where there is less than 0.05 km² of suitable habitat, are above this conservative MAPV calculated by Velez-Espino et al. (2010).

Stewardship and habitat improvement actions (table 4) should be directed geographically to address the most serious threats identified in waterbodies inhabited by Pugnose Shiner (refer to table 3 for threat information).

Broad strategy 4: stewardship, outreach and awareness

Recovery measure 20 (habitat improvement/threat reduction activities): Large-scale efforts to improve habitat quality are required in watersheds inhabited by Pugnose Shiner. This represents an opportunity to engage landowners, local communities, First Nations, and stewardship councils on the issues of Pugnose Shiner recovery, environmental and ecosystem health, clean water protection, nutrient management, Best Management Practices (BMPs), stewardship projects, and related financial incentives. To this end, the ecosystem recovery teams for the Ausable River and Essex-Erie region have already established ongoing stewardship programs and activities (implemented by multiple agencies) that will benefit Pugnose Shiner. The implementation of BMPs will be largely facilitated through established stewardship programs. Additional stewardship activities will be coordinated with existing agencies in areas outside the boundaries of ecosystem-based programs. To be effective, BMPs should be targeted to address the primary threats affecting critical habitat. BMPs implemented will include those relating to: the establishment of riparian buffers, soil conservation, septic improvements to prevent nutrient run-off, herd management, nutrient and manure management, and tile drainage. Environmental Farm Plans prioritize BMP implementation at the level of individual farms and are often a prerequisite for funding programs. For more information on BMPs see Ministry of Agriculture and Food, Best Management Practices Series. Stewardship agencies can work with Drainage Engineers to improve upon and incorporate features beneficial to Pugnose Shiner while providing for drainage activities through an Engineer’s Report, which will allow these features to be protected under the Drainage Act. The Stewardship Guide for the Lake Huron Coastline provides similar materials for cottagers and rural, non-farm landowners, which outline suitable BMPs in the Lake Huron area.

Recovery measure 21 (awareness: incidental harvest): Promoting awareness of Pugnose Shiner and its current status among bait fishers, and enhancing their ability to identify the species, may increase the likelihood that specimens are released in the event that they are incidentally captured, and lead to the avoidance of locations where Pugnose Shiner seem to be present in high densities. Furthermore, an improved proficiency to identify Pugnose Shiner within the bait fisher community may lead to detections of this species at locations where this species was previously not known to occur. This awareness would include an information packagefor relevant bait harvesters outlining key identification features, reminding them that Pugnose Shiners need to be immediately released and that they are encouraged to report new sightings to their local MNRF district office and DFO.

Recovery measure 22 (awareness: invasive species/baitfish introductions): Promoting public awareness of the impacts of invasive species on the natural ecosystem and encouraging the use of existing invasive species reporting systems through work with MNRF, MECP and partner organizations will be carried out to continue educating anglers and remind them that it is illegal to empty the contents of their bait buckets within 30 m of a waterbody. This will reduce the transport and release of invasive species (including baitfish) and prevent their establishment in areas inhabited by Pugnose Shiner that do not already have them.

Recovery measure 23 (awareness of stewardship opportunities and mitigation approaches): Developing awareness materials and programs that encourage landowners, First Nations, and the general public to support and participate in local stewardship programs and implementing activities to restore and protect habitat will be needed to achieve this recovery measure. Awareness activities may include conducting outreach sessions and providing information packages to inform the general public and First Nations of BMPs that can be employed to reduce threats to critical habitat.

Recovery measure 24 (awareness: funding programs): Outreach programs will be advertised to inform audiences that there may be funding sources available for landowner, First Nations and local community groups engaged in stewardship activities that benefit species at risk. For example, the Habitat Stewardship Program for Species at Risk provides funding to environmental government organizations such as conservation authorities, which often involve the implementation of habitat improvement and restoration projects, easements, and farm management plans on private lands for the benefit of species at risk. Similarly, funding is available for First Nation groups through the Aboriginal Fund for Species at Risk for projects that support recovery implementation for species at risk.

