Ursus thibetanus 

Scope: Global
Language: English

Translate page into:

Taxonomy [top]

Kingdom Phylum Class Order Family
Animalia Chordata Mammalia Carnivora Ursidae

Scientific Name: Ursus thibetanus G. [Baron] Cuvier, 1823
Common Name(s):
English Asiatic Black Bear, Himalayan Black Bear
French Ours à collier, Ours de l'Himalaya, Ours du Tibet, Ours noir d'Asie
Spanish Oso de Collar, Oso Negro de Asia
Taxonomic Notes:

Seven subspecies have been recognized, many of which have been corroborated as distinct genetic clades (Kim et al. 2011, Yusefi 2013, Wu et al. 2015).

This species was previously included in the genus Selenarctos (meaning moon bear). The principal colour phase is black, with a white or cream/yellow “crescent moon” on the chest. Rare brown phases are also known, and a rare blond colour phase was discovered in Cambodia, Thailand, and Lao People’s Democratic Republic (Galbreath et al. 2000). One case of a wild Asiatic Black Bear–Sun Bear (Helarctos malayanus) hybrid has been reported in Cambodia (Galbreath et al. 2008).

Assessment Information [top]

Red List Category & Criteria: Vulnerable A2cd ver 3.1
Year Published: 2016
Date Assessed: 2016-03-17
Assessor(s): Garshelis, D. & Steinmetz, R.
Reviewer(s): Obbard, M. & McLellan, B.
Contributor(s): LaBruna, D., Abbas, F., Bendixsen, T., Broadis, N., Choudhury, A., Fahimi, H., Galbreath, G., Ghadirian, T., Hameed, S., Htun, S., Hwang, M., Islam, M., Jeong, D., Khan, M., Koike, S., Liu, F., Long, B., Ngoprasert, D., Oi, T., Olsson, A., Robinson, J., Sathyakumar, S., Scotson, L., Seryodkin, I., Shepherd, C., Wangchuk, S., Yadav, B., Yamazaki, K. & Yusefi, G.

Widespread illegal killing of bears and trade in parts, combined with loss of habitat indicate that this species is likely declining in most parts of its range. Country bear experts on the IUCN SSC Bear Specialist Group (representing all range countries except the Democratic People's Republic of Korea) estimated rates of population change for the past 30 years (three bear generations), and projected rates of change for the next 30 years (see Figure 2 in the attached Supplementary Material). These assessments were based on perceived levels of exploitation, loss and degradation of habitat, and changes in area of occupancy within their respective countries; no range countries have estimates of abundance or indices of abundance that are sufficient to document population trend. One country (Pakistan) obtained empirical estimates of a decline in occupancy of 33% in 30-40 years (Abbas et al. 2015).

Weighting each country’s estimate of population change by the country’s areal proportion of the geographic range yielded an overall estimated decline of 31% for the past 30 years.  All countries that reported population declines also reported that these declines have not ceased. Thus, this species meets the criteria for Vulnerable. Projected decline was less (20-30%) for a 30-year window over-lapping the present, and for 30 years into the future.

Estimates of population change for China have a very large influence on range-wide estimates because China comprises more than half the total range area. Forest area for China is increasing, but much of this reforestation is poor habitat for Asiatic Black Bears. Moreover, poaching levels are still reported to be high. Past trends in China were gleaned mainly from an extensive sign survey of occupied area combined with reports by local people in Sichuan Province, which is believed to harbour the largest numbers of Asiatic Black Bears. Projections into the future, though, are highly speculative, especially given uncertainty about future poaching pressure in China, which is largely motivated by bear bile, and may change with marketing of synthetically produced bile. Excluding China, the range-wide estimated rate of decline for the 30-year window including the present averages ~30%, and the projected rate for the next 30 years was 40%, indicating that the outlook for this species is getting worse in most of these other range countries.

For further information about this species, see 22824_Ursus_thibetanus.pdf.
A PDF viewer such as Adobe Reader is required.
Previously published Red List assessments:

Geographic Range [top]

Range Description:

Fossil remains of the Asiatic Black Bear have been found in various sites in Europe, as far north as the Ural Mountains and Germany and west to France, dating from the early Pliocene to late Pleistocene (Erdbrink 1953, Kosintsev 2007, Baryshnikov and Zakharov 2013, Fourvel et al. 2014); however, in historic times the species has been limited to Asia. The western range limit is in southeastern Iran, inhabited by the so-called Baluchistan bear (U. t. gedrosianus) (Ahmadzadeh et al. 2008, Ghadirian et al. 2012). This small population is likely connected to the Baluchistan bear population in southern Pakistan. Disjunct populations of Asiatic Black Bears also occur in the more mountainous regions of northern Pakistan (Khan et al. 2012) and Afghanistan (Ostrowski et al. 2009). Eastward they continue within a narrow band along the foothills and south side of the Himalayas (up to treeline) across India, Nepal, and Bhutan, and then more widely distributed at lower elevations (generally >70 m but occasionally to 20 m) in the hill states of northeastern India (Sathyakumar and Choudhury 2007). They occur across mainland Southeast Asia, stretching south in Myanmar and Thailand to ~200 km north of the Malaysian border (Kanchanasakha et al. 2010); there are no records of Asiatic Black Bears ever existing in Malaysia. Over half the total range area of this species exists in China, especially in the south-central and southwestern parts of the country. This distribution includes portions of Tibet, from which the specific name, thibetanus, is derived. Smaller, remnant populations occur in eastern China. Another population cluster exists in northeastern China, the southern Russian Far East, and North Korea. A small isolated population exists in southern South Korea. They also live on the southern islands of Japan (Honshu and Shikoku) and on Taiwan and Hainan. Although they have been extirpated from large portions of their range, they remain in all 18 historic range countries.

The distribution of the Asiatic Black Bear roughly coincides with forest distribution in southern and eastern Asia (FAO 2010), except that in central and southern India this species is replaced by the Sloth Bear (Melursus ursinus), in Malaysia it is replaced by the Sun Bear and north and west of the Russian Far East it is replaced by the Brown Bear (Ursus arctos). However, the Asiatic Black Bear overlaps the ranges of each of these species, especially the Sun Bear in a large portion of Southeast Asia and small portions of northeast India. It also greatly overlaps the range of Giant Pandas (Ailuropoda melanoleuca) in south-central China. In Afghanistan, Pakistan, and India, the Asiatic Black Bear range overlaps the Brown Bear (at elevations >3,000 m) in the Himalayas (but curiously, does not appear to overlap Brown Bears in Nepal (A. Aryal, Massey University, New Zealand, pers. comm, 2016; Bista and Aryal 2013). It also overlaps Brown Bears in south-central and northeastern China, North Korea, and the Russian Far East. In India, Asiatic Black Bear range overlaps the Sloth Bear at low elevations (<1,000 m) in some protected areas including Corbett Tiger Reserve and Rajaji National Parks, Uttarakhand (Bargali 2012). However, there is no evidence of overlap with Sloth Bears in neighbouring Nepal (Garshelis et al. 1999). In North Karbi Anglong wildlife sanctuary in Assam, northeast India, Asiatic Black Bear range overlaps both Sloth Bears and Sun Bears—one of the few places in the world where all three of these species coexist, although all are reported to be rare (Choudhury 2011, Choudhury and Chand 2012).

Countries occurrence:
Afghanistan; Bangladesh; Bhutan; Cambodia; China; India; Iran, Islamic Republic of; Japan; Korea, Democratic People's Republic of; Korea, Republic of; Lao People's Democratic Republic; Myanmar; Nepal; Pakistan; Russian Federation; Taiwan, Province of China; Thailand; Viet Nam
Additional data:
Upper elevation limit (metres):4300
Range Map:Click here to open the map viewer and explore range.

