Timber rattlesnake (Crotalus horridus): recovery strategy 2010
Species at Risk Act
Recovery Strategy Series
TABLE OF CONTENTS
- RESPONSIBLE JURISDICTIONS
- STRATEGIC ENVIRONMENTAL ASSESSMENT STATEMENT
- EXECUTIVE SUMMARY
- 1. BACKGROUND
- 1.1 Species Assessment Information from COSEWIC
- 1.2 Description of the Species
- 1.3 Populations and Distribution
- 1.4 Needs of the Timber Rattlesnake
- 1.4.1 Habitat and biological needs
- 1.4.2 Ecological role
- 1.4.3 Limiting factors
- 1.5 Threats
- 1.5.1 Threat classification
- 1.5.2 Description of threats
- 1.6 Actions Already Completed or Underway
- 1.7 Knowledge Gaps
- 2. RECOVERY FEASIBILITY
- 3. CRITICAL HABITAT
- 3.1 Identification of the Species’ Critical Habitat
- 4. CONSERVATION APPROACH
- 5. REFERENCES
- 6. TECHNICAL TEAM MEMBERS
List of Figures
List of Tables
Timber Rattlesnake (Crotalus horridus)
About the Species at Risk Act Recovery Strategy Series
What is the Species at Risk Act (SARA)?
SARA is the Act developed by the federal government as a key contribution to the common national effort to protect and conserve species at risk in Canada. SARA came into force in 2003, and one of its purposes is “to provide for the recovery of wildlife species that are extirpated, endangered or threatened as a result of human activity.”
What is recovery?
In the context of species at risk conservation, recovery is the process by which the decline of an endangered, threatened, or extirpated species is arrested or reversed, and threats are removed or reduced to improve the likelihood of the species’ persistence in the wild. A species will be considered recovered when its long-term persistence in the wild has been secured.
What is a recovery strategy?
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 goals and objectives and identifies the main areas of activities to be undertaken. Detailed planning is done at the action plan stage.
Recovery strategy development is a commitment of all provinces and territories and of three federal agencies -- Environment Canada, Parks Canada Agency, and Fisheries and Oceans Canada -- under the Accord for the Protection of Species at Risk. Sections 37–46 of SARA outline both the required content and the process for developing recovery strategies published in this series.
Depending on the status of the species and when it was assessed, a recovery strategy has to be developed within one to two years after the species is added to the List of Wildlife Species at Risk. A period of three to four years is allowed for those species that were automatically listed when SARA came into force.
In most cases, one or more action plans will be developed to define and guide implementation of the recovery strategy. Nevertheless, directions set in the recovery strategy are sufficient to begin involving communities, land users, and conservationists in recovery implementation. Cost-effective measures to prevent the reduction or loss of the species should not be postponed for lack of full scientific certainty.
This series presents the recovery strategies prepared or adopted by the federal government under SARA. New documents will be added regularly as species get listed and as strategies are updated.
To learn more
To learn more about the Species at Risk Act and recovery initiatives, please consult the Species at Risk (SAR) Public Registry.
Recovery Strategy for the Timber Rattlesnake (Crotalus horridus) in Canada - 2010
Environment Canada. 2010. Recovery Strategy for the Timber Rattlesnake (Crotalus horridus) in Canada . Species at Risk Act Recovery Strategy Series. Environment Canada, Ottawa. v + 17 pp.
Additional copies can be downloaded from the SAR Public Registry.
Cover illustration: Wayne Weller
Également disponible en français sous le titre
« Programme de rétablissement du crotale des bois (Crotalus horridus) au Canada »
© Her Majesty the Queen in Right of Canada, represented by the Minister of the Environment, 2010. All rights reserved.
Catalogue no.: En3-4/65-2009E-PDF
Content (excluding the illustrations) may be used without permission, with appropriate credit to the source.
This recovery strategy has been prepared in cooperation with the jurisdictions responsible for the timber rattlesnake. Environment Canada has reviewed and accepts this document as its recovery strategy for the timber rattlesnake, as required under the Species at Risk Act (SARA). This recovery strategy also constitutes advice to other jurisdictions and organizations that may be involved in recovering this species.
It was determined that the recovery of the timber rattlesnake in Canada is not technically or biologically feasible. The feasibility determination will be re-evaluated as warranted in response to changing conditions and/or knowledge.
Province of Ontario
Environment Canada drafted the recovery strategy in conjunction with the Timber Rattlesnake Technical Team. The Technical Team provided extensive information, personal knowledge, and guidance for the development of the document and reviewed the strategy extensively prior to posting.
