|Scientific Name:||Lynx rufus|
|Species Authority:||(Schreber, 1777)|
|Taxonomic Notes:||Taxonomy is currently under review by the IUCN SSC Cat Specialist Group (2014). Placed in Lynx according to genetic analysis (Johnson et al. 2006).|
|Red List Category & Criteria:||Least Concern ver 3.1|
|Assessor(s):||Kelly, M., Morin, D. & Lopez-Gonzalez, C.A.|
|Reviewer(s):||Nowell, K., Hunter, L., Schipper, J., Breitenmoser-Wursten, C. & Lanz, T. and Breitenmoser, U.|
The Bobcat is listed as Least Concern because it is abundant and wide-ranging and is not suspected to be declining at a rate that would qualify it for Near Threatened. Bobcats are widely-distributed and their current range consists of most of the United States, southern Canada, and Mexico where the state of Oaxaca remains the southern-most limit for the species. However, local threats may present challenges for long term persistence in some regions including market hunting for the fur trade, direct habitat loss caused by increased urbanization, and indirect effects of urbanization such as genetic isolation and lethal/sublethal exposure to anticoagulant rodenticides (southern California). Florida is the only US state to report Bobcat declines with Bobcat observations decreasing dramatically as invasive pythons have increased in the southern part of the state. Additionally, some concern exists about sustainability of current bag limits with the increasing value of Bobcat pelts (West Virginia). Other local threats include possible disease transmission (canine distemper in Bobcats in eastern Canada), direct conflict with domestic/feral animals including feral dogs (northern Mexico), and poisoning and medicinal uses of Bobcats (central and southern Mexico). Bobcat densities are low in central and southern, compared to northern, Mexico. The recent discovery of hybridization between the Bobcat and the sympatric Canadian Lynx may result in conservation actions for the endangered lynx recovery.
|Previously published Red List assessments:|
|Range Description:||Bobcats occur in southern Canada and throughout the United States and Mexico. In Canada, Bobcats appear to be extending their range northward as forest clearing occurs (Nowell and Jackson 1996, Sunquist and Sunquist 2002). Recent confirmation of Bobcats via remote camera, suggests Bobcat range extends further into the Canadian Rocky Mountains than previously thought (Lobo and Millar 2010). In the United States, bobcats were thought to be extirpated by the early 1900s from several Midwestern states including Iowa, Illinois, Indiana, Ohio, and Missouri, due to habitat loss and exploitation (Lariviére and Walton 1997), but they have recently recolonized these areas (Roberts and Crimmins 2010). Bobcats now occur in all contiguous United States except Delaware. Bobcats are found throughout Mexico, particularly in western Mexico and southward from the Sonoran desert. Competitive interactions with ecologically similar felids could be a factor in limiting their southern distribution, but similar competitors are present in other areas of Mexico (Sanchez-Cordero et al. 2008). Thus, the absence of Lynx rufus below the Isthmus of Tehuantepec may be due to the absence of prey species. However, confirmative data of Bobcat presence throughout Mexico is somewhat scanty. While Bobcat range is thought to stop at the Isthmus of Tehuantepec in southern Mexico (Sanchez-Cordero et al. 2008, Gonzalez-Salazar et al. 2013), this is based on habitat modeling rather than verified confirmations. While generally favoring low and mid-elevations, in the western US, Bobcat have been trapped at elevations up to 2,575 m (Nowell and Jackson 1996). In Mexico, radio-collared Bobcats were located at 3,500 m on the Colima Volcano in western Mexico (Burton et al. 2003).|