Population [top]


The only rigorous population estimates for this species have been produced in Thailand, based on mark–recapture with camera traps, using distinctive chest patterns (Ngoprasert et al 2010; Higashide et al. 2012, 2013) to identify individual bears. This work yielded density estimates in three study sites in Khao Yai National Park, ranging from 8-29 bears per 100 km² (Ngoprasert et al. 2012, 2013). Bear sign density was found to be correlated with estimates of bear density, so sign surveys conducted across the country may, in the future, yield a reasonably reliable country-wide population index and trend information.

In the Lower Dachigam area of Dachigam National Park and surrounding agricultural landscapes in Kashmir, India, genetic analysis of hair samples revealed the presence of 109 unique individuals in an area of 650 km², or17 bears per 100 km² (Mukesh et al. 2015). Notably, this is a particularly food-rich area.

Others have used a variety of ad hoc procedures to generate rough country-wide estimates. Largest populations occur in China (government estimate: ~28,000; Gong and Harris 2006), Japan (government estimate: 12,000-19,000, with much wider confidence intervals; Ministry of the Environment 2011), India (5,000-7,000; Sathyakumar and Choudhury 2007), and Russia (5,000-7,000; Aramilev 2006). Although these country-wide estimates are large, small, isolated populations also exist. For example, Japan has one large metapopulation as well as a few, disjunct small populations (Horino and Miura 2000, Yamamoto et al. 2012). Northern Pakistan may contain as many as nine separate populations (Abbas et al. 2015). Thailand has a number of small populations inside protected areas, separated by expanses of agriculture (Kanchanasakha et al. 2010).

Countries with the smallest total numbers of Asiatic Black Bears are Iran (~100-200) and South Korea. Iran’s population has a relatively wide but disconnected distribution and occurs at very low density, due to the scarcity of suitable habitat. This population’s low genetic diversity and distinct genetic clade indicate that it has been small and disjunct for a long time (Yusefi 2013). South Korea’s population was nearly extirpated, but saved by a reintroduction program in Jirisan National Park, started in 2004 (Jeong et al. 2011). All of the reintroduced animals were radio-collared, so their fate is known.  It is believed that there were about 40 bears in the Republic of Korea population in 2015.

Population trend has been deduced from sign, interviews, changes in habitat, and evidence of poaching. Republic of Korea and Japan report stable to increasing populations, Bhutan and Thailand report stable populations, and India reports stable to declining populations. All other countries report probable declining numbers (no report from Democratic People's Republic of Korea). The most severe declines, estimated at >60% in the past 30 years, were reported in Viet Nam and Bangladesh. However, Asiatic Black Bears have fared better than Bangladesh’s other native bear species, which have been extirpated (Sloth Bears) or nearly extirpated (Sun Bears) due to severe habitat deterioration (Islam et al. 2013). Likewise, Sun Bears have disappeared from the only portion of their range in China (Yunnan province), whereas Asiatic Black Bears still remain there (Wen and Wang 2013).

For further information about this species, see 22824_Ursus_thibetanus.pdf.
A PDF viewer such as Adobe Reader is required.
Current Population Trend:Decreasing
Additional data:
Population severely fragmented:No

Habitat and Ecology [top]

Habitat and Ecology:

Asiatic Black Bears occupy a variety of forested habitats, both broad-leaved and coniferous, from near sea level to an elevation of 4,300 m (in northeastern India and Sikkim; Sathyakumar and Choudhury 2007, Sathyakumar et al. 2011). They also infrequently use open alpine meadows. A photo-capture was made in the alpine region of Nanda Devi Biosphere Reserve, Uttarakhand, India at 4,500 m (>1,000 m above the mean tree line; S. Sathyakumar, Wildlife Institute of India, pers. comm., 2014). In some areas of Nepal, local people have reported Asiatic Black Bears at higher than normal elevations, possibly a result of climate change (Aryal et al. 2012).

Individual bears move to different habitats and elevations seasonally (Izumiyama and Shiraishi 2004, Hwang et al. 2010), tracking changes in food abundance. In seasonal climates, foods include succulent vegetation (shoots, forbs and leaves) in spring, turning to insects and a variety of tree and shrub-borne fruits in summer, and hard mast (nuts) in autumn (Bromlei 1965, Reid et al. 1991, Hashimoto 2002, Hwang et al. 2002, Huygens et al. 2003, Koike 2010). In the tropics and subtropics, fruits are the mainstay year-round (Steinmetz et al. 2013). The diet may vary year to year with differences in food availability (Koike 2010), and this opportunistic species appears to be able to adapt its diet to gradually changing habitat conditions (Koike et al. 2013). In some places the diet includes a sizeable portion of meat from wild mammalian ungulates (which they either kill or scavenge, including tiger kills; Hwang et al. 2002, Seryodkin et al. 2005, Narita et al. 2006), livestock (Abbas et al. 2015), ants (which they may forage upon for 7-8 hours per day; Yamazaki et al. 2012), or bees (Hashimoto 2002).

Asiatic Black Bears also use regenerating forests, which may have a high production of berries or young bamboo shoots (Takahata et al. 2014). They also feed in plantations, where they may damage trees by stripping the bark and eating cambium (Yamazaki 2003, Yamada and Fujioka 2010), and in cultivated areas, especially corn and oat fields and fruit orchards (Carr et al. 2002, Mizukami et al. 2005, Gong and Harris 2006, Abbas et al. 2015, Mukesh et al. 2015).

In southeastern Iran and Pakistan, this species occupies a very dry, sparsely-forested landscape (often called steppe forest or steppe woodland). This is the driest landscape inhabited by this species. Bears here use riparian areas, abandoned groves of date palm, and wild olive and pistachio forests (Ahmadzadeh et al. 2008, Ghadirian et al. 2012a). In some parts of this region, access to anthropogenic foods, particularly orchards (e.g., date palm, apricots, figs, walnuts), enable them to persist in a habitat with scarce natural food (Ghadirian 2012b). They use rock caves as shelters during daytime, and feed at night, possibly to avoid the sun or encounters with people in this very exposed habitat (Fahimi et al. 2011).  By contrast, in more forested parts of the species’ range, they tend to be diurnally active (Hwang and Garshelis 2007) or crepuscular (Sharma et al. 2010).

Asiatic Black Bears feed on a wide array of fleshy fruits and nuts. They were observed to feed on fruits from over 30 species of woody plants within a small, mountainous study site in Japan (Koike 2009). An equal dietary diversity was observed in a mountainous site in northern India (Sharma et al. 2014). In tropical Thailand, dietary diversity was even greater: they were found to feed on fruits from least 30 families of trees (Steinmetz et al. 2013).

Fruiting tree density is a good predictor of the occurrence and relative density of Asiatic Black Bears (Ngoprasert et al. 2011, Steinmetz et al. 2011). In Thailand, these bears were noted to seek out rare fruits in the forest, possibly to diversify their diet (Steinmetz et al. 2013). Asiatic Black Bears are likely an important disperser of the seeds of some fleshy fruits (Sathyakumar and Viswanath 2003; Koike et al. 2008, 2010). They climb trees to eat fruits, and also eat fruits that drop to the ground. Sympatric Sun Bears also eat these same fruits. In Thailand, both species commonly feed on fruits in the cinnamon (Lauraceae) and pea (Fabaceae or Leguminosae) families.  Both species live together in lowland habitats (<1,200 m), but Asiatic black bears predominate at higher elevations (Steinmetz et al. 2011).