Particular gratitude is expressed to both Craig Campbell and Wayne Weller. Craig Campbell collected and assembled much of the information for this species in Canada, and was instrumental in informing the assessment and listing of this species under the Ontario Endangered Species Act in the early 1970s. Additional thanks are extended to Rulon Clarke who was extremely helpful in sharing his knowledge and experiences from recovery initiatives for the timber rattlesnake in the United States. Finally, thanks are extended to those who have provided information or reviewed this document: Kate Hayes, Anne Yagi, Rob Tervo, Amy Brant, and Kim Barrett. The work of Francis Cook, Kim Barrett, and Jeff Rowell is also much appreciated as they have helped to document the occurrence of the timber rattlesnake in Canada.
A strategic environmental assessment (SEA) is conducted on all SARA recovery planning documents, in accordance with the Cabinet Directive on the Environmental Assessment of Policy, Plan and Program Proposals. The purpose of a SEA is to incorporate environmental considerations into the development of public policies, plans, and program proposals to support environmentally sound decision-making.
Recovery planning is intended to benefit species at risk and biodiversity in general. However, it is recognized that strategies may also inadvertently lead to environmental effects beyond the intended benefits. The planning process based on national guidelines directly incorporates consideration of all environmental effects, with a particular focus on possible impacts upon non-target species or habitats. The results of the SEA are incorporated directly into the strategy itself, but are also summarized below.
Because the timber rattlesnake is extirpated and recovery is determined to be not feasible, no further recovery action is considered necessary. Accordingly, this recovery strategy will have no effect on the environment.
SARA defines residence as: a dwelling-place, such as a den, nest or other similar area or place, that is occupied or habitually occupied by one or more individuals during all or part of their life cycles, including breeding, rearing, staging, wintering, feeding or hibernating [Subsection 2(1)].
Residence descriptions, or the rationale for why the residence concept does not apply to a given species, are posted on the SAR Public Registry.
The timber rattlesnake (Crotalus horridus) was designated Extirpated by the Committee on the Status of Endangered Wildlife in Canada (COSEWIC) in 2001 and was officially listed under the Species at Risk Act (SARA) in June 2003. SARA (Section 37) requires the competent Minister to prepare a recovery strategy for all listed extirpated, endangered, or threatened species. The Canadian Wildlife Service – Ontario, Environment Canada, led the development of this recovery strategy, and it was developed in cooperation with the Government of Ontario. All responsible jurisdictions reviewed and acknowledged receipt of this strategy.
Based on advice from a group of external experts, federal and provincial agency representatives (including people from Ontario Ministry of Natural resources (OMNR), Parks Canada Agency (PCA), Environment Canada (Canadian Wildlife Service ), Halton Region Conservation Authority, Niagara Parks Commission, academics, species experts), Environment Canada has determined that the recovery of the timber rattlesnake is not feasible.
Timber rattlesnake (Crotalus horridus) is the only wide-ranging woodland rattlesnake of deciduous forests in eastern North America. It was designated as Extirpated by the Committee on the Status of Endangered Wildlife in Canada (COSEWIC) in 2001.
A review of historic records of the timber rattlesnake in southwestern Ontario (including records from Essex, Kent, Elgin, Halton and Peel counties) and extreme southwestern Quebec finds the reliability and validity of the records to be circumspect for a variety of reasons including inadequate documentation, confirmed or presumed mis-identifications, or an inability to confirm historic sighting records (Rowell, in prep.). As a result, although these records were reviewed and considered, they have not been accepted as valid species’ records with complete documentation or used in the determination of recovery feasibility for the timber rattlesnake in Canada.
The only historic records that can be supported with any degree of certainty are records from the Niagara area. The last confirmed collection of the species in Canada was in the Niagara Gorge in 1941.
There are a number of threats that face United States populations and may face any reintroduced populations in Canada, including: indiscriminate killing, habitat loss/degradation, and the pet trade.
The recovery of the timber rattlesnake has been determined to be “not feasible” because sufficient suitable habitat is not available.
This feasibility determination will be re-evaluated as warranted in response to changing conditions and/or knowledge.
Date of Assessment: May 2001
Common Name (population): Timber Rattlesnake
Scientific Name: Crotalus horridus
COSEWIC Status: Extirpated
Reason for Designation: The Timber Rattlesnake once occupied much of the Niagara Escarpment and other regions of southern Ontario, but has not been seen in the province since 1941 despite intensive searches and its easy identification.
Canadian Occurrence: Ontario
COSEWIC Status History: Designated Extirpated in May 2001. Assessment based on a new status report.
The timber rattlesnake (Crotalus horridus) is the only wide-ranging woodland rattlesnake of deciduous forests in eastern North America (Smith 2001). The adult snakes are large, ranging from 887-1892 mm (34.92 – 74.49 inches) in total length (Collins and Knight 1980).