8 Critical habitat

8.1 Identification of Pugnose Shiner critical habitat

8.1.1 General description Pugnose Shiner critical habitat

Critical habitat is defined in SARA 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.” [subsection 2(1)]

Also, SARA defines habitat for aquatic species as “… spawning grounds and nursery, rearing, food supply, migration and any other areas on which aquatic species depend directly or indirectly in order to carry out their life processes, or areas where aquatic species formerly occurred and have the potential to be reintroduced.” [subsection 2(1)]

For Pugnose Shiner, critical habitat is identified to the extent possible, using the best available information, and provides the functions and features necessary to support the species’ life‑cycle processes and to achieve the species’ population and distribution objectives.

It is unknown if the critical habitat identified in this amended recovery strategy is sufficient to achieve the species’ population and distribution objectives. The Schedule of studies (section 8.2) outlines the research required to acquire more detailed information about the critical habitat needed to achieve the species’ population and distribution objectives.

8.1.2 Information and methods used to identify critical habitat

Using the best available information, critical habitat has been identified using a “bounding box” approach for the following areas where the species occurs: the Teeswater River, OAC, Mouth Lake, St. Clair NWA, Maxwell Creek, Little Bear Creek, Long Point Bay (including Long Point Bay NWA)/Big Creek (including Big Creek NWA), Wellers Bay (including Wellers Bay NWA), West Lake, East Lake, Waupoos Bay, the Trent River, and the St. Lawrence River/Thousand Islands National Park. Additional areas of potential critical habitat within the Lake St. Clair/Walpole Island area will be considered in collaboration with Walpole Island First Nation.

Using this approach, the ”bounding box” outlines areas within which the species is known to occur (that is, areas where multiple adults and/or YOY have been captured). It is further refined through the use of essential functions, features, and attributes for each life stage of the Pugnose Shiner to identify patches of critical habitat within the ”bounding box”. Life stage habitat information was summarized in chart form using available data and studies referenced in section 4.3. The ”bounding box” approach was the most appropriate, given the limited information available for the species and the lack of detailed habitat mapping for these areas. Where habitat information was available (for example, bathymetry data), it was used to inform the identification of critical habitat.

For all river locations, critical habitat was identified based on a ”bounding box” approach and further refined with an ecological classification system, the Aquatic Landscape Inventory System (ALIS, version 1) (Stanfield and Kuyvenhoven 2005). ALIS was developed by the MNRF to define stream segments based on a number of unique characteristics found only within those valley segments. Each valley segment is defined by a collection of landscape variables that are believed to have a controlling effect on the biotic and physical processes within the catchments. Therefore, if a population has been found in1 part of the ecological classification, there is no reason to believe that it would not be found in other spatially contiguous areas of the same valley segment. Critical habitat for Pugnose Shiner was therefore identified as the reach of rivers that includes all contiguous ALIS segments from the uppermost stream segment with the species present to the lowermost stream segment with the species present. Different approaches, as described below, were used to identify critical habitat in the Teeswater River and the OAC. For lake locations, critical habitat is currently identified, based on a “bounding box” approach, and in some cases (that is, Long Point Bay, Waupoos Bay) was refined using National Oceanic and Atmospheric Administration (NOAA) bathymetry data, as is described below. The identification of critical habitat in the St. Lawrence River/Thousand Islands National Park used a different approach to establishing bounding boxes, which is also described below.

Teeswater River: Pugnose Shiner has been detected in the Teeswater River in the Cargill Mill Pond. A total of 2 specimens were also captured downstream of the reservoir; however, these records were not used to identify critical habitat, as it is likely that these specimens originated in the reservoir and were washed over the dam. Furthermore, the habitat downstream of the dam did not appear suitable. For this reason critical habitat was confined to the Cargill Mill Pond.

OAC: Sampling data in the OAC were taken from the DFO database for the period of 1982–2010; subsequent detections occurred in 2012 and 2015. These populations have been sampled extensively, relative to some other Canadian Pugnose Shiner populations. Additionally, a detailed spatial analysis linking species occurrence to habitat conditions within a portion of the OAC has been completed by the Ausable River Recovery Team (ARRT) and is the basis of determining critical habitat within the OAC.