In temperate forests, Asiatic Black Bears rely heavily on hard mast in autumn, in part to attain sufficient fat reserves for winter denning (hibernation).  Therefore, these bears tend to focus their activities in habitats with high abundance of oak acorns, beechnuts, walnuts, chestnuts, hazelnuts, or stone pine seeds (Schaller et al. 1989, Reid et al. 1991, Hwang et al. 2002, Hashimoto et al. 2003, Huygens et al. 2003). When Asiatic Black Bears feed in hard mast trees they often break branches and pile them up in the canopy, forming what appears to be a platform or “nest”. Males may socially exclude females, juvenile bears, and Sun Bars from rich stands of hard mast (Huygens and Hayashi 2001, Hwang et al. 2010, Steinmetz et al. 2011, Koike et al. 2012). When hard mast is poor, these bears expand their home ranges to find alternate fall foods (Hwang et al. 2010, Kozakai et al. 2011, Koike et al. 2012). In Japan, hard mast failures have led to massive intrusions of bears into residential areas, where they seek anthropogenic foods as a substitute (Oka et al. 2004, Oi and Furusawa 2008).

In northern latitudes, where food becomes unavailable in winter, or in high altitudes covered by snow, both sexes hibernate. Therefore, Asiatic Black Bears hibernate throughout their range in Russia, Korea, Japan and northeastern China, and in high elevation areas of more southerly range states. Bears enter dens as early as October and as late as late-December; when hard mast is poor, den entry is earlier (Kozakai et al. 2013). They exit dens as early as mid-March to as late as the end of May (Seryodkin et al. 2003, Koike and Hazumi 2008). They den in rock crevices, hollow trees or stumps, under upturned trees, in dug-out earthen dens, natural cavities under roots, or in ground nests. In a mature natural forest in Japan, they were reported denning inside hollow trees, with entrances above ground level (Hazumi et al. 2001). In Russia, Asiatic Black Bears selected flat river bottoms for denning (Seryodkin et al. 2003), whereas in central China they moved to high elevation rocky outcrops on steep slopes (Reid et al. 1991).  Likewise in Japan, dens tended to be in remote, difficult to access mountainous areas (Huygens et al. 2001, Koike and Hazumi 2008). Hunters often have knowledge of the sorts of places and types of dens that the bears tend to use, and have been reported finding and killing bears in dens. Denning and active Asiatic Black Bears are also subject to predation by other Asiatic Black Bears, Brown Bears, and Tigers (Seryodkin et al. 2005).

Asiatic Black Bears do not hibernate from the Himalayan foothills southward where food is available all year and not covered by snow. However, pregnant females den throughout the range (even where food is available and other bears remain active) because they give birth to altricial cubs during the winter (Hwang and Garshelis 2007).

Asiatic Black Bears generally breed during June-July and give birth during November-March; however, timing of reproduction is not known for all portions of the range. Age of first reproduction is typically 4-5 years old, and they normally produce litters of 1 or 2 cubs every other year (at most) (Yamanaka et al. 2011). Maximum lifespan is over 30 years, but average lifespan is less in the wild. No data are available on survival rates or causes of mortality.


Generation Length (years):10

Use and Trade [top]

Use and Trade:

Bear bile has been an important component of traditional medicine in Eastern Asia for millennia. The first written account of such use was recorded in the first pharmacopeia of China in 659 A.D. (Feng et al. 2009). Bear bile is used in Traditional Chinese Medicine (TCM) for reducing fever and inflammation, detoxifying the liver, arresting convulsions, improving eyesight, and dissolving gall stones.

The medicinally active ingredient of bear bile is ursodeoxycholic acid (UDCA). In controlled, clinical trials, this compound (and its associated conjugates) has been shown to have many of the medicinal properties claimed in TCM. In western societies it has been approved as a drug to treat certain liver diseases. More recently it has been shown to prevent retinal degeneration (Boatright et al. 2006), protect against Type I diabetes (Engin et al. 2013), and to have therapeutic effects for a number of neurodegenerative diseases, including amyotrophic lateral sclerosis, Alzheimer’s disease, Parkinson’s disease, and Huntington’s disease (Vang et al. 2014).

Despite the availability of synthesized UDCA, and the widespread use of this product in China, Japan, and South Korea, as well as a large number of herbal alternatives to bear bile in the Chinese pharmacopeia, many TCM practitioners (in Asia and elsewhere) prefer using bear bile because it is thought to be more effective and more natural than synthetic products. Some have claimed that other compounds in bear bile aid in the medicinal functions of UDCA, although no clinical trials have compared the efficacy of bear bile versus synthesized UDCA. Evidence suggests that UDCA in bear bile, which is a potent inhibitor of cell death (apoptosis), may serve to protect bears during hibernation (Solá et al. 2006). Asiatic Black Bears produce high levels of UDCA. Historically, the Asiatic Black Bear has been sought after for its bile more than any other bear species. It is sold in various forms including whole gallbladders, raw bile, pills, powders, flakes, and ointments (Foley et al. 2011).

Increased demand, stemming from burgeoning human populations, coupled with more effective hunting of wild bears and increased ability to sell and transport products has led to the over-exploitation of many Asiatic Black Bear populations, especially in China and Southeast Asia. This trade was further fuelled by an increasing use of bear paws in a high-priced soup (having nothing to do with TCM; Burgess et al. 2014).

In the late 1970s, a technique was developed to extract bile from captive bears without killing them. This practice, called bear bile farming (or bear farming), started in Korea, then spread to China in 1984, and later to Vietnam, and most recently to Lao PDR and Myanmar. In Republic of Korea, Viet Nam, Lao PDR, and Myanmar, bear bile farming is technically illegal. In China, farmed bile is legally sold for use in TCM; it has been argued that this helps to satisfy public demand for bile while reducing the illegal hunting and sale of gall bladders of wild bears.

Bear farming, though, has raised a number of concerns, both about animal welfare and conservation. In Viet Nam, many small-scale bile farms were stocked by thousands of cubs removed from the wild. The condition in which these bears were kept precluded successful breeding and cub rearing. Moreover, although this practice has been illegal since 1992, with regulations strengthened in 2002, the number of wild-caught farmed bears in Viet Nam continually increased, peaking at over 4,000, but declined by over 70% since the mid-2000s with stricter governmental efforts. In part as a result of the decline in farms in Viet Nam, farming operations sprang up in Lao PDR in 2000, and have been increasing rapidly (~120 bears by 2012; Livingstone and Shepherd 2016). Notably, prices of wild bear bile in Lao increased 180x from pre-farming years (1990s) to 2012, suggesting that the availability of farmed bile was actually enticing more users into the market, some of whom were willing to pay considerably more for the wild product (Livingstone and Shepherd 2016). As there is no evidence of breeding of farmed bears anywhere in Southeast Asia, the farms have a negative impact on wild populations both by taking cubs from the wild and by promoting more demand for products of wild bears.

In China, it appears that many bear farms now have active breeding programs. It is unknown what degree of restocking occurs with cubs from the wild, but cases are still reported of people being apprehended with over 20 bear cubs apparently destined for a Chinese bear farm. The biggest unknown issue in China is whether the legal supply of bile has indeed reduced the demand for (illegal) wild bile, and hence reduced poaching of bears, or, as in Lao PDR, has stimulated more demand.