This species has a dorsal pattern consisting of 15 to 34 (mean 24) dark bands which become crossbands near the tail (Collins and Knight 1980). These markings are typically chevron-shaped but may break into a series of three transversely elongated blotches towards the front of the body. In some snakes, the pattern is obscured by the nearly black ground colour (Collins and Knight 1980). There are two common colour phases1 observed in the timber rattlesnake, “yellow” and “black”, which refer to the ground colour of the snake. Rowell [In Prep.] reports that both colour phases appear to have been present in Ontario, with dark “almost black” timber rattlesnakes reported in the Hamilton area (Galinee 1669), yellow phases reported in the Niagara Glen area (Logier 1939), and additional documentation provided by Gourlay (1822). This ground colour can also be brown, black, or grey (Collins and Knight 1980; Smith 2001). The top of the head varies from dark to pale, sometimes with round occipital spots (Collins and Knight 1980). A distinguishing characteristic of the timber rattlesnake from all other species of snakes found in Ontario is the presence of a number of small irregular scales on the top of the head, as opposed to 9 larger plates found on other species. The dorsal scales are keeled, giving the snake a dull appearance (Collins and Knight 1980). Juveniles are similar to adults but may be a lighter shade.
Males tend to be larger than females. Sex may be determined by tail length, which is greater in males (Brown 1993; Galligan and Dunson 1979). This is largely believed to be due to the slower growth rate in females once they reach maturity, and/or a longer lifespan in males (Galligan and Dunson 1979).
The timber rattlesnake is a pit viper and uses the pits on its head to sense heat and movement of prey. These pits, along with the vertical nature of the pupils and the triangular head, which is distinct from its neck, distinguish it from non-venomous snakes (Harding 1997). Another distinguishing feature is the rattles on the snake’s tail (Smith 2001). The snake will vibrate its rattles when threatened, making a distinct buzzing sound. The rattle consists of a series of articulated keratinized segments, with a new segment added with each shedding. The number of segments varies depending on the amount of wear and the rattle may be missing altogether (Rowell, In Prep).
1 “Colour phases” refers to the different colouration types which are present within a species. These phases or types indicate the overall colour or background colour of the species.
Considered ‘apparently globally secure’ (G4)2, the timber rattlesnake is found throughout eastern and the mid-western United States (NatureServe 2006). While it has a large range, occurrences are spotty in some regions (NatureServe 2006). The species ranges from central New England to northern Florida, west to eastern Texas, central Oklahoma, eastern Kansas, southeastern Nebraska, southern and eastern Iowa and southeastern Minnesota (NatureServe 2006).
At the time of European settlement, the timber rattlesnake inhabited 30 states as well as Ontario and was known to be abundant within its North American range. However, by the 1970s, the species had been nearly extirpated from all but a few locations in the United States (Morris 1974). In the United States, the species is listed as apparently secure nationally (N4). However, out of the 19 states in which timber rattlesnake populations are found, it is critically imperiled (S1) in 5 states, imperiled (S2) in 3 states, and vulnerable in 9 while it is extirpated from 2 states (NatureServe 2006; Table 1). In Canada, it is designated as extirpated by COSEWIC (Nature Serve 2006; COSEWIC 2001). Timber rattlesnake is designated as Endangered-Regulated in Ontario (OMNR 2006).
The earliest reports of timber rattlesnakes in Canada occurred in 1669 in what is now known as Waterdown in Halton County (Logier 1939 in Smith 2001). A review of historic records of the timber rattlesnake in Ontario (Figure 1 and Rowell, in prep.) shows the reliability and validity of many of these records to be circumspect (Rowell, in prep.). The only historic record that can be supported with any degree of certainty is that from the Niagara area. The last known collection was in the Niagara Gorge -specifically, the Niagara Glen- in 1941 (Cook, 1999). There were a few unconfirmed sightings in Ontario, in the 1950s and 1960s, mostly in the Niagara Gorge area; however, there is general consensus that the species has been extirpated form the province (Rowell, in prep.). Beyond the Niagara area, the extent of the historic distribution of the timber rattlesnake in very unclear. There are historic, unconfirmed sightings from a few sites in southwestern Ontario, including Pelee Island. There are also two timber rattlesnake specimens thought to be from Campbellton and Fitzwilliam Island (Figure 1) for which locality information cannot be confirmed (Rowell, in prep.; M. J. Oldham pers. comm. 2010). Sighting records have remained unconfirmed for a variety of reasons including records are lacking information or complete documentation (e.g., specific locality information), are difficult to interpret as they date from the mid-1900s to 1960 and cannot be validated or are believed to be mis-identifications of the species (Rowell in prep.). In addition, there have been sighting records in extreme southern Quebec (Phillipsburg and Covey Hill areas); again, none of these has been substantiated (Martin 1982).
2 G4: NatureServe Global Conservation Status Rank, Apparently Secure - Uncommon but not rare; some cause for long-term concern due to declines or other factors (NatureServe, 2007)
As a result, although these records were reviewed and considered, they have not been accepted as valid species’ records with complete documentation or used in the determination of recovery feasibility for the timber rattlesnake in Canada.