Long Point Bay and Big Creek (Haldimand-Norfolk County): The 1 m^{Footnote 6} contour was used to delineate the area within which critical habitat is found, as the vast majority of records were contained within this shallow region (only 1 record, from 1947, falls outside of the 1 m contour). The area within which critical habitat is found extends up to the high-water mark elevation for Lake Erie at 174.62 m above sea level (International Great Lakes Datum 1985). The high-water mark may extend to areas that are dry due to low water levels and may extend higher where coastal wetlands exist and habitat function is connected to Lake Erie.

Waupoos Bay: The 2 m contour was used to delineate the area within which critical habitat is found, as all records were contained within this contour.

St. Lawrence River: The first record of Pugnose Shiner in the St. Lawrence River is from 1935 at a dock at Gananoque and the most recent record is from 2018. There is an additional record for the species in the Gananoque River proper (a tributary of the St. Lawrence River) in 1935 and more recently in 2013. The 1935 record occurred at a location just over 1 km upstream from the confluence with the St. Lawrence River. However, a dam located just north of Highway 2 separates this record from 2 specimens captured in 2013 downstream, as well as the records in the St. Lawrence River. For this reason, critical habitat was only identified in the Gananoque River up to the dam above Highway 2. The historical populations found upstream of the dam were considered separately from the St. Lawrence River population. Given that no Pugnose Shiner have been detected upstream of the dam since 1935, no further critical habitat was identified in the Gananoque River. Critical habitat throughout the St. Lawrence River was identified based on a specific “bounding box” approach and refined using species detection records, sampling effort, bathymetry, and high-water mark data. A population range envelope is a projected rectangle around occurrence points, based on the minimum and maximum latitude and longitude values. This rectangle is then buffered by a value of 10% to the minimum and maximum latitude and longitude values of all occurrence points. Within the projected rectangle, the area within which critical habitat is found was further refined using bathymetry data generated by DFO, to exclude areas deeper than 2 m. Due to the scale and size of the upper St. Lawrence River,4 separate bounding boxes were identified in areas that are ≤2 m in depth, where higher numbers of Pugnose Shiner have been consistently detected, and in some cases these boxes include areas between records where sampling has been insufficient, precluding them from being determined as unoccupied (for example, sections of the Lake St. Lawrence bounding box).

8.1.3 Population viability

Comparisons of the area of critical habitat identified for each population were made with estimates of the spatial requirements for a minimum sustainable population size. The MAPV for Pugnose Shiner was estimated for Canadian populations for both riverine (river) and lacustrine (lake) populations. The MAPV is defined as the amount of exclusive and suitable habitat required for a demographically sustainable recovery target based on the concept of a minimum viable population (MVP) size (Vélez-Espino et al. 2008). The estimated MVP for adult and YOY Pugnose Shiner is: 1,929 and 165,810, respectively, based on modelling scenario with a 5% probability of catastrophic (50%) decline; and 14,325 and 1,231,327, respectively, based on a 10% probability of catastrophic decline (Venturelli et al. 2010). The MAPV for the Pugnose Shiner has been estimated to be 1.52 ha and 5.04 ha in rivers and lakes, respectively, using the more conservative MVP estimate of 14,325 adults (Venturelli et al. 2010). MAPV values are somewhat conservative in that they represent the sum of habitat needs calculated for all life-history stages of the Pugnose Shiner; these numbers do not take into account the potential for overlap in the habitat of the various life-history stages and may overestimate the area required to support an MVP. However, since many of these populations occur in areas of degraded habitat (MAPV assumes habitat quality is optimal), areas larger than the MAPV may be required to support an MVP. In addition, for many populations, it is likely that only a portion of the habitat within that identified as the critical habitat would meet the functional requirements of the species’ various life stages. For more information on the MVP and MAPV and associated methodology, please refer to Venturelli et al. (2010).

8.1.4 Identification of critical habitat

Geographic information: Using the best available information, critical habitat has been identified for Pugnose Shiner populations in the following waterbodies:

• Teeswater River
• Old Ausable Channel (OAC)
• Mouth Lake
• St. Clair Unit of the St. Clair National Wildlife Area (NWA)
• Little Bear Creek (Lake St. Clair tributary)
• Maxwell Creek
• Long Point Bay (including Long Point Bay NWA)/Big Creek (including Big Creek NWA)
• Wellers Bay (including all occasionally exposed lands of Wellers Bay NWA lying between the high-water mark and the water’s edge of Wellers Bay, which forms the boundary of Wellers Bay NWA and which varies with water level fluctuations of Lake Ontario)
• West Lake
• East Lake
• Waupoos Bay
• Trent River
• St. Lawrence River and Gananoque River: Thousand Islands National Park (Gananoque area)
• St. Lawrence River: Thousand Islands National Park (Grenadier Island/Mallorytown Landing area)
• St. Lawrence River: Lake St. Lawrence