Native:Canada (Alberta, British Columbia, Manitoba, New Brunswick, Nova Scotia, Ontario, Prince Edward I., Québec, Saskatchewan); Mexico (Baja California, Baja California Sur, Chihuahua, Coahuila, Durango, Guanajuato, Guerrero, Hidalgo, Jalisco, México Distrito Federal, México State, Michoacán, Morelos, Nayarit, Nuevo León, Oaxaca, Puebla, Querétaro, San Luis Potosí, Sinaloa, Sonora, Tamaulipas, Tlaxcala, Veracruz); United States (Alabama, Arizona, Arkansas, California, Colorado, Connecticut, Florida, Georgia, Idaho, Illinois, Indiana, Iowa, Kansas, Kentucky, Louisiana, Maine, Maryland, Massachusetts, Michigan, Minnesota, Mississippi, Missouri, Montana, Nebraska, Nevada, New Hampshire, New Jersey, New Mexico, New York, North Carolina, North Dakota, Ohio, Oklahoma, Oregon, Pennsylvania, Rhode Island, South Carolina, South Dakota, Tennessee, Texas, Utah, Vermont, Virginia, Washington, West Virginia, Wisconsin, Wyoming)
|Range Map:||Click here to open the map viewer and explore range.|
|Population:||In 2010, Roberts and Crimmins surveyed state wildlife management agencies in each of the 48 contiguous states regarding the current population status of Bobcats. Populations were reported to be stable or increasing in 40 states, with six states unable to report population trends and only one state (Florida) reporting decreases in Bobcat populations. The total Bobcat population for the US is estimated to be between 2,352,276 to 3,571,681 individuals, indicating that Bobcat populations have increased throughout the majority of their range in North America since the late 1990s. In particular, Bobcat populations have rebounded in the Midwestern states in recent decades. Bobcats now occur in all contiguous United States except Delaware. Five Canadian provinces reported stable Bobcat populations, one reported a stable or increasing population, and one reported a fluctuating population. Bobcat population sizes and status in Mexico are not well known.|
Despite being widespread, there are only a few estimates for the densities that bobcats can attain. Density estimates include: 57-62 / 100km² in California (Alonso et al. 2015), 48/100 km² in Texas (Heilbrun et al. 2006), 25/100 km² in Arizona (Lawhead 1984), <9/100 km² in Idaho (Knick 1990), and 11/100 km² in Virginia (minimum estimate, M. Kelly and D. Morin pers. comm. 2015). Bobcat densities in the northern parts of their range are generally lower than in the south (Sunquist and Sunquist 2002). A density estimate for Bobcats in Mexico was low, at five individuals per 100 km² (Arzate et al. 2007). Bobcat densities can vary dramatically depending on site and Thornton and Perkins (2015) found that densities in Texas were lowest in the most heavily modified landscape, and that Bobcat capture probability was positively related to forest cover.
|Current Population Trend:||Stable|
|Habitat and Ecology:||In the US, the Bobcat ranges through a wide variety of habitats, including boreal coniferous and mixed forests in the north, bottomland hardwood forest and coastal swamp in the southeast, and desert and scrubland in the southwest. Only large, intensively cultivated areas appear to be unsuitable habitat. Areas with dense understory vegetation and high prey density are most intensively selected by Bobcats (Nowell and Jackson 1996). The requisite features of Bobcat habitat typically include areas with abundant rabbit and rodent populations, dense cover, and shelters that function as escape cover or den sites (Sunquist and Sunquist 2002). In Mexico, Bobcats are found in dry scrub and grassland, as well as tropical dry forest including pine, oak and fir (Monroy-Vilchis and Velazquez 2003, Arzate et al. 2007, C. Lopez-Gonzalez pers. comm. 2007). |
Like its close relative Lynx canadensis the Bobcat preys primarily on lagomorphs (rabbits), but is much less of a specialist. Rodents are commonly taken, and Bobcats are capable of taking larger prey, including young ungulates (Nowell and Jackson 1996, Sunquist and Sunquist 2002). A study in Virginia found Bobcats preyed on a wide variety of species (15 total) including squirrels, chipmunks, white-tailed deer, voles, and rabbits, appearing to switch prey seasonally as certain prey items became more available (Montague 2014, Morin et al. in review).