Populations within the United States have been studied to determine the minimum viable population size. Some authorities believe that in order to maintain a “stable” population, a minimum of 40 individuals is required with an even aged distribution within the population (Ewing 2003).
Figure 1. Timber rattlesnake historical occurrence map in Canada (NHIC, 2001)
Specimen/Photo/Taped Call category in legend is a standard category used by NHIC; taped calls do not apply to timber rattlesnake.
The timber rattlesnake is secretive and shy by nature and prefers areas not frequented by humans (Brown 1981). This snake typically inhabits forested areas with rock outcrops, dry ridges and second growth deciduous or coniferous forests with southern exposures (Brown 1993; Smith 2001). The most common overstory trees include red oak, eastern hemlock, sugar maple, white ash, white pine, American beech, birch, American basswood, and eastern red cedar (Brown 1993).
Ditmars (1939 as reported in Rowell, In Prep.) refers to timber rattlesnakes in New Jersey as inhabiting ‘flat forested country back of the central coast, [and] quite damp in spots’. This suggests that, if this snake was ever widely distributed throughout Ontario, it likely occupied similar habitat in addition to forested areas with rocky outcrops.
Specific summer habitat requirements differ according to sex (Brown 1993; Smith 2001; Ewing 2003). Males and non-gravid females tend to use habitat with greater than 50% forest canopy cover, dense surface vegetation, and few fallen logs (Ernst 1992). Gravid females tend to use less densely forested areas with 25% canopy cover, numerous fallen logs, equal portions of vegetation and leaf litter as well as warmer microclimate (Brown et al. 1982, Ernst 1992). Studies in the United States have indicated that an area of approximately 51 km² of suitable habitat is necessary to sustain a population of timber rattlesnakes (Brown 1993).3
Hibernacula for this species are typically located in a rocky area with underground crevices (Brown 1993). A hibernaculum will characteristically be one of three types: fissure in a ledge or crevice interface between ledge and ground; talus below a cliff, or open scree slope; or fallen rock partly covered by soil (Brown 1993). In Ontario, hibernacula were most often located along the Niagara Escarpment (Logier and Toner 1961). Timber rattlesnakes have high fidelity to their hibernacula, returning year after year (Odum 1979).
Snakes near the northern extent of the range usually hibernate for 7.4 months. Typically they emerge in early to mid-May and enter hibernation generally in mid September to early October but may stay out as late as November (Brown 1993). Emergence and entrance into hibernation are likely affected but not completely determined by temperature (Smith 2001). They are also known to hibernate communally, putting them at risk of being captured or killed by poachers, or susceptible to catastrophic loss due to land development (Odum 1979). There is very little information specific to dens historically found in Ontario, although two potential den sites – one in Spencer Gorge below Dundas Peak and the other in Medad Valley – are noted by Lamond (1994).
Timber rattlesnakes also use specific habitat transition zones to migrate from their hibernacula to their summer habitat that tends to be located within 200 m of the hibernaculum. The transition zone is often broken by the rough topography and rocky terrain with a more open woodland containing exposed clearings and shelter rocks (Brown 1993). This habitat is used for basking by migrating snakes in the spring and fall as well as by gravid females for gestation and birth (Brown 1993). These snakes are known to have strong site fidelity for specific basking rocks within this habitat (Brown 1993).
During the summer, the snakes may be active during the day or night; however, nocturnal activity is especially common during hot summer nights (Smith 2001; Ewing 2003). Snakes travel throughout their summer range in search of food and mates. Timber rattlesnakes are also known to be proficient climbers and swimmers, although they are primarily terrestrial. Mean maximum migratory distance from the hibernaculum during the summer was 4.07 km (2.5 miles) for males and 2.05 km (1.3 miles) for females tracked in New York (Brown 1993), although the majority travel a maximum of 1.6 km (1.0 miles) from their den sites during the summer.
Mean sizes of activity areas for timber rattlesnakes in New Jersey and Pennsylvania ranged from 4 ha for gravid females to a maximum of 207 ha for males (Brown 1993).
Gravid females do not typically leave the transitional habitats (Reinert and Zappalorti 1988b). Males tend to move greater distances in search of mates, while females are more passive in the search for mates (Reinert and Zappalorti 1988b). As well, the higher energy costs associated with reproducing may leave non-gravid females with lower energy reserves than males, reducing the distance they can travel (Reinert and Zappalorti 1988b).
Timber rattlesnakes males reach maturity at an average age of 5.3 years while the mean age of first reproduction for females is 7.8 years (Smith 2001). In the northern regions of their range, females reproduce on average every three years (Brown 1981). Therefore, a female might have only three to five reproductions in a lifetime (Brown 1981).