For farming to reduce pressure on wild populations consumers must regard wild and farmed products as similar in quality or value—they must be substitutable (Phelps et al. 2013). In the case of bear bile, interview surveys in both China and Viet Nam show that many consumers regard wild bile as superior to farmed bile, are willing to pay higher prices for it, and are disinclined to use substitutes (Drury et al. 2008, Dutton et al. 2011). Further, the widespread availability of farmed bile may draw more people into the market via more prescriptions by TCM doctors and more promotions by the farming industry; some of these new users may be prompted to use wild bile for some illnesses, considering it to be more potent and pure. Farmed bile has also been promoted (via advertising) for non-medicinal uses, such as general well-being (administered in lotions, shampoos, cosmetics, tonics, etc.) or hangovers, although such uses are technically illegal. Because farmed bile is cheap, some people also use it recreationally (Vu 2010).

Currently there are 67 registered bear farms in China, with an undisclosed number of bears (recently estimated at >17,000). With China’s consent, the World Conservation Congress in 2012 approved an IUCN Recommendation (WCC-2012-Rec-139-EN Bear farming in Asia, with particular reference to the conservation of wild populations) that (1) halts any increase in the number of farms and bears on farms, and (2) calls for a scientifically independent and peer-reviewed “situation analysis” to assess whether bear farming has a positive or negative effect (or no effect) on wild bear populations (Garshelis and Scotson 2012). Meanwhile, the recommendation adopted by the IUCN calls for the other four bear farming countries to phase out bear farming.

All international trade in bile from Asiatic Black Bears, including farmed bile, is illegal under CITES. Despite this, a wide and complex network of international bear bile trading exists, which includes China, Republic of Korea, Japan, Taiwan, and all of the Asiatic black bear range countries in Southeast Asia (Foley et al. 2011).

Threats [top]

Major Threat(s):

Habitat loss due to logging, expansion of agriculture and plantations, roadway networks and dams, combined with hunting for skins, paws and especially gall bladders are the main threats to this species.

Habitat loss due to logging and conversion to agriculture is a major threat to bears in 9 of 18 range countries, including Afghanistan, Bangladesh, Cambodia, India, Lao PDR, Myanmar, Nepal, Pakistan, and Russia. Of these countries, Myanmar stands out as it encompasses a relatively large portion (about 12%) of the global range, so habitat loss here will have a large impact on the global status of the species.

Habitat loss and degradation is most severe in the southern portion of the range. In India, <10% of the species’ range is within protected areas (PAs), and areas outside PAs are subject to development projects and extraction of wood for fuel and livestock fodder (Sathyakumar 2006, Sathyakumar et al. 2012). In Bangladesh, where forest cover is now <7% of the land area, Asiatic Black Bears survive only in small remnant patches in the east, generally near the Myanmar and Indian borders. Cambodia and Myanmar, although still well forested (57% and 48%, respectively), are third and fourth in the world in the annual rate of loss of forested area (among countries occupied by black bears; North Korea and Pakistan have higher rates: FAO 2010). Thailand has lower forest cover (<30%), but most of its remaining forests are within PAs, and three-fourths of these are occupied by black bears (Kanchanasakha et al. 2010). Forest area has recently been increasing in Viet Nam, but much of the present remaining natural forest is highly degraded from both legal and illegal lumbering (Nguyen Xuan Dang 2006, FAO 2010).

Forest area is increasing rapidly in China, which is now first in the world in terms of area gained per year. This increasing forest area stems from mandated government programs aimed mainly toward reducing flooding and erosion; the replanted trees may or may not be particularly suitable for bears. However, good forest habitat does persist in northeastern China, Taiwan, Korea, Russia, and Japan. In Japan, Asiatic Black Bear range has expanded with increasing forest area and diminishing rural human populations (Oi and Yamazaki 2006, Takahata et al. 2014).

Direct killing represents another potential threat. Local people in Nepal, for example, use meat, organs, and bile for food, for healing, to alleviate pain, or even to deter ghosts (Yadav et al. 2012). The sustainability of this practice has never been measured.

Commercial poaching is believed to be a major threat to bears in at least half the range countries, including China, Taiwan, Russia, India, and the five range countries in Southeast Asia (Cambodia, Lao PDR, Myanmar, Thailand, and Viet Nam). Commercial poaching is likely to have especially severe synergistic effects where it coincides with logging and habitat encroachment (Cambodia, Myanmar, Lao, Russia), which increase access for poachers and concentrate bears in ever smaller and fragmented pockets.

Poachers primarily seek gall bladders and paws. The market for bear paws appears to be increasing commensurate with an increasing number of wealthy people who find it within their means to indulge in this very expensive delicacy (Burgess et al. 2014). In 2013, two seizures in two months recovered parts of 81 individual Asiatic Black Bears being smuggled (from Russia) into or within China (Servheen 2013). Such seizures probably represent a small portion of the actual trade in bear paws.

The demand for these bear products has fuelled a growing network of international trade throughout Southeast Asia, fed through poaching of wild bears (Shepherd and Nijman 2008, Foley et al. 2011). Though difficult to quantify because of its covert nature, bear poaching for the wildlife trade is clearly widespread. Hunting of bears for the wildlife trade was reported in over 70% (10 of 14) of the villages interviewed in a northeastern Lao National Protected Area, facilitated by wildlife dealers from Viet Nam who comb rural areas to place orders, supply weapons and ammunition, and transport the off-take (Scotson 2010). In parts of Nepal and Myanmar near the Chinese border, Asiatic Black Bears are among the top preferred species that are hunted commercially for sale of their body parts to China (Rao et al. 2005, Yadav 2012).

It is difficult to evaluate the actual impacts of this trade on wild populations because reliable population estimates and assessments of trends of wild bear populations are unavailable (Garshelis 2002, 2006). Nevertheless, there is evidence that this commercially-driven trade in bear parts is unsustainable and therefore causing populations to decline. In Sichuan Province, which likely has the highest numbers of Asiatic Black Bears in China, bear abundance and distribution have been in steady decline according to opinions of local people, driven predominantly by illegal poaching for bear parts (Liu et al. 2009, 2011). Demand for wild bears drives poaching throughout Southeast Asia. Local inhabitants of a large Thai reserve perceived a 50% decline in Asiatic Black Bear abundance over the previous 20 years, due almost solely to commercial poaching (Steinmetz et al. 2006). Across four countries in Southeast Asia (Myanmar, Thailand, Cambodia, Lao PDR), relative abundance of Asiatic Black Bears determined from camera trapping was half that of Sun Bears (with which they are widely sympatric) on average, indicating much lower densities (Steinmetz 2011). Notably, areas with the most depleted black bear populations are also closer to the Chinese border (Steinmetz 2011). The Asiatic Black Bear is the most highly valued species for consumers of bear parts, and seizures of bear parts in Southeast Asia are almost exclusively from Asiatic Black Bears (Shepherd and Nijman 2008).

Use of cable snares to capture wildlife is widespread in Southeast Asia, and is particularly intensive in Viet Nam, Lao PDR, Myanmar, and Taiwan. In Lao PDR and Vietnam, 1,000s to 10,000s of snares have been removed from single protected areas within a few months (Scotson and Brocklehurst 2013; B. Robichaud, pers. comm). Intensive snaring poses a serious threat to bears because they are often caught inadvertently even if snares are targeted at other species. For example, 8 of 15 bears observed by researchers in Taiwan had missing toes or paws from snares set for wild pigs and other wildlife (Hwang et al. 2010). The recent discovery in Lao PDR of commercially-motivated snare lines designed specifically for bears (Scotson and Hunt 2012) points to increasing pressure on wild populations driven by international demand from the trade in bear parts.