In the future, with new information, additional areas could be identified and/or additional information may be obtained to allow further clarification about the functional descriptions. Areas of critical habitat identified at some locations may overlap with critical habitat identified for other co-occurring species at risk; however, the specific habitat requirements within these areas may vary by species.

The areas delineated on the following maps (figures 4 to 13) represent the area within which critical habitat is found for the aforementioned waterbodies. Using the ”bounding box” approach, critical habitat is not comprised of all areas within the identified boundaries, but only those areas where the specified biophysical features/attributes are present that are capable of supporting 1 or more habitat functions (refer to table 6). Note that existing permanent anthropogenic structures that may be present within the delineated areas (for example, marinas, navigation channels) are specifically excluded (unless said structures are maintaining critical habitat); it is understood that maintenance or replacement of these features may be required at times^{Footnote 7}. Brief explanations for the areas identified as critical habitat are provided below.

Teeswater River: The area within which critical habitat is found (the critical habitat area) in the Teeswater River has been identified as the area from the dam in Cargill Mill Pond extending up to the end of the first ALIS segment, upstream of the reservoir (figure 4). This extent includes all contiguous waters and wetlands within Cargill Mill Pond and the first upstream ALIS segment. This represents a stretch of the river approximately 1.4 km long and an approximate area of 0.014 km². The critical habitat geospatial limit includes the active channel or bankfull channel width.

OAC: The critical habitat area in the OAC has been identified as the area from the mouth of the channel at the Ausable River, upstream to its end near Grand Bend (figure 5). The majority of this area lies within the boundaries of the Pinery Provincial Park. This represents approximately 13 km of river, which covers an area of 0.61 km². The critical habitat geospatial limit includes the active channel or bankfull channel width.

Mouth Lake: The critical habitat area in Mouth Lake has been identified as the entire lake (figure 6). This represents an area of approximately 0.05 km². The critical habitat geospatial limit includes the contiguous waters and wetlands, extending up to the high-water mark.

St. Clair Unit of the St. Clair NWA: The critical habitat area has been identified as the contiguous waters and wetlands (excluding permanently dry areas), up to the high-water mark, of the entire western diked marsh in the St. Clair Unit of the St. Clair NWA (figure 7). This represents an area of approximately 1.24 km². The critical habitat geospatial limit includes the contiguous waters and wetlands, extending up to the high-water mark.

Maxwell Creek: The critical habitat area has been identified beginning at the mouth of Little Bear Creek at Chenail Ecarté, to a point approximately 7 km upstream, where the creek intersects with Fraser Road. This represents a stretch of river approximately which covers an area of 0.42 km².

Little Bear Creek: The critical habitat area has been identified to occur from the mouth of Little Bear Creek at the Chenail Ecarté, to a point approximately 2.4 km upstream of Centre Sideroad, northwest of Appledore (figure 8). This area includes all contiguous ALIS segments from the uppermost to the lowermost stream segments where the species is present. This represents a stretch of river approximately 22 km, which covers and area of0.42 km². The critical habitat geospatial limit includes the active channel/bankfull, which is often the 1:2 year flood flow return level. Note that Little Bear Creek is designated as a municipal drain under the Ontario provincial Drainage Act.

Long Point Bay/Big Creek: The critical habitat area has been identified as the contiguous waters and wetlands of Big Creek and Long Point Bay. In Long Point Bay, this area extends from the high-water mark down to the 1 m contour (figure 9a). In Big Creek, the area includes all contiguous waters and wetlands from the causeway west to, and including, the Big Creek Unit of Big Creek NWA, except habitat contained within the interior diked cell of the NWA (figure 9b). This area also includes all contiguous wetlands to the north of Big Creek and the first 2 contiguous ALIS segments of Big Creek proper, extending to Concession A Road. The area extends up to the high-water mark elevation for Lake Erie at 174.62 m above sea level (International Great Lakes Datum 1985). The high-water mark may extend to areas that are dry due to low water levels and may extend higher where coastal wetlands exist and habitat function is connected to Lake Erie. A total of 97.84 km² has been identified in Long Point Bay/Big Creek with 92.84 km², 5.28 km², and 0.44 km² identified in Long Point Bay, Big Creek NWA, and Big Creek, respectively.