Mating takes place in late summer (Martin 1993). In northern New York state, the mating season is estimated to occur between mid-July and late September (Aldridge and Brown 1995). There appears to be sperm storage in the oviduct of the female over the winter (Aldridge and Brown 1995). Males may use scent trails to locate receptive females during the breeding season (Reinert and Zappalorti 1988b).
Gestation periods are likely between four and six weeks, however, periods of up to three months have also been reported (Martin 1993). Females give birth to about 5-13 young, with reports ranging from 3–19 and an average of about 8, typically between late August and mid-September (Martin 1982). Neonates are about 200-280 mm snout to vent length (Galligan and Dunson 1979). There is also some evidence to indicate that neonates follow scent trails of their mothers and other rattlesnakes in order to find a hibernaculum for the winter (Reinert and Zappalorti 1988a).
The average lifespan of the timber rattlesnake is 25 years (Brown 1993; Ewing 2003). However, mortality tends to be high in the first few years. One study estimated mortality at 45% in the first year and 25% annually thereafter (Smith 2001). A timber rattlesnake lived for approximately 36.5 years in captivity and reached a total length of 1770 mm (Cavanaugh 1994).
The timber rattlesnake is predominately an ambush predator (Ernst 1992). It coils adjacent to fallen logs with its head positioned perpendicular to the long axis of the log and waits for its prey (Smith 2001). It feeds primarily on small rodents, such as white footed mouse, red-backed voles, eastern chipmunks, and cottontail rabbits. It may also consume carrion, other reptiles, amphibians, birds and bird eggs (Uhler et al. 1939, Myers 1956, Anderson 1965), although reptiles and amphibians appear to make up only a small proportion of their diet (Clark 2002).
The timber rattlesnake injects venom into its prey in order to kill it. The snake’s venom is harmful to humans, especially small children who are more sensitive to the venom due to their small size (Guidry 1953), and it has a reported striking distance of 46 cm (Ditmars 1907). However, reports of humans being accidentally bitten are rare, and timber rattlesnakes are generally viewed as being quite placid in nature, preferring to escape unnoticed (Ditmars 1907, Anderson 1965). In fact, Minton and Minton (1969) describe the timber rattlesnake as being ‘one of the more mild tempered rattlers’.
3 “Occasional individual rattlesnakes are known to move as far as 4.5 miles (7.2 km) from their den. The maximum migratory distance averages 2.5 miles (4.07 km) for males. With the den as a central focal point, a radial distance of 2.5 miles in all directions from a den yields a total area of 19.6 square miles (51 km²) of habitat area for a healthy population.” (Brown 1993)
Timber rattlesnakes are small mammal predators and therefore help control the rodent population. This can help to reduce damage to crops.
There are a number of biological traits which limit timber rattlesnake population growth and its ability to recover from large-scale losses. This species has a low reproductive rate and females are not typically capable of reproducing until nine years of age (Brown 1993). This along with the small litter size, low adult survivorship, and the triennial reproduction period prevent a high recruitment rate (Brown 1993). The snake also has a highly variable reproductive success that hinders its ability to replace snakes which are removed from the population (Brown 1993). High juvenile mortality rates, often as a result of predation by species such as crows, ravens, hawks, and carnivorous mammals, also inhibit a larger population size (Brown 1993).
Research has shown that individuals within the same hibernaculum are more closely related to each other than they are to individuals from other hibernacula. The potential for a high frequency of mating among individuals sharing the same hibernation site can lead to inbreeding and reduced genetic variation (Bushar, et al. 1998).
Note: The reference to unknown in the Threat Attributes category indicates where the threat level is not known for Canada due to the absence of the species here. The level is based on information from the United States or that obtained from similar species in Ontario.
The precise threats leading to the decline and ultimate extirpation of the timber rattlesnake from Ontario are not understood with any degree of certainty; however, it is likely that habitat loss and human persecution played a significant role. The threats are presented in order of decreasing significance:
18.104.22.168 Disturbance or Persecution and Consumptive Use
In Ontario, these snakes have been historically subjected to direct persecution and it is anticipated that this would be true today, similar to the persecution directed at the Massasauga Rattlesnake. It is not uncommon for snakes, particularly venomous ones, to be killed for being in the vicinity of human activity. Rowell (in prep.) documents various sources to suggest that the consumption of timber rattlesnake and its use in folk remedies may have also played a role in its decline.
Recreational activities, such as the use of hiking trails, in areas that were historically used by timber rattlesnake might pose a direct threat to the species if they were reintroduced through disturbance to the individuals and to their habitat. Timber rattlesnakes are believed by some researchers to be susceptible to disturbance by human beings and result in behavioural changes including abandonment of basking areas (Brown, 1993). Other researchers have concluded that non-threatening activities by human beings, including pedestrian and vehicular traffic in close proximity, do not typically result in long term changes in the snake’s behaviour (Reinert and Zappalorti, 1988a).