Bobcats in New Hampshire appear to favour areas with few roads, limited human development, high stream densities, and steep topography (Broman et al. 2014). Similarly, Bobcats in Vermont have positive responses to shrub, wetland, deciduous, and coniferous cover types, and negative responses to road and mixed cover types, and Bobcats prefer to move through forested land and scrub/rock cover rather than move through developed land cover types (Donovan et al. 2011). The recently re-established Bobcats in Iowa showed a strong preference for forest over any other habitat type (Reding et al. 2013, Tucker et al. 2008). In Virginia, Bobcats were also shown to occur more often father away from roads (Kelly and Holub 2008). So while Bobcats can adjust to some levels of human encroachment, studies support the preference of Bobcats for vegetative cover and water in areas away from roads. Bobcat populations have been shown to decline in areas where forests have matured and no longer support abundant prey, namely cottontails (Litvaitis et al. 2006). Additionally, in Texas, when in the presence of Ocelots, Bobcats selected areas with <75% canopy cover, likely facilitating coexistence between the two predators and demonstrating the Bobcat’s flexibility in habitat selection (Horne et al. 2009). Alternatively, another study has shown the Bobcat will expand its use of different environmental features and use of marginal habitat in the presence of Canada Lynx (Peers et al. 2013).
Ferguson et al. (2009) gathered home range information from 29 Bobcat populations across the US and found that on average, males maintained home ranges 1.65 times the size of females. Female home ranges were 0.989–42.7 km² with a mean of 15.83 km² compared to male home ranges of 2.86– 167.9 km² with a mean of 39.70 km². Females demonstrated a strong positive association between home-range size and productivity (i.e. food availability), whereas males were influenced more by changes in size of female home ranges than by resource availability (Ferguson et al. 2009, Sandell 1989).
|Use and Trade:||For information on use and trade , see under Threats.|
World demand for Bobcat fur rose gradually in the late 1960s and early 1970s and jumped in the mid-1970s after CITES entered into force, when the pelts of cats listed on Appendix I became legally unobtainable for the commercial fur trade (Nowell and Jackson 1996). Of particular and concern is the recent increase in Bobcat pelt prices from $85 in 2000, to record highs of $589 in 2013, $447 in 2014, and $305 in 2015, driven by high demand for fur in China, Europe, and Russia (Knudson 2016). The number of Bobcat pelts exported from the U.S. has quadrupled in recent years, climbing to a high of 65,000 in 2013 when pelt prices were highest.
The US government has found that trade is not detrimental to Bobcat survival and is well-managed by state authorities. They have petitioned CITES numerous times, most recently in 2007, to remove the Bobcat from the CITES Appendices, arguing that the Bobcat does not meet the biological criteria for CITES listing and that their research indicates that importing governments should be able to reliably distinguish Bobcat skins from other species to prevent illegal trade (Govt of US 2007). However, the proposal was rejected by majority vote of the Parties to CITES (Nowell et al. 2007).
Habitat loss is viewed as another primary threat to bobcats in all three range countries. Increasing urbanization results in direct habitat loss when human density is high, although Bobcats have proven to be fairly adaptive to urbanization (Ordenana et al. 2010, Tracey et al. 2013 ) and low density developments (one house per two acres), particularly in areas with landscaped green spaces and golf courses, and Bobcats have been documented denning and raising litters in human structures (Riley et al. 2010). However, as Bobcats adjust to human developed landscapes, indirect effects increase. Vehicle collisions can be a primary source of mortality in urban Bobcat populations (Riley et al. 2006) and in populations with a high proportion of transients (Blankenship et al. 2006). In addition, exposure to common rodenticides in urban landscapes can result in direct mortality (anticoagulant toxicosis) and increased susceptibility to severe notoedric mange resulting in the death of Bobcats (Riley 1999, Riley et al. 2003, Riley et al. 2006, Riley et al. 2007, Ruell et al. 2009, Serieys et al. 2013). Increases in urbanization and roads have also resulted in recent genetic isolation of Bobcats populations in several areas, indicating human developments are affecting historic dispersal patterns and gene flow, resulting in local and regional population structure (Riley et al. 2003, Croteau et al. 2012, Ruell et al. 2012, but see Millions and Swanson 2007).