Trent River: The critical habitat area has been identified beginning upstream of Trent Severn Waterway Lock 3 and the dam at the Glen Miller Generating Station upstream to Trent Severn Waterway Lock 7 and the Glenn Ross Dam (figure 10). This area includes all contiguous ALIS segments from the uppermost to the lowermost stream segments where the species is present This represents a stretch of river approximately 17 km. The critical habitat geospatial limit includes the active channel/bankfull.

Wellers Bay: The critical habitat area has been identified as all contiguous waters and wetlands of Wellers Bay up to the high-water mark elevation for Lake Ontario at 75.32 m above sea level (International Great Lakes Datum 1985). This includes all occasionally exposed lands of Wellers Bay NWA lying between the high-water mark (75.32 m above sea level) and the water’s edge of Wellers Bay, which forms the boundary of Wellers Bay NWA, and which varies with water level fluctuations in Lake Ontario. The existing maintained, dredged channel at the northwest end of Wellers Bay, which provides the only water access for Wellers Bay, is not included in this description (figure 11). The high-water mark may extend to areas that are dry due to low water levels and may extend higher where coastal wetlands exist and habitat function is connected to Lake Ontario. This area is approximately 19 km².

West Lake and East Lake: The critical habitat area has been identified as all contiguous waters and wetlands of West Lake and East Lake (figure 12), up to the high-water mark elevation for Lake Ontario at 75.32 m above sea level (International Great Lakes Datum 1985). The high-water mark may extend to areas that are dry due to low water levels and may extend higher where coastal wetlands exist and habitat function is connected to Lake Ontario. The area includes the creek that flows into West Lake, upstream to the junction with Wesley Acres Road and the creek that flows into West Lake, upstream to the junction with Highway 12. This area represents an area of approximately 19 km² in West Lake. The area for East Lake also includes the creek that flows into East Lake from downstream of Highway 10. This area is approximately 31 km².

Waupoos Bay: The critical habitat area has been identified as all contiguous waters and wetlands of Waupoos Bay (figure 13), up to the high-water mark elevation for Lake Ontario at 75.32 m above sea level (International Great Lakes Datum 1985) and down to the 2 m contour. The high-water mark may extend to areas that are dry due to low water levels and may extend higher where coastal wetlands exist and habitat function is connected to Lake Ontario. This area is approximately 1.6 km².

St. Lawrence River and Gananoque River: Thousand Islands National Park (Gananoque area): The 2 bounding boxes were used to identify critical habitat in this specific area of the river. The first bounding box, which is centred around Bostwick Island, contains a number of islands known as the Admiral Islands, including but not limited to: Mermaid, Anchorage, Botswick, Black Duck, Hemlock, Hale, Bluff, Minota, Manitouana, Beaurivage, Lindsay, Sagistawika, McDonald, Rockland, Idlewyld, Stonethrow, Towers, Pitchpine, Burnt, Mudlunta, Lemon, Ynyscrag, Eaglescrag, Moneysunk, Polaris, Forsyth, Sampson, Big White Calf, Pike, and sisters islands, as well as Island 6. The area within which critical habitat is found includes all contiguous waters and wetlands, down to the 2 m contour and up to the high-water mark elevation for Lake Ontario at 75.32 m above sea level (International Great Lakes Datum 1985). The high-water mark may extend to areas that are dry due to low water levels and may extend higher where coastal wetlands exist and habitat function is connected to Lake Ontario. In addition, this bounding box also includes critical habitat in the Gananoque River extending from the shoreline of the St. Lawrence River, where the 2 rivers converge upstream to the first barrier, which is a dam approximately 150 m upstream of Highway 2. A total of 1.42 km² was identified as critical habitat in the first bounding box.