The timber rattlesnake’s colouration and ability to adapt well to captivity make them an attractive species for people involved in the pet trade (Brown, 1993). Collection of individuals for the pet trade is known to occur in the United States (Ewing, 2003), and may threaten a population reintroduced into Canada. Currently, there are no “harvestable” snakes in many existing populations of timber rattlesnake because of the demographic constraints and age structure of the populations (Brown et al. 1982). In fact, the removal of even one individual, especially an adult female, can easily reduce the population’s ability to be self sustaining (Brown et al. 1982). Such removals would be anticipated to have significant impacts on any natural or reintroduced populations.
In the United States, timber rattlesnakes have been the subject of bounty hunting since 1719 (Smith 2001). Until recently, a number of county and state governments, including Minnesota, New York, Pennsylvania, Vermont, and Wisconsin, paid such bounties, which ultimately contributed to dramatic declines in some populations (Brown 1993).
In addition to bounty hunting, timber rattlesnakes have been harvested for commercial purposes. Snakes are harvested for their rattles and oil (Galligan and Dunson 1979). They are also captured for roadside reptile “farms” and tourist exhibits. Fortunately, the popularity of these is declining (Brown 1993).
Organized snake round ups still occur in parts of the northeastern United Sates. These round ups are organized hunts for snakes, to remove snakes from the area or to continue the tradition of hunting snakes, and are often treated as community events and are often used as fundraisers for the community. These hunts are legal in the United States. These events are contributing to the population decline (Reinert 1990; Brown 1993). Although some snakes are released, they may not be released in the same areas where they were captured or might have sustained internal injuries from being captured and ultimately die as a consequence (Reinert 1990). In the late 1960s and early 1970s, it was a common occurrence in north-central Pennsylvania for local communities to host fall fairs at which timber rattlesnake belts and mounted heads, made from snakes captured the previous week, were sold and displayed (W.F. Weller, pers. comm.).
Overall, hunters have noted large declines in local populations and much of this decline can be attributed to hunting practices (Galligan and Dunson 1979). For example, it has been observed that a large population within one hibernaculum can be completely eliminated within five to seven years (Galligan and Dunson 1979).
22.214.171.124 Habitat Loss and Degradation
Habitat loss through urban development, logging, and aggregate extraction reduces the amount of available habitat for the species, leading to population declines (Wright and Wright 1957, Weller 1982). The timber rattlesnake’s historic Canadian range was within some of the most developed areas in Ontario, which suggests that suitable habitat has since been largely destroyed.
There has been considerable industrial, agricultural, and residential development in the Niagara area where the timber rattlesnake historically occurred. A limestone extraction operation located near the Whirlpool began in the early 1800s and continued for many years. As well, in the late 1800s, the Tablerock area was developed for tourism, the Maid-of-the-Mist operation began, as well as development and the operation of the railway system, located (in some areas) near the Niagara river shoreline, was initiated. The Ontario Power Generating Station just below Niagara Falls was put into service in 1905. Finally, the construction of Sir Adam Beck generating stations (#1 and #2), both owned by Ontario Power Generation Inc., were put into service in 1922 and the early 1950s respectively. (Weller, pers. comm.). This development and increased activity degraded habitat in the Niagara region and likely contributed to the extirpation of the species.
Road kill is an additional aspect of human-induced mortality (Martin et al. 1992). Roads are a significant cause of mortality to many species of snakes. A very extensive road network and increasing traffic are leading to increasing incidences of road mortality. This would likely be a threat to timber rattlesnakes if they were reintroduced to Ontario. Roads may also act as a barrier to dispersal as many snakes are killed crossing roads.
Habitat degradation by humans may also affect population numbers. Alterations such as continuous repositioning of basking and shelter rocks or repeated visits by humans to basking sites may eventually lead to the snake’s abandonment of the site entirely (Brown 1993).
The alterations made to the habitat of the timber rattlesnake in Ontario cannot be mitigated and the habitat cannot be rehabilitated.
126.96.36.199 Natural Processes or Activities
The natural progression of forest succession may be incompatible with the long-term survival of timber rattlesnakes, if the canopy cover results in too much shade (Brown 1993). Eventually such growth may render a hibernaculum unsuitable for use and cause the extirpation of the species from the area. However, the impacts of increased shading are not entirely understood, with some suggestions that selective tree removal may actually harm the snakes more (Smith 2001).
Actions that have been completed or are underway include:
- Museum and library searches for specimens and information.
- Meetings with rattlesnake experts in Canada and the United States.
- Zoo checks for a source of genetic material.
Information gaps for timber rattlesnake include:
- Impact of reintroduction on other species
- Critical habitat requirements
- Habitat restoration techniques – creation of hibernacula, artificial birthing sites, etc.