There is concern in the northeastern US about interspecific competition with expanding coyote populations (Moruzzi et al. 2002, Litvaitis and Harrison 1989, Litvaitis et al. 2006). However, in Florida, where Coyotes have also increased, Thornton et al. (2004) found that Bobcats and Coyotes favoured different prey species, with coyotes taking larger ungulates and Bobcats rodents and smaller mammals, and Coyotes and Bobcats coexist throughout most of the western portions of their ranges, likely through niche shifts in diet and activity (Fedriani et al. 2000). Bobcats coexist with Ocelots in Texas (Horne et al. 2009) and Canada Lynx in zones of sympatry (Peers et al. 2013) through habitat partitioning. Aside from exploitative competition, there is evidence of interference competition through intraspecific killing by Mountain Lions (Haas 2009) and hybridization has been detected with few federally threatened Canada Lynx (Lynx canadensis) in Maine, Minnesota, and New Brunswick (Homyack et al. 2008). In addition, increased or novel sources of depredation in have been documented in several areas. Bobcat observations in southern Florida have decreased dramatically as invasive python densities have increased (Dorcas et al. 2012). In Ventura County, California, Coyotes were found to be the leading source of Bobcat kitten mortality (Moriarty 2007), although this increase in predation pressure is likely a result of reduced avoidance options in highly fragmented urban habitat (Riley et al. 2003). Interactions with domestic dogs may also present threats to the Bobcat population. Canine distemper and canine distemper-associated encephalitis has been documented in Bobcats in eastern Canada (Daoust et al. 2009) validating the proposed role of dogs as a pathogen-mediated apparent competitor with Bobcats (Vanek and Gompper 2009), and several studies demonstrate negative correlation between domestic dog activity and Bobcat activity (George and Crooks 2006, Reed and Merenlender 2011).
In localized areas Bobcats take domestic livestock and are persecuted as pests (Sunquist and Sunquist 2002). In addition, there have been recent concerns about the effects of harvest on local Bobcat populations in West Virginia (WV-DNR), and Michigan (Preuss and Gehring 2007) and poaching may result in higher harvest rates than anticipated in some areas (Millions and Swanson 2006), which can result in population declines as it has in New Hampshire (Litviatus et al. 2006). However, there is evidence from a survey of state game management agencies that Bobcat populations are stable or increasing, with densities greater than initially estimated, in all US states with the exception of Florida (Roberts and Crimmins 2010).
Included on CITES Appendix II. The Mexican subspecies Lynx rufus escuinapae was listed on CITES Appendix I until 1992, when it was downlisted to Appendix II on the grounds that it is not a valid taxon (Govt of US 2007). Bobcats are legally harvested for the fur trade in 38 US states, and in seven Canadian provinces. In Mexico, the Bobcat is legally hunted in small numbers as a trophy animal (Govt of US 2007). There appears to be little illegal international trade (Govt of US 2007), although within the US, Millions and Swanson (2006) used molecular forensics techniques to determine that skins reported as originating from an area with a higher bag limit were probably illegally taken from an area with a lower limit.
Bobcat status in the mid-western United States has improved since their extirpation in the early 1900s. In Iowa, Bobcats were downgraded to threatened in 2001 and are now harvested in many counties. In Illinois, Bobcats were removed from the states’ list of threatened in 1999 and they are now found in nearly all counties. Indiana has sightings in much of the state and Bobcats were downgraded to special concern in 2005. In Ohio, the Bobcat is still classified as an endangered species and provided full protection.