The second bounding box, which is centred around Stave Island, contains further islands known as the Fleet Islands, including but not limited to: Endymion, Sundown, Astounder, Axeman, Sugar, Prince Regent, Princess Charlotte, Stave, Hickey, and Curtis islands. The area within which critical habitat is found includes all contiguous waters and wetlands, down to the 2 m contour and up to the high-water mark elevation for Lake Ontario at 75.32 m above sea level (International Great Lakes Datum 1985). The high-water mark may extend to areas that are dry due to low water levels and may extend higher where coastal wetlands exist and habitat function is connected to Lake Ontario. A total of 0.53 km² was identified as critical habitat in the second bounding box. In total, 1.94 km² of critical habitat has been identified within the Gananoque area (both bounding boxes combined) (figure 14a).

St. Lawrence River: Thousand Islands National Park (Grenadier Island/Mallorytown Landing area): The bounding box used to identify critical habitat contains the shoreline of the mainland from the Rockport area to a point just downstream of Mallorytown Landing, including Thompson Bay where Pugnose Shiner is known to occur in relatively high abundance. In addition, the bounding box includes Tar and Grenadier islands, as well as a number of smaller islands, including but not limited to: Doctor, Little Grenadier, Baby Tar, Buck, Duck, Van Buren, O’Neal, Goose, Berry, Grassy Point, Indian, Chichester, Jeroy, Poole, Broadbill, Twin, Bobs, Corn, Little Corn, Grape, Marsh, Peel, Robert, Bagot, Rough, Adelaide, St. Helena, Dromedary, Cook, Harrowsmith, Long Schooner, Pilot, Willoughby, Poverty, Round, Slim, Bloomfield, Hooper, and Shanty islands. The area within which critical habitat is found includes all contiguous waters and wetlands, down to the 2 m contour and up to the high-water mark elevation for Lake Ontario at 75.32 m above sea level (International Great Lakes Datum 1985). The high-water mark may extend to areas that are dry due to low water levels and may extend higher where coastal wetlands exist and habitat function is connected to Lake Ontario (figure 14b).

St. Lawrence River – Lake St. Lawrence: The critical habitat area includes all contiguous waters and wetlands, down to the 2 m contour and up to the high-water mark elevation for Lake Ontario at 75.32 m above sea level (International Great Lakes Datum 1985). The high-water mark may extend to areas that are dry due to low water levels and may extend higher where coastal wetlands exist and habitat function is connected to Lake Ontario. The area within which critical habitat is found extends downstream from a point near Morrisburg on the downstream bank of Hoasic Creek, at its confluence with the St. Lawrence River, adjacent to Broder Island, and extends downstream to the Moses-Saunders Power Dam (figure 14c).

Table 6 provides the geographic coordinates that situate the boundaries within which critical habitat is found for the Pugnose Shiner; these points are indicated on figures 4 to 14c. Riverine habitats are delineated to the midpoint of channel of the uppermost stream segment(s) and lowermost stream segment.

Biophysical functions, features and attributes

Table 7 summarizes the best available knowledge of the functions, features, and attributes for each life stage of the Pugnose Shiner (refer to section 4.3). Note that not all attributes in table 7 must be present in order for a feature to be identified as critical habitat. If the features as described in table 7 are present and capable of supporting the associated functions, they are considered critical habitat for the species, even though some of the associated attributes might be outside of the range indicated in table 7.

a. Function: a life-cycle process of the listed species taking place in critical habitat (for example, spawning, nursery, rearing, feeding, and migration).

b. Feature: features describe the essential structural component that provides the requisite function(s) to meet the species’ needs. Features may change over time and are usually comprised of more than 1 part, or attribute. A change or disruption to the feature, or any of its attributes, may affect the function and its ability to meet the biological needs of the species.

c. Attribute: attributes are measurable properties or characteristics of a feature. Attributes describe how the identified features support the identified functions necessary for the species’ life processes.

d. This includes seasonally wetted habitats.

e. Note that < 3 m depth applies to each location unless otherwise specified. At Long Point Bay, the 1 m contour is used to delineate critical habitat and at Waupoos Bay and the St. Lawrence River, the 2 m contour is used. This is due to differences in where Pugnose Shiner, as well as other attributes of critical habitat, occur at these locations.