- Causes of the species extirpation from Canada
- Former range, population size and habitat needs in Canada
- Prey availability studies at former and potentially suitable sites.
- Habitat quality at former and potentially suitable sites
- Verification of historical reports
The recovery of timber rattlesnake has been determined not to be technically and biologically feasible for the following reasons:
- Are individuals capable of reproduction currently available to improve the population growth rate or population abundance?
Unknown. There are no known extant populations of the timber rattlesnake in Canada. The species is, however, relatively widespread in the United States. The U.S. populations could be used to assist with the reintroduction of the species to Canada, if it is determined that the populations can withstand removal of individuals for this purpose.
- Is sufficient suitable habitat available to support the species or could it be made available through habitat management or restoration?
No. There is not sufficient habitat for the species remaining in the verified historical locations in Canada. There is insufficient land available as suitable habitat or for management or restoration. The extensive network of roads and intensely cultivated landscape on the tablelands around Niagara fragments any potential habitat to a size that is insufficient to support a viable population. Also, there is little green space remaining in this area which could be managed for the species. Studies in the United States have indicated that an area of approximately 51 km2 of suitable habitat is necessary to sustain a population of timber rattlesnakes (Brown 1993). Habitat of this extent does not exist in areas within the verified historical locations.
- Can significant threats to the species or its habitat be avoided or mitigated through recovery actions?
Unknown. It is unknown if the threats to the species can be avoided or mitigated through recovery actions. The threats which led to the extirpation of the species are not fully understood.
- Do the necessary recovery techniques exist and are they demonstrated to be effective?
Unknown. The necessary techniques for reintroducing this species are currently being studied in the United States. It is unclear whether these techniques would be effective for recovering the timber rattlesnake in Canada and therefore more study would be required. It is also unclear what recovery techniques would be required to address the threats to the species.
Critical habitat is not identified in this recovery strategy because, as explained in the feasibility section, sufficient suitable habitat is not available for management or restoration. If conditions should change, critical habitat identification will be reconsidered.
The recovery of this species is considered not feasible because sufficient suitable habitat is not available. No specific recovery efforts will be made. The conservation approach will be reexamined as warranted in response to changing conditions and/or knowledge.
Monitoring and follow-up work (e.g. confirmation) on timber rattlesnake observations reported by individuals during surveys done for other species in southern Ontario will be undertaken should such observations be made.
Aldridge, R.D. and W.S. Brown. 1995. Male reproductive cycle, age at maturity, and cost of reproduction in the timber rattlesnake (Crotalus horridus). Journal of Herpetology 29: 399-407.
Anderson, P. 1965. The reptiles of Missouri. University of Missouri Press, Columbia, Missouri.
Brown, W.S. 1981. Conserving the Timber Rattlesnake. Conservationalist. 36: 27-29.
Brown, W.S. 1993. Biology, status and management of the timber rattlesnake (Crotalus horridus): a guide for conservation. SSAR Herpetological Circular No. 22.
Brown, W.S., D.W. Pyle, K.R. Greene and J.B. Friedlaender. 1982. Movements and temperature relationships of timber rattlesnake (Crotalus horridus) in northeastern New York. Journal of Herpetology 16:151-161.
Bushar, L.M., H.K. Reinert, and L. Gelbert. 1998. Genetic variation and gene flow within and between local populations of the timber rattlesnakes (Crotalus horridus). Copeia. 1998: 411-422.
Cavanaugh, C.J. 1994. Crotalus horridus (Timber Rattlesnake) longevity. Herpetological Review. 25:70.
Clark, R.W. 2002. Diet of the Timber Rattlesnake (Crotalus horridus). Journal of Herpetology. 36: 494-499.
Collins, J.T., and J.L. Knight. 1980. Crotalus horridus. Catalogue of American Amphibians and Reptiles.
Cook, F.R. (1999). Unpublished timber rattlesnake account in “The Natural History of Amphibians and Reptiles in Canada.”
Cook, F.R. 1993. Unpublished timber rattlesnake manuscript as cited in Rowell, J.C. In Preparation. The Snakes of Ontario – A Natural History
COSEWIC. 2001. COSEWIC assessment and update status report on the timber rattlesnake, Crotalus horridus, in Canada. Committee on the Status of Endangered Wildlife in Canada. Ottawa.
Ditmars, R.L. 1907. The reptile book. Doubleday, Page and Company.
Ditmars, R.L. 1939. A Field Book of North American Snakes. Doubleday, Garden City, New York as reported in Rowell, J.C. In Preparation. The Snakes of Ontario – A Natural History.
Ernst, C.H. 1992. Venomous reptiles of North America. Smithsonian Institution Press, Washington.
Ewing, R. (ed). 2003. Wayne National Forest – Species Data Collection Form. Last updated: September 6, 2003.