The capture of live bears presents yet another threat to this species. In several Southeast Asian countries Asiatic Black Bears are routinely confiscated from people attempting to raise them as pets, possibly originating from the poaching of their mother for the gall bladder and paws. In Pakistan, several thousand bears were taken from the wild for exhibitions (referred to as bear baiting) in which individual bears (with canines and claws removed) fight with dogs. This practice was made illegal in 2001, but continues to some extent surreptitiously. More commonly now, bears are used for “dancing”.

Conflict between humans and black bears is a widespread problem that occurs across the range of the species: Iran (Ghadirian et al. 2012), Pakistan (Dar et al. 2009, Khan et al. 2012), India (Charoo et al. 2011, Choudhury 2013), Nepal (Stubblefield and Shrestha 2007), Bhutan (Sangay and Vernes 2008; Sonam Wangchuk, Wildlife Conservation Division, Bhutan, pers. comm., 2014), Lao PDR (Scotson et al. 2014), Thailand (Ngoprasert et al. 2011), China (Liu et al. 2011), and Japan (Kishimoto 2009). Human-bear conflicts have negative effects on both people and bears―they include losses to livestock, crops, and apiaries; human injuries and deaths; and killing of bears in defence or retribution. Crop raiding is often extensive especially where farm fields and orchards are close to forest, as in India, Bhutan, and Lao PDR, and large numbers of farmers have reported crop damage from black bears (Charoo et al. 2011, Rinzin et al. 2009, Scotson et al. 2014). Killing of Asiatic Black Bears in crop fields may be motivated more by the value of their parts than the protection of the crops (Liu et al. 2011, Yadav et al. 2012, Scotson et al. 2014).

Human injuries and deaths sometimes occur at tragically high rates, especially in densely settled areas with abundant bears: in Sikkim state, India, at least 25 people were killed or injured by black bears during 2008-2013 (Choudhury 2013). In Honshu, Japan, about 80 people are injured annually, including a few deaths (Japan Bear Network 2011). Such conflicts commonly give rise to negative attitudes towards black bears (Wang et al. 2006, Charoo et al. 2011, Liu et al. 2011, Sakurai and Jacobson 2011). Human-bear conflict can be a source of significant bear mortality when local people or government authorities kill bears to reduce damage; in an extreme case, over 4,000 bears were killed as pests in Japan in 2006 (Kishimoto 2009), representing a significant portion of the country’s population of black bears.

Protected areas are often too small to contain resident black bears. Black bears have large home ranges (>100 km² in some areas; Hwang et al. 2010, Chongsomchai 2013), and their wide-ranging movements may bring them near or beyond the borders of protected areas, where they are more vulnerable to poaching and more likely to come into conflict with farmers (Hwang et al. 2010, Ngoprasert et al. 2011, Choudhury 2013). The availability of natural foods also has a strong effect on whether bears roam outside protected areas. Periods of mast failure or low fruit availability can induce bears to seek human foods outside the forest (Kishimoto 2009, Ngoprasert et al. 2011). Black bear raiding of corn fields adjacent to a park in Thailand coincided with annual periods of low fruit availability, and resulted in some being killed by farmers (Ngoprasert et al. 2011).

For further information about this species, see 22824_Ursus_thibetanus.pdf.
A PDF viewer such as Adobe Reader is required.

Conservation Actions [top]

Conservation Actions:

Protection of forested habitats would be an important conservation measure for this species. China, Thailand, and Viet Nam have imposed various sorts of logging bans, but with varying effects (Durst et al. 2001). In some cases this has resulted in trees being obtained (often illegally) from neighbouring countries, or in creating plantations which do not provide food resources for bears. However, in 2010 Russia banned the felling of Korean Pine, a key bear food source (I. Seryodkin, Russian Academy of Sciences, pers. comm. 2014).

In most countries, closer government collaboration with local people and communities would help conserve natural forests. Community-managed forests have become increasingly important tools for conservation of large mammals in Asia: they can provide breeding habitat, create corridors that link isolated state managed protected areas, facilitate dispersal, and increase habitat that supports an overall larger number of animals. Community-managed forests in Nepal, for example, have created habitat that now holds breeding populations of one-horned rhinos and tigers (Gurung et al. 2008). These community-managed forests may provide similarly valuable habitat for bears, although this remains unexplored. The value of community-managed forests for bears should be investigated further, and expansion of community forest networks promoted where appropriate. The use of existing community-managed forests by bears should also be monitored, such as through sign surveys or camera trapping.

The most beneficial conservation measure for Asiatic Black Bears would be to substantially lessen the demand for bear products, and thus reduce hunting and trade. Large scale, multifaceted, long-term campaigns are urgently required to change social norms regarding consumption of bear parts. Such campaigns are especially important in the main consumer nations of China and Viet Nam, and have indeed been initiated in both those countries by NGOs. As a result, public awareness of bear conservation issues has expanded greatly in the past 10 years in China and Vietnam and attitudes and behaviour are starting to change. In 2014 business leaders in China pledged to cease the practice of corporate gifting of wildlife products and committed to setting new trends for others to follow (TRAFFIC 2014).  As of 2011 over 100,000 Vietnamese citizens had pledged to not consume bear bile, and a number of bear farms had closed due mainly to intensified social pressure (ENV 2012).

The governments of Republic of Korea and Viet Nam are attempting to phase out bear bile farming. Conversely, bear bile farming is on the rise in Lao PDR and Myanmar, stocked by cubs from the wild. Authorities must recognize that these farms have become established due to loopholes in the laws and misreporting of the activities (Livingstone and Shepherd 2016). Meanwhile, China contends that farming must continue or poaching would increase; whereas no solid data are available to evaluate that view, it remains clear that poaching is still the primary threat, and that this will lessen only if the public demand for bile is reduced. Promotion of synthesized UDCA (or a product that includes UDCA as well as other bile compounds) is likely to be the best course for long-term reduction in demand for bear bile.

The Asiatic Black Bear is protected under both international and national laws, but often these laws are not enforced. The Asiatic Black Bear has been included on CITES Appendix I since 1979. In most range countries Asiatic Black Bears are listed as a protected species. For example, they are protected under Class 2 of China's Wildlife Protection Law (a limited number of permits are issued to kill nuisance animals), and under Schedule I of the Indian Wild Life (Protection) Act. In South Korea they are designated as a national monument (No. 329) within the Cultural Properties Protection Law and also as an Endangered Wild Animal. In Japan, this species is listed under the Law for Conservation of Endangered Species of Wild Fauna and Flora, which for trade requires certification of legal take; however, gall bladders and paws are exempted.  Throughout Southeast Asia this species is totally protected in every range country, with the exception of Myanmar, where it is classified as “normally protected”, meaning that it may be killed with a special license, although such licenses are rarely issued (Saw Htun, Wildlife Conservation Society, Myanmar, pers. comm., 2014). The Baluchistan subspecies was listed as Critically Endangered in the 1996 IUCN Red List, and is nationally listed as critically endangered in Pakistan and Iran.

Despite these measures of protection, unabated poaching puts this species at risk across most of its range. Much greater efforts are needed to reduce poaching and snaring pressure, especially where populations are small or fragmented. This can be partly accomplished through anti-poaching patrols, which are typically conducted by trained reserve staff but may also include village volunteers. Such patrols are important for finding and physically removing snares, particularly in Lao PDR and Viet Nam where snaring pressure is intense (Scotson and Brocklehurst 2013). Another indispensable function of patrols is to assess and monitor hunting pressure, in order to gauge the effectiveness of conservation interventions. However, the ability of patrols to actually deter poaching and snaring from happening in the first place, while widely assumed, is little supported by empirical data (Steinmetz et al. 2014). Patrolling is particularly difficult in the remote, mountainous environments that serve as key, remnant habitats for this species. Additional approaches are required.