Reintroduction of Bobcats to Cumberland Island, Georgia was highly successful (Diefebach et al. 2013) suggesting Bobcats can do well when protected. In addition, Kapfer and Potts (2012) found Bobcat harvest in Minnesota could be predicted by season length and suggest population densities can be manipulated by change in length of hunting season.
Alonso, R.S., McClintock, B.T., Lyren, L.M., Boydson, E.E. and Crooks, K.R. 2015. Mark-Recapture and Mark-Resight Methods for Estimating Abundance with Remote Cameras: A Carnivore Case Study. PLoS ONE 10(3): e0123032.
Arzate, C. N. M., Martinez, A. R., Sierra, R. G. and Lopez-Gonzales, C. A. 2007. Spatial ecology and abundance of Mexican bobcats in northwestern Mexico to assess its conservation status. In: J. Hughes and R. Mercer (eds), Felid biology and conservation conference 17-20 September: Abstracts, pp. 119. WildCRU, Oxford.
Blankenship, T.L., Haines, A.M., Tewes, M.E. and N.J. Silvy. 2006. Comparing survival and cause-specific mortality between resident and transient bobcats Lynx rufus. Wildlife Biology 12: 297-303.
Broman,D.J.A., Litvaitis ,J.A., Ellingwood, M., Tate, P. and Reed, G.C. 2014. Modeling bobcat Lynx rufus habitat associations using telemetry locations and citizen-scientist observations: are the results comparable? Wildlife Biology 20: 229–237.
Burton, A. M., Navarro Perez, S. and Chavez Tovar, C. 2003. Bobcat ranging behavior in relation to small mammal abundance on Colima Volcano, Mexico. Anales del Instituto de Biolog┬ía, Universidad Nacional Auton┬óma de MΓÇÜxico, Serie Zoolog┬ía 74(1): 67.
Croteau, E.K., Heist, E.J., Nielsen, C.K., Hutchinson, J.R. and Hellgren, E.C. 2012. Microsatellites and mitochondrial DNA reveal regional population structure in bobcats (Lynx rufus) of North America. Conservation Genetics 13: 1637-1651.
Daoust, P-Y., McBurney, S.R., Godson, D.L., van de Bildt, M.W.G. and Osterhaus, A.D.M.E. 2009. Canine distemper virus–associated encephalitis in free-living lynx (Lynx canadensis) and bobcats (Lynx rufus) of eastern Canada. Journal of Wildlife Diseases 45: 611–624.
Diefenbach, D.R., Hansen, L.A., Miller-Butterworth, C., Bohling, J.H., Warren, R.J. and Conroy, M.J. 2013. Re-introduction of bobcats to Cumberland Island, Georgia, USA: status and lessons learned after 25 years. In: Soorae, P.S. (ed.), IUCN/SSC Re-introduction Specialist Group and Environment Agency, pp. 235-240. Abu Dhabi.
Donovan, T.M., Freeman, M., Abouelezz, H., Royar, K., Howard, A. and Mickey, R. 2011. Quantifying home range habitat requirements for bobcats (Lynx rufus) in Vermont, USA. Biological Conservation 144: 2799-2809.
Dorcas, M.E., Wilson, J.D., Reed, R.N., Snow, R.W., Rochford, M.R., Miller, M.A., Mesheka Jr., W.E., Andreadis, P.T., Mazzotti, F.J., Romagosa, C.M. and Hart, K.M. 2012. Severe mammal declines coincide with proliferation of invasive Burmese pythons in Everglades National Park. Proceedings of the National Academy of Sciences 109(7): 2418-2422.
Fedriani, J.M., Fuller, T.K., Sauvajot, R.M. and York, E.C. 2000. Diets of three sympatric carnivores in the Santa Monica Mountains of California: the importance of habitat, human presence and interspecific competition. Oecologia 125: 258-270.