Galinee, R. 1669. Journey of Dollier and Galinee, 1669-1670.
Galligan, J.H., and W.A. Dunson. 1979. Biology and status of timber rattlesnake (Crotalus horridus) populations in Pennsylvania. Biological Conservation 15: 13-58.
Gourlay, R.F. 1822. A Statistical Account of Upper Canada with a view to a grand system of emigration (Vol I). Simpkin and Marshall, Stationers Court.
Guidry, E.V. 1953. Herpetological notes from southeastern Texas. Herpetologica. 9:49-56.
Harding, J.H. 1997. Amphibians and reptiles of the Great Lakes region. The University of Michigan Press, Ann Arbor: MI.
Lamond, W.G. 1994. The Reptiles and Amphibians of the Hamilton Area: An historical summary and the results of the Hamilton Herpetofaunal Atlas. Hamilton: Hamilton
Logier, E.B.S. 1939. The reptiles of Ontario. Royal Ontario Museum of Zoology, Handbook. No. 4. University of Toronto Press, Toronto, Ontario.
Logier, E.B.S. and G.C. Toner. 1961. Check list of the amphibians and reptiles of Canada and Alaska (2nd Edition). Contributions of the Royal Ontario Museum Life Sciences 53.
Martin, W.H. 1982. The timber rattlesnake in the northeast: its range, past and present. Herpetological Bulletin of the New York Herpetological Society. 17: 15-20.
Martin, W.H. 1993. Reproduction of the timber rattlesnake (Crotalus horridus) in the Appalachian Mountains. Journal of Herpetology. 72: 133-143.
Martin, W.H., J.C. Mitchell, and R. Hoggard. 1992. Crotalus horridus (Timber Rattlenake). Herpetological Review. 23: 91.
Minton, S.A., and Minton, M.R. 1969. Venemous Reptiles. New York: Scribner's Sons.
Morris, P.A. 1974. An introduction to the reptiles and amphibians of the United States. Dover Publications, Inc., New York.
Myers, C.W. 1956. An unrecorded food item of the timber rattlesnake. Herpetologica. 12:326
NatureServe. 2006. Comprehensive species report – Timber Rattlesnake.
NatureServe. 2007. Glossary – NatureServe. Downloaded on September 20, 2007.
Odum, R.A. 1979. The distribution and status of the New Jersey timber rattlesnake including an analysis of Pine Barrens populations. HERP Bulletin of the New York Herpetological Society 15: 27-35.
Oldham, M. J. 2010. Pers. comm. January 13, 2010.
Ontario Ministry of Natural Resources. 2006. Species at risk in Ontario list, June 30, 2006. Accessed: January 16, 2007
Reinert, H.K. 1990. A profile and impact assessment of organized rattlesnake hunts in Pennsylvania. Journal of the Pennsylvania Academy of Sciences 64: 136-144.
Reinert, H.K. and R.T. Zappalorti. 1988a. Field observation of the association of adult and neonatal timber rattlesnakes, Cortalus horridus, with possible evidence of conspecific trailing. Copeia 4: 1057-1059.
Reinert, H.K. and R.T. Zappalorti. 1988b. Timber rattlesnakes (Crotalus horridus) of the Pine Barrens: their movement patterns and habitat preferences. Copeia 4: 964-978.
Rowell, J.C. In Preparation. The Snakes of Ontario – A Natural History.
Smith, K. 2001. COSEWIC status report on the timber rattlesnake, Crotalus horridus, in Canada, Committee on the Status of Endangered Wildlife in Canada. Ottawa.
Uhler, F.M., C. Cottam and T.E. Clarke. 1939. Food of snakes of the George Washington National Forest, Virginia. Transactions of the 4th North American wildlife conference.
Weller, W.F. 1982. Rare and endangered reptiles in Ontario (Part 1). Canadian Amphibian and Reptile Conservation Society Bulletin. 20: 1-8.
Weller, W.F. Pers. comm.
Wright, A.H., and A.A. Wright. 1957. Handbook of snakes of the United States and Canada. Comstock Publishing Associates, Ithaca.
Ron Brooks, University of Guelph
Kim (Smith) Barrett, Halton Region Conservation Authority
Alain Branchaud, Canadian Wildlife Service, Quebec
Craig Campbell, Retired Herpetologist
Ron Dale, Parks Canada
Andrew Lentini, Toronto Zoo
Angela McConnell, Canadian Wildlife Service, Ontario
Michael Oldham, Ontario Ministry of Natural Resources
Andrew Promaine, Parks Canada
Rob Ritchie, Niagara Parks Commission
Rob Tervo, Ontario Ministry of Natural Resources, Guelph District
Wayne Weller, Expert
Anne Yagi, Ontario Ministry of Natural Resources, Guelph District
Kate Hayes, formerly Canadian Wildlife Service, Ontario (2006-2007)
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