Poaching could also be reduced by building conservation and co-management partnerships with local communities around parks and reserves, and by supporting community-based conservation in the absence of designated protected areas. Such approaches seek to build trust, raise awareness, provide motivation, support local resource management institutions, use local (as well as outside) knowledge, offer opportunities for action, boost confidence to act, and generate social pressure against poaching—behavioural change is promoted when these conditions converge. Such approaches have been demonstrated to reduce overall poaching pressure (Steinmetz et al. 2014) and increase tolerance for crop-raiding bears (Khan et al. 2012), improving the status of local bear populations (Khan et al. 2012; Steinmetz, unpublished data). Much more effort should be devoted to enhancing the involvement of local communities as conservation partners in protected areas where bears occur.

Sport hunting of Asiatic Black Bears is legal only in Japan and Russia. Russia reports a legal harvest of 75-100 bears/year and an estimated illegal take of about 500 bears/year. Sport harvests of black bears in Japan average about 500/year and have been slowly declining since the late 1980s due to diminishing interest in hunting (Oi and Yamazaki 2006). However, a higher number (generally 1,000-2,000) of nuisance black bears are killed annually (using mainly traps) in towns or agricultural areas of Japan.

The Republic of  Korea has been partially successful in restoring their wild bear population through restocking, initially with captive-born bears, and later with orphaned wild bears from Russia (which are genetically similar to native Korean bears; Kim et al. 2011). These bears are now reproducing. Some Southeast Asian countries, like Cambodia and Thailand are also considering reintroducing bears from captivity, in part to augment wild populations, and in part to relieve pressures on captive facilities which cannot sustain the steady influx of confiscated animals.

Throughout much of the southern portion of the range of this species, efforts to reduce habitat degradation outside PAs and to increase the number and/or area of PAs would be highly beneficial. An increasing number of PAs are being established in China, Russia, India, and a few other countries within the range of Asiatic black bears (Chape et al. 2008, Sathyakumar et al. 2012), mainly to protect other species, but serving as well to increase protection for black bears. Additionally, the recently amended (2003) Indian Wild Life (Protection) Act provides options for new categories of PAs that could be established to form travel corridors between existing PAs.

More attention is needed on the issue of human-bear conflicts. A few recent studies have examined mitigation methods to reduce conflicts (Charoo et al. 2011, Scotson et al. 2014) and to create risk models to predict where conflicts are most likely to occur (Honda et al. 2009, Takahata et al. 2014). However, solutions to this issue remain largely elusive, because conflicts are in part due to varying food conditions in the wild, and in part to nearby availability of human food sources. Participation of local people in designing solutions and monitoring outcomes will be critical to success. Projects will probably need to be implemented for a number of years to produce useful outcomes; long-term funding will thus be needed to advance the science of human–bear conflict resolution. Where sufficient human resources and funding exist, conflict rapid-response teams (staffed by NGOs, government personnel, and local people) can be effective. Safety guidelines can be devised and disseminated, based on knowledge of bear behaviour and ecology in an area, to help people avoid bears or minimize chances of being attacked. Better methods to deter bears are also needed. Additionally, educational efforts to increase awareness and promote greater tolerance of some level of crop-raiding and livestock loss are likely to be key to success (Khan et al. 2012).

Aside from the global Status Survey and Conservation Action Plan for this species, published by the IUCN in 1999 (Servheen et al. 1999), which is incomplete and now quite outdated, two range countries, Taiwan and India, have developed National Conservation Action Plans for bears (Hwang et al. 2012, Sathyakumar et al. 2012). These are the first such conservation action plans for bears in Asia (although other countries have developed less extensive plans that aid conservation, as for example to deal with human-bear conflicts). Both of these country action plans were developed through a wide range of consultations with stakeholders. The Taiwanese plan concerns only Asiatic Black Bears, since this is the only bear species in the country (and also an endemic subspecies, U. t. formosanus). The Indian plan covers all four species present in that country: Asiatic Black Bears, Sloth Bears, Brown Bears, and Sun Bears. Both plans emphasize the same key themes: reduction in illegal hunting, mitigation of human–bear conflicts, increased habitat management, enhanced research and information gathering, capacity building, and improved communication and education.  Both plans stress actions aimed against illegal hunting, including intelligence gathering, incentivized enforcement, community awareness, restriction of guns, and creation of a database to monitor trade. However, the root of the hunting issue is different in the two countries: in India hunters are motivated to sell bear parts, some of which are traded internationally, whereas in Taiwan bears are taken mainly opportunistically or as by-catch from illegal snaring for ungulates, and the parts (including meat) are used or sold locally (Hwang 2003). Other priority actions in the action plans include: strengthening methods of crop and livestock protection; reducing bear-caused human injuries (India), creating rapid response teams to investigate conflicts with bears (and possible claims for monetary compensation); enhancing human tolerance toward bears; identifying critical habitats and corridors used by bears, especially those outside PAs; increasing habitat protection and restoring degraded habitats outside PAs; reducing dependency of local communities on resources needed by bears; discouraging shifting agriculture; developing methods to track population size and trends; involving communities in bear monitoring programs; equipping forest and wildlife staff with adequate knowledge and modern equipment to manage all types of human-bear interactions; and developing an advocacy program for bear conservation through active communication to the public and pressure on corporations and politicians.

Errata [top]

Errata reason: The Supplementary Material was accidentally left off the assessment when it was published; this omission is corrected in this version of the assessment. Some country names have also been updated and a few typographical errors have been corrected.

Classifications [top]

1. Forest -> 1.1. Forest - Boreal
suitability:Suitable  major importance:No
1. Forest -> 1.4. Forest - Temperate
suitability:Suitable  major importance:Yes
1. Forest -> 1.5. Forest - Subtropical/Tropical Dry
suitability:Suitable  major importance:Yes
1. Forest -> 1.6. Forest - Subtropical/Tropical Moist Lowland
suitability:Suitable  major importance:Yes
1. Forest -> 1.9. Forest - Subtropical/Tropical Moist Montane
suitability:Suitable  major importance:Yes
3. Shrubland -> 3.5. Shrubland - Subtropical/Tropical Dry
suitability:Suitable  major importance:No
4. Grassland -> 4.7. Grassland - Subtropical/Tropical High Altitude
suitability:Suitable  major importance:No
5. Wetlands (inland) -> 5.3. Wetlands (inland) - Shrub Dominated Wetlands
suitability:Suitable  major importance:No
14. Artificial/Terrestrial -> 14.1. Artificial/Terrestrial - Arable Land
suitability:Suitable  major importance:No
14. Artificial/Terrestrial -> 14.3. Artificial/Terrestrial - Plantations
suitability:Suitable  major importance:No
14. Artificial/Terrestrial -> 14.6. Artificial/Terrestrial - Subtropical/Tropical Heavily Degraded Former Forest
suitability:Suitable  major importance:No
1. Land/water protection -> 1.1. Site/area protection
2. Land/water management -> 2.1. Site/area management
4. Education & awareness -> 4.3. Awareness & communications
5. Law & policy -> 5.4. Compliance and enforcement -> 5.4.1. International level
5. Law & policy -> 5.4. Compliance and enforcement -> 5.4.2. National level
5. Law & policy -> 5.4. Compliance and enforcement -> 5.4.3. Sub-national level
6. Livelihood, economic & other incentives -> 6.2. Substitution
6. Livelihood, economic & other incentives -> 6.3. Market forces
6. Livelihood, economic & other incentives -> 6.5. Non-monetary values