Ferguson, A.W., Currit, N.A. and Weckerly, F.W. 2009. Isometric scaling in home-range size of male and female bobcats (Lynx rufus). Canadian Journal of Zoology 87: 1052-1060.
George, S.L. and Crooks, K.R. 2006. Recreation and large mammal activity in an urban nature reserve. Biological Conservation 133: 107-117.
González-Salazar, C., Stephens, C.R. and P.A. Marquet. 2013. Comparing the relative contributions of biotic and abiotic factors as mediators of species’ distributions. Ecological Modelling 248: 57-70.
Government of US. 2007. Proposal for deletion of Lynx rufus from Appendix II. COP14 Prop 2. CITES, The Hague.
Hass, C.C. 2009. Competition and coexistence in sympatric bobcats and pumas. Journal of Zoology 278: 174-180.
Heilbrun, R. D., Silvy, N. J., Peterson, M. J. and Tewes, M. E. 2006. Estimating bobcat abundance using automatically triggered cameras. Wildlife Society Bulletin 12: 328.
Homyack, J., Vashon, J.H., Libby, C., Lindquist, E.L., Loch, S., McAlpine, D.F., Pilgrim, K.L. and Schwartz, M.K. 2008. Canada lynx-bobcat (Lynx canadensis x L. rufus) hybrids at the southern periphery of lynx range in Maine, Minnesota, and New Brunswick. American Midland Naturalist 159: 504-508.
Horne, J.S., Haines, A.M., Tewes, M.E. and Laack, L.L. 2009. Habitat partitioning by sympatric ocelots and bobcats: Implications for recovery of ocelots in southern Texas. The Southwestern Naturalist 54: 119-126.
Hunter, L. 2015. Wild Cats of the World. Bloomsbury Publishing. New York.
IUCN. 2016. The IUCN Red List of Threatened Species. Version 2016-1. Available at: www.iucnredlist.org. (Accessed: 30 June 2016).
Johnson, W.E., Eizirik, E., Pecon-Slattery, J., Murphy, W.J., Antunes, A., Teeling, E. and O'Brien, S.J. 2006. The late Miocene radiation of modern Felidae: A genetic assessment. Science 311: 73-77.
Kapfer, P.M. and Potts, K.B. 2012. Socioeconomic and ecological correlates of bobcat harvest in Minnesota. The Journal of Wildlife Management 76: 237-242.
Kelly, M.J. and Holub, E.L. 2008. Camera trapping of carnivores: trap success among camera types and across species, and habitat selection by species, on Salt Pond Mountain, Giles County, Virginia. Northeastern Naturalist 15: 249-262.
Knick, S. T. 1990. Ecology of bobcats relative to exploitation and a prey decline in southeastern Idaho. Wildlife Monographs 108: 1-42.
Knudson, T. 2016. America’s trapping boom relies on cruel and grisley tools. Available at: https://www.revealnews.org/article/americas-trapping-boom-relies-on-cruel-and-grisly-tools/.
Lariviére, S. and Walton, L.R. 1997. Lynx rufus. Mammalian Species 563: 1-8.
Lawhead, D. N. 1984. Bobcat Lynx rufus home range density and habitat preference in south central Arizona USA. 29(1): 105.
Litvaitis, J. A. and Harrison, D. J. 1989. Bobcat-coyote niche relationships during a period of coyote population increase. Canadian Journal of Zoology 67: 1180-1188.
Litvaitis, J. A., Tash, J. P. and Stevens, C. L. 2006. The rise and fall of bobcat populations in New Hampshire: Relevance of historical harvests to understanding current patterns of abundance and distribution. Biological Conservation 128: 517-528.
Lobo, N. and J.S. Millar. 2010. Photographic Evidence of Bobcats, Lynx rufus, in the Kananaskis Valley in Southwestern Alberta. Canadian Field-Naturalist 124: 260-262.