Summary of critical habitat relative to population and distribution objectives

The locations defined in table 6 represent the critical habitat, based on current best available information, that the Minister of Fisheries and Oceans considers necessary to partially achieve the species’ population and distribution objectives required for the survival/recovery of the species. Additional critical habitat may be identified in future updates to the recovery strategy. The area within which critical habitat is found for each population was compared to the estimated MAPV for Pugnose Shiner in Canada (table 8). It should be noted that for some populations, it is likely that only a portion of the habitat within locations identified as critical habitat would meet the functional habitat requirements of the species’ various life stages. In addition, since these populations occur in areas of degraded habitat (MAPV assumes habitat quality is optimal), areas larger than the MAPV may be required to support a MVP.

a. The MAPV estimate is based on modelling approaches described in section 8.1.2.

b. Note that some locations may contain more than 1 population (for example, some of the larger areas, such as Long Point Bay). In such cases, the MAPV would be applied to each individual population.

8.2 Schedule of studies to identify critical habitat

Further research is required to refine the boundaries of the currently identified critical habitat in order to: refine the understanding of the functions, features, and attributes of the currently identified critical habitat necessary to support the species’ population and distribution objectives; protect the critical habitat from destruction; and identify additional areas of critical habitat. The activities listed in table 9 are not exhaustive, and it is likely that additional research will lead to the discovery of further knowledge gaps that need to be addressed.

a. Timeline reflects the amount of time required for the study to be completed from the time this amended recovery strategy is published as final on the Species at Risk Public Registry. Timelines are subject to change in response to demands on resources and/or personnel, and as new priorities arise.

Activities identified in this schedule of studies will be carried out through collaboration among DFO, relevant ecosystem recovery teams, and other groups and land managers. Note that many of the individual recovery approaches will address some of the information requirements listed above.

8.3 Examples of activities likely to result in the destruction of critical habitat

Under SARA, critical habitat must be legally protected from destruction within 180 days of being identified in a recovery strategy or action plan and included in the Species at Risk Public Registry. However, for those areas of critical habitat located within the St. Clair NWA, Big Creek NWA, Long Point NWA, Wellers Bay NWA, and the Thousand Islands National Park, a description of critical habitat was published in the Canada Gazette 90 days after the posting of the original recovery strategy in January of 2013, pursuant to subsection 58(2). The subsection 58(1) prohibition against destruction of critical habitat took effect 90 days following this publication of the critical habitat description in the Canada Gazette. An additional Critical Habitat Order for Pugnose Shiner was made in 2019 for areas identified in the original recovery strategy that are outside of National Parks and National Wildlife Areas, pursuant to subsections 58(4) and (5). This amended recovery strategy identifies further critical habitat in Maxwell Creek and the Trent River, as well as additional and reconfigured critical habitat in the St. Lawrence River for which the Critical Habitat Order applies . Although the configuration of critical habitat has changed in the Thousand Islands area of the St. Lawrence River, critical habitat is still identified in the Thousand Islands National Park; therefore, the existing critical habitat description in the Canada Gazette, pursuant to subsection 58(2) would still apply and will not require amendments. Therefore, the subsection 58(1) prohibition now applies for all areas identified as critical habitat within this recovery strategy.

The following examples of activities likely to result in the destruction^{Footnote 8} of critical habitat (table 9) are based on known human activities that are likely to occur in and around critical habitat and would result in the destruction of critical habitat if unmitigated. The list of activities is neither exhaustive nor exclusive and has been guided by the threats described in section 5 (Threats). The absence of a specific human activity from this table does not preclude or restrict the Department’s ability to regulate that activity under SARA. Furthermore, activities identified in the table are not automatically prohibited, nor does it suggest that an identified activity will inevitably result in destruction of critical habitat. Every proposed activity must be assessed on a case-by-case basis and site-specific mitigation will be applied where it is available and reliable. Where information is available, thresholds and limits have been developed for critical habitat attributes to better inform management and regulatory decision-making. However, in many cases, knowledge of a species and the thresholds of tolerance of its critical habitat to disturbance from human activities are lacking and must be acquired.

Barriers, such as dikes and dams at 3 locations (OAC, St. Clair Unit of the St. Clair NWA and Big Creek NWA), maintain habitat conditions for Pugnose Shiner populations. As such, the loss of these structures may result in the destruction of critical habitat.