In-Place Research, Monitoring and Planning
In-Place Land/Water Protection and Management
  Conservation sites identified:Yes, over entire range
In-Place Species Management
In-Place Education
  Included in international legislation:Yes
  Subject to any international management/trade controls:Yes
2. Agriculture & aquaculture -> 2.1. Annual & perennial non-timber crops -> 2.1.1. Shifting agriculture
♦ timing:Ongoing ♦ scope:Majority (50-90%) ♦ severity:Slow, Significant Declines ⇒ Impact score:Medium Impact: 6 
→ Stresses
  • 1. Ecosystem stresses -> 1.2. Ecosystem degradation
  • 2. Species Stresses -> 2.1. Species mortality
  • 2. Species Stresses -> 2.2. Species disturbance

2. Agriculture & aquaculture -> 2.1. Annual & perennial non-timber crops -> 2.1.2. Small-holder farming
♦ timing:Ongoing ♦ scope:Majority (50-90%) ♦ severity:Slow, Significant Declines ⇒ Impact score:Medium Impact: 6 
→ Stresses
  • 1. Ecosystem stresses -> 1.1. Ecosystem conversion
  • 2. Species Stresses -> 2.1. Species mortality
  • 2. Species Stresses -> 2.2. Species disturbance

2. Agriculture & aquaculture -> 2.1. Annual & perennial non-timber crops -> 2.1.3. Agro-industry farming
♦ timing:Ongoing ♦ scope:Majority (50-90%) ♦ severity:Slow, Significant Declines ⇒ Impact score:Medium Impact: 6 
→ Stresses
  • 1. Ecosystem stresses -> 1.1. Ecosystem conversion
  • 2. Species Stresses -> 2.2. Species disturbance

2. Agriculture & aquaculture -> 2.2. Wood & pulp plantations -> 2.2.1. Small-holder plantations
♦ timing:Ongoing ♦ scope:Minority (<50%) ♦ severity:Unknown ⇒ Impact score:Unknown 
→ Stresses
  • 1. Ecosystem stresses -> 1.1. Ecosystem conversion
  • 2. Species Stresses -> 2.2. Species disturbance

2. Agriculture & aquaculture -> 2.2. Wood & pulp plantations -> 2.2.2. Agro-industry plantations
♦ timing:Ongoing ♦ scope:Minority (<50%) ♦ severity:Slow, Significant Declines ⇒ Impact score:Low Impact: 5 
→ Stresses
  • 1. Ecosystem stresses -> 1.1. Ecosystem conversion
  • 2. Species Stresses -> 2.2. Species disturbance

2. Agriculture & aquaculture -> 2.3. Livestock farming & ranching -> 2.3.1. Nomadic grazing
♦ timing:Ongoing ♦ scope:Minority (<50%) ♦ severity:Unknown ⇒ Impact score:Unknown 
→ Stresses
  • 1. Ecosystem stresses -> 1.2. Ecosystem degradation
  • 2. Species Stresses -> 2.2. Species disturbance

4. Transportation & service corridors -> 4.1. Roads & railroads
♦ timing:Ongoing ♦ scope:Minority (<50%) ♦ severity:Slow, Significant Declines ⇒ Impact score:Low Impact: 5 
→ Stresses
  • 1. Ecosystem stresses -> 1.3. Indirect ecosystem effects
  • 2. Species Stresses -> 2.1. Species mortality
  • 2. Species Stresses -> 2.2. Species disturbance

5. Biological resource use -> 5.1. Hunting & trapping terrestrial animals -> 5.1.1. Intentional use (species is the target)
♦ timing:Ongoing ♦ scope:Majority (50-90%) ♦ severity:Very Rapid Declines ⇒ Impact score:High Impact: 8 
→ Stresses
  • 2. Species Stresses -> 2.1. Species mortality

5. Biological resource use -> 5.1. Hunting & trapping terrestrial animals -> 5.1.2. Unintentional effects (species is not the target)
♦ timing:Ongoing ♦ scope:Majority (50-90%) ♦ severity:Rapid Declines ⇒ Impact score:Medium Impact: 7 
→ Stresses
  • 2. Species Stresses -> 2.1. Species mortality

5. Biological resource use -> 5.1. Hunting & trapping terrestrial animals -> 5.1.3. Persecution/control
♦ timing:Ongoing ♦ scope:Majority (50-90%) ♦ severity:Causing/Could cause fluctuations ⇒ Impact score:Medium Impact: 6 
→ Stresses
  • 2. Species Stresses -> 2.1. Species mortality

5. Biological resource use -> 5.3. Logging & wood harvesting -> 5.3.1. Intentional use: (subsistence/small scale) [harvest]
♦ timing:Ongoing ♦ scope:Minority (<50%) ♦ severity:Slow, Significant Declines ⇒ Impact score:Low Impact: 5 
→ Stresses
  • 1. Ecosystem stresses -> 1.1. Ecosystem conversion

5. Biological resource use -> 5.3. Logging & wood harvesting -> 5.3.2. Intentional use: (large scale) [harvest]
♦ timing:Ongoing ♦ scope:Majority (50-90%) ♦ severity:Very Rapid Declines ⇒ Impact score:High Impact: 8 
→ Stresses
  • 1. Ecosystem stresses -> 1.1. Ecosystem conversion

7. Natural system modifications -> 7.2. Dams & water management/use -> 7.2.10. Large dams
♦ timing:Future ♦ scope:Minority (<50%) ♦ severity:Very Rapid Declines ⇒ Impact score:Low Impact: 5 
→ Stresses
  • 1. Ecosystem stresses -> 1.1. Ecosystem conversion
  • 2. Species Stresses -> 2.2. Species disturbance

1. Research -> 1.2. Population size, distribution & trends
1. Research -> 1.6. Actions
2. Conservation Planning -> 2.1. Species Action/Recovery Plan
3. Monitoring -> 3.1. Population trends
3. Monitoring -> 3.3. Trade trends
3. Monitoring -> 3.4. Habitat trends

Bibliography [top]

Abbas, F., Bhatti, Z.I., Haider, J., and Mian, A. 2015. Bears in Pakistan: distribution, population biology and human conflicts. Journal of Bioresource Management 2: 1-13.

Ahmadzadeh F., Liaghati, H., Kiabi, B.H., Mehrabian, A.R., Abdoli, A., and Mostafavi, H. 2008. The status and conservation of the Asiatic black bear in Nikshahr County, Baluchistan District of Iran. Journal of Natural History 42: 2379–2387.

Aramilev, V. V. 2006. The conservation status of Asiatic black bears in the Russian Far East. Understanding Asian Bears to Secure Their Future, pp. 86-89. Japan Bear Network, Ibaraki, Japan.

Aryal, A., Raubenheimer, D., Sathyakumar, S., Poudel, B. S., Ji, W., Kunwar, K. J., Kok, J., Kohshima, S., and Brunton, D. 2012. Conservation strategy for brown bear and its habitat in Nepal. Diversity 4(301-317).

Bargali, H.S. 2012. Distribution of different species of bears and status of human-bear conflict in the State of Uttarakhand, India. Advances in Biological Research 6(3): 121-127.

Baryshnikov, G.F., and Zakharov, D.S. 2013. Early Pliocene bear Ursus thibetanus (Mammalia, Carnivora) from Priozernoe locality in the Dniester Basin (Moldova Republic). Proceedings of the Zoological Institute of the Russian Academy of Sciences 317: 3-10.

Bista, R., and Aryal, A. 2013. Status of the Asiatic black bear Ursus thibetanus in the southeastern region of the Annapurna Conservation Area, Nepal. Zoology and Ecology.