Millions, D. G. and Swanson, B. J. 2006. An application of Manel's model: Detecting bobcat poaching in Michigan. Wildlife Society Bulletin 34: 150-155.
Millions, D.G. and Swanson, B.J. 2007. Impact of natural and artificial barriers to dispersal on the population structure of bobcats. Journal of Wildlife Management 71: 96-102.
Monroy-Vilchis, O. and Velazquez, A. 2003. Regional distribution and abundance of bobcats (Lynx rufus escuinape) and coyotes (Canis latrans cagottis), as measured by scent stations: a spatial approach. CienciasNaturales y Agropecuarias 9: 293-300.
Montague, D.M. 2014. Diet and Feeding Ecology of the Coyotes, Black Bears, and Bobcats in Western Virginia, and Preliminary Assessment of Coyote Parasites. Virginia Tech, Masters Thesis.
Moriarty, J.G. 2007. Female bobcat reproductive behavior and kitten survival in an urban fragmented landscape. Master’s Thesis. California State University, Northridge.
Morin, D.J., Higdon, S.D., Holub, J.L., Montague, D.M., Fies, M.L., Waits, L.P. and Kelly, M.J. Submitted. Bias in carnivore diet analysis resulting from misclassification of predator scats based on field identification. Wildlife Society Bulletin.
Moruzzi, T. L., Fuller, T. K., Degraaf, R. M., Brooks, R. T. and Li, W. 2002. Assessing remotely triggered cameras for surveying carnivore distribution. Wildlife Society Bulletin 30: 380-386.
Nowell, K. and Jackson, P. 1996. Wild Cats. Status Survey and Conservation Action Plan. IUCN/SSC Cat Specialist Group, Gland, Switzerland and Cambridge, UK.
Nowell, K., Bauer, H. and Breitenmoser, U. 2007. Cats at CITES COP14. Cat News 47: 33-34.
Ordenana, M.A., Crooks, K.R., Boydston, E.E., Fisher, R.N., Lyren, L.M., Siudyla, S., Haas, C.D., Harris, S., Hathaway, S.A., Turschak, G.M., Miles, A.K. and Van Vuren, D.H. 2010. Effects of urbanization on carnivore species distribution and richness. Journal of Mammalogy 91: 1322-1331.
Peers, M.J.L., Thornton, D.H. and Murray, D.L. 2013. Evidence for large-scale effects of competition: niche displacement in Canada lynx and bobcat. Proceedings Royal Society B 280: 1-10.
Preuss, T.S. and Gehring, T.M. 2007. Landscape analysis of bobcat habitat in the northern lower peninsula of Michigan. Journal of Wildlife Management 71: 2699-2706.
Reding, D.M., Cushman, S.A., Gosselink, T.E. and Clark, W.R. 2013. Linking movement behavior and fine-scale genetic structure to model landscape connectivity for bobcats (Lynx rufus). Landscape Ecology 28: 471-486.
Reed, S.E. and Merenlender, A.M. 2011. Effects of management of domestic dogs and recreation on carnivores in protected areas in northern California. Conservation Biology 25: 504-513.
Riley, S.P.D. 1999. Spatial organization, food habits and disease ecology of bobcats (Lynx rufus) and gray foxes (Urocyon cinereoargenteus) in National Park areas in urban and rural Marin County, California. Dissertation, University of California.
Riley S.P.D., Boydston, E.E., Crooks, K.R. and Lyren, L.M. 2010. Bobcats (Lynx rufus). In: S.D. Gehrt, S.P.D. Riley and B.L. Cypher (eds), Urban Carnivores: Ecology, Conflict, and Conservation, pp. 121-140. The Johns Hopkins Univeristy Press, Baltimore, MD.
Riley, S.P.D., Bromley, C., Poppenga, R.H., Uzal, F.A., Whited, L. and Sauvajot, R.M. 2007. Anticoagulant exposure and notoedric mange in bobcats and mountain lions in urban southern California. Journal of Wildlife Management 71: 1874-1884.