Certain habitat management activities are recognized as being beneficial to the long-term survival and/or recovery of the species and may be permitted under section 73 of SARA when required, as long as DFO is satisfied that the conditions of section 73 can be met. Such activities may include, but are not limited to, the removal/control of invasive aquatic/semi-aquatic vegetation, water level management (including dike maintenance) and habitat restoration activities (for example, fire management). For example, in NWAs, water levels may be managed and some aquatic vegetation may be removed, to maintain hemi-marsh conditions (that is, 50/50 emergent/open water habitat). The Interior cells of Big Creek NWA, and the entirety of St. Clair NWA, have been diked and have had ongoing water level/aquatic vegetation management for the past 25 to 60 years (Robinson pers. comm. 2008). In some instances, intentional drawdowns have been undertaken, while in other cases, water-level fluctuations resulting from weather events and infrastructure problems have also occurred at these locations. Short-term water level draw-downs result in improved habitat conditions for waterfowl and, despite the obvious loss of habitat in the short term, also appear to improve habitat conditions for Pugnose Shiner in the long term. However, the impacts to the population and its long-term viability are unknown and require further investigation. Future research will inform such water management approaches to minimize short-term impacts to existing Pugnose Shiner populations. Many other restoration activities that improve the quality and/or quantity of available wetland habitat for the Pugnose Shiner may be necessary.

Note that in cases where critical habitats of multiple species occur, as in NWAs, an ecosystem approach to the management of habitat is required to maximize benefit to all co-occurring species at risk (for example, fishes, birds, reptiles). Such an approach would require multi-jurisdictional cooperation and recognizes that negative impacts to some species and their habitats may result from habitat management practices aimed at achieving an overall net benefit to the ecosystem and the species at risk that it supports. This approach could be formalized within a management plan for the relevant NWAs, developed by ECCC in consultation with DFO.

9 Measuring progress

The performance indicators presented below provide a way to define and measure progress toward achieving the population and distribution objectives. A successful recovery program will achieve the overall aim of recovering populations to a state where they are stable or increasing, with low risk from known threats. Progress towards meeting these objectives will be reported in the report on the progress of implementing the first recovery strategy and potentially elements of this amended recovery strategy implementation.

The performance indicators are as follows:

1. The continued presence of Pugnose Shiner within its current distribution by 2025
2. Population trajectories in areas with defined critical habitat evaluated to be stable or increasing by 2030
3. Determination of the status of Pugnose Shiner populations at locations where the population status is unknown (for example, Teeswater River, Mouth Lake, St. Clair Unit of the St. Clair NWA, Trent River, Waupoos Bay, Wellers Bay, West Lake, East Lake) by 2030
4. Re-evaluation of the population status at locations considered poor (that is, Long Point Bay) and assess populations previously amalgamated as Lake St. Clair and tributaries as separate locations where feasible (for example, Whitebread Drain/Grape Run, Little Bear Creek) by 2025
5. Exploratory sampling conducted in new and suspected locations by 2025 (for example, St. Clair River, Maxwell Creek, Sydenham River, West Otter Creek, south shore of Lake St. Clair, Detroit River, Lake St. Francis)

10 Statement on action plans

The federal government’s approach to recovery planning is a 2-part approach, the first part being the recovery strategy and the second part being an action plan. An action plan contains specific recovery measures or activities required to meet the objectives outlined in the recovery strategy.

Ecosystem action plans that include implementation activities that benefit Pugnose Shiner have been completed by DFO, as well as PC. For example, the “Ausable River Ecosystem Recovery Strategy” (ARRT 2006) and the “Action Plan for the Ausable River in Canada: An Ecosystem Approach” (DFO 2020) includes recovery activities for the Pugnose Shiner. Although an ecosystem/multispecies document, this action plan includes several components that specifically implement recovery objectives for Pugnose Shiner in the OAC as well as Mouth Lake. Similarly, PC has published the “Multi-species Action Plan for Thousand Islands National Park of Canada” (PCA 2016), which also includes recovery actions that will benefit Pugnose Shiner within the Thousand Islands National Park. It is expected that an additional action plan will be developed within 5 years of posting this amended recovery strategy to implement the goals and objectives identified in the recovery strategy for populations outside the Ausable River watershed and Thousand Islands National Park areas.

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