Boatright, J.H., Moring, A.G., McElroy, C., Phillips, M.J., Do, V.T., Chang, B., Hawes, N.L., Boyd, A.P., Sidney, S.S., Stewart, R.E., Minear, S.C., Chaudhury, R., Ciavatta, V.T., Rodrigues, C.M.P., Steer, C.J., Nickerson, J.M., and Pardue, M.T. 2006. Tool from ancient pharmacopoeia prevents vision loss. Molecular Vision 12: 1706–1714.

Bromlei, F. G. 1965. Bears of the South Far-eastern USSR. Indian National Scientific Documentation Center, New Delhi, India.

Burgess, E.A., Stoner, S.S. and Foley, K.E. 2014. Brought to bear: an analysis of seizures across Asia (2000-2011). TRAFFIC Southeast Asia, Petaling Jaya, Selangor, Malaysia.

Carr, M. M., Yoshizaki, J., van Manen, F. T., Pelton, M. R., Huygens, O. C., Hayashi, H. and Maekawa, M. 2002. A multi-scale assessment of habitat use by asiatic black bears in central Japan. Ursus 13: 1-9.

Chang, H-C., Chang, H-J., Chao, T-Y. and Chan, S-Y. 1995. A survey of bear gallbladder commodities in the Taiwan market. Department of Health, Taipei, Taiwan.

Chape, S. Spalding, M. Jenkins, M. 2008. The World's protected areas: status, values and prospects in the 21st century. University of California Press, Berkeley, USA.

Charoo, S.A., Sharma, L.K., and Sathyakumar, S. 2011. Asiatic black bear-human interactions around Dachigam National Park, Kashmir, India. Ursus 22: 106–113.

Chongsomchai, Y. 2013. Habitat utilization and daily activity of Asiatic black bear (Ursus thibetanus) in Huai Kha Khaeng wildlife sanctuary. Kasetsart University, Bangkok.

Choudhury, A. 2011. Records of Black-breasted Parrotbill Paradoxornis flavirostris from Manas National Park, Assam, in north-east India. Forktail 27: 106-107.

Choudhury, A.U. 2013. Records of Asiatic black bear in North East India. Final report to International Association for Bear Research and Management (IBA). The Rhino Foundation for nature in NE India, Guwahati, Assam, India.

Choudhury, A.U. and Chand, S. 2012. Bear conservation action plan Assam. In: Sathyakumar, S., R. Kaul, N.V.K. Ashraf, A. Mookherjee, and V. Menon (eds), National bear conservation and welfare action plan, pp. 93-101. Ministry of Environment and Forests, Wildlife Institute of India, and Wildlife Trust of India.

Dar, N.I., .Minhas, R.A., Zaman, Q., and Linkie, M. 2009. Predicting the patterns, perceptions and causes of human–carnivore conflict in and around Machiara National Park, Pakistan. Biological Conservation 142: 2076–2082.

Durst, P.B, Waggener, T.R., Enters, T. and Cheng, T.L. 2001. Forests out of bounds: impacts and effectiveness of logging bans in natural forests in Asia-Pacific. Food and Agricultural Organization of the United Nations, Regional Office for Asia and the Pacific, Bangkok, Thailand.

Engin, F., Yermalovich, A., Ngyuen, T., Hummasti, S., Fu, W., Eizirik, D.L., Mathis, D., and Hotamisligil, G.S. 2013. Restoration of the unfolded protein response in pancreatic b cells protects mice against Type 1 diabetes. Science Translational Medicine 5.

ENV (Education for Nature Vietnam). 2012. New from the front line newsletter. Issue 2. Education for Nature Vietnam, Hanoi, Vietnam.

Erdbrink, D.P. 1953. A review of fossil and recent bears of the Old World with remarks on their phylogeny based upon their dentition. Drukkerij Jan de Lange, Deventer, Netherlands.

Fahimi, H., Yusefi, G.H., Madjdzadeh, S.M., Damangir, A.A., Sehhatisabet, M.E., and Khalatbari, L. 2011. Camera traps reveal use of caves by Asiatic black bears (Ursus thibetanus gedrosianus) (Mammalia: Ursidae) in southeastern Iran. Journal of Natural History 45: 2363–2373.

FAO. 2006. Global forest resources 2005. Progress towards sustainable forest management, Food and Agriculture Organization of the United Nations, Rome, Italy.

Feng, Y., Siu, K., Wang, N., Ng, K-M., Tsao, S-W., Nagamatsu, T., and Tong, Y. 2009. Bear bile: dilemma of traditional medicinal use and animal protection. Journal of Ethnobiology and Ethnomedicine 5.

Foley, K.E., Stengel, C.J. and Shepherd, C.R. 2011. Pills, Powders, Vials and Flakes: the bear bile trade in Asia. TRAFFIC Southeast Asia, Petaling Jaya, Selangor, Malaysia.

Fourvel, J-B, Fosse, P., Brugal, J-P., Cregut-Bonnoure, E., Slimak, L., and Tournepiche, J-F. 2014. Characterization of bear remains consumption by Pleistocene large carnivores (Felidae, Hyaenidae, Canidae). Quaternary International: 339–340: 232–244.

Galbreath, G. J., Hean, S. and Montgomery, S. M. 2000. A new color phase of Ursus thibetanus (Mammalia: Ursidae) from Southeast Asia. Natural History Bulletin of the Siam Society 49: 107-111.

Galbreath, G.J., Hunt, M., Clements, T. and Waits, L.P. 2008. An apparent hybrid wild bear from Cambodia. Ursus 19: 85-86.

Garshelis, D.L. 2002. Misconceptions, ironies, and uncertainties regarding trends in bear populations. Ursus 13: 321-334.

Garshelis, D.L. 2006. Assessing the status of the world’s bears—what can we tell from the trade in bear parts? In: Williamson, D. (ed.). Proceedings of the 4th international symposium on the trade in bear parts. pp. 6–20. TRAFFIC, East Asia–Japan, Tokyo.

Garshelis, D.L. and Scotson, L. 2012. World conservation congress votes to curtail bear farming. International Bear News 21: 12-16.

Garshelis, D.L., Joshi, A.R., Smith, J.L.D. and Rice, C.G. 1999. Sloth bear conservation action plan. In: C. Servheen, S. Herrero, and B. Peyton (eds), Bears: status survey and conservation action plan, pp. 225-240. IUCN/SSC Bear and Polar Bear Specialist Groups, Gland, Switzerland and Cambridge, U.K.

Ghadirian, T., Ghoddousi, A., Abolghasemi, H., Riazifar, A., Nekoei G., and Dehghani, M. 2012a. First camera-trap photos of Asiatic black bears in the Bashagard Region of southeastern Iran. International Bear News 21(1): 15-17.

Ghadirian, T., Ghoddousi, A., Qashqaei, A.T., Soufi, M. and Abolghasemi, H. 2012b. What can Asiatic Black Bears find to eat at the western edge of their geographic range (southern Iran)? . International Bear News 21(3): 27–28.

Gong, J. and Harris, R.B. 2006. The status of bears in China. Understanding Asian bears to secure their future, pp. 50-56. Japan Bear Network, Ibaraki, Japan.

Gurung, B., Smith, J.L.D., McDougal, C,. Karki, J.B., and Barlow, A. 2008. Factors associated with human-killing tigers in Chitwan National Park, Nepal. Biological Conservation 141: 3069–3078.

Gutleb, B. and Ziaie, H. 1999. On the distribution and status of the Brown Bear, Ursus arctos, and the Asiatic Black Bear, U. thibetanus, in Iran. Zoology in the Middle East 18: 5-8.

Hashimoto, Y. 2002. Seasonal food habits of the Asiatic black bear (Ursus thibetanus) in the Chichibu