Riley, S.P.D., Pollinger, Sauvajot, R.M., York, E.C., Bromle, C., Fuller, T.K. and Wayne, R.K. 2006. A southern California freeway is a physical and social barrier to gene flow in carnivores. Molecular Ecology 15: 1733-1741.
Riley, S.P.D., Sauvajot, R.M., Fuller, T.K., York, E.C., Kamradt, D.A., Bromley, C. and Wayne, R.K. 2003. Effects of urbanization and habitat fragmentation on bobcats and coyotes in southern California. Conservation Biology 17: 566-576.
Roberts, N.M. and Crimmins, S.M. 2010. Bobcat population status and management in North America: evidence of large-scale population increase. Journal of Fish and Wildlife Management 1: 169-174.
Ruell, E.W., Riley, S.P.D., Douglas, M.R., Antolin, M.F., Pollinger, J.R., Tracey, J.A., Lyren, L.M., Boydston, E.E., Fisher, R.N. and Crooks, K.R. 2012. Urban habitat fragmentation and genetic population structure of bobcats in coastal southern California. 168: 265-280.
Ruell, E.W., Riley, S.P.D., Douglas, M.R., Pollinger, J.R. and Crooks, K.R. 2009. Estimating bobcat population sizes and densities in a fragmented urban landscape using noninvasive capture–recapture sampling. Journal of Mammalogy 90: 129-135.
Sánchez-Cordero, V., Stockwell, D., Sarkar, S., Liu, H., Stephens, C.R. and Giménez, J. 2008. Competitive interactions between felid species may limit the southern distribution of bobcats Lynx rufus. Ecography 31: 757-764.
Sandell, M. 1989. The mating tactics and spacing patterns of solitary carnivores. In: Gittleman, J.L. (ed.), Carnivore Behavior, Ecology and Evolution, pp. Cornell University Press. Ithaca NY.
Serieys, L.E.K., Foley, J., Owens, S., Woods, L., Boydston, E.E., Lyren, L.M., Poppenga, R.H., Clifford, D.L., Stephenson, N., Rudd, J. and Riley, S.P.D. 2013. Serum chemistry, hematologic, and post-mortem findings in free-ranging bobcats (Lynx rufus) with notoedric mange. Journal of Parasitology 99: 989-996.
Sunquist, M. and Sunquist, F. 2002. Wild Cats of the World. University of Chicago Press.
Thornton, D.H, and Perkins, C.E. 2015. Spatially explicit capture–recapture analysis of bobcat (Lynx rufus) density: implications for mesocarnivore monitoring. Wildlife Research 42: 394-404.
Thornton, D. H., Sunquist, M. E. and Main, M. B. 2004. Ecological separation within newly sympatric populations of coyotes and bobcats in south-central Florida. Journal of Mammalogy 85: 973-982.
Tracey, J.A., Zhu, J., Boydson, E., Lyren, L., Fisher, R.N. and Crooks, K.R. 2013. Mapping behavioral landscapes for animal movement: a finite mixture modeling approach. Ecological Applications 23: 654-669.
Tucker, S.A., Clark, W.R. and Gosselink, T.E. 2008. Space use and habitat selection by bobcats in the fragmented landscape of south-central Iowa. Journal of Wildlife Management 72: 1114-1124.
Vanak, A.T. and Gompper, M.E. 2009. Dogs Canis familiaris as carnivores: their role and function in intraguild competition. Mammal Review 39: 265-283.
|Citation:||Kelly, M., Morin, D. & Lopez-Gonzalez, C.A. 2016. Lynx rufus. The IUCN Red List of Threatened Species 2016: e.T12521A50655874.Downloaded on 28 February 2017.|
|Feedback:||If you see any errors or have any questions or suggestions on what is shown on this page, please provide us with feedback so that we can correct or extend the information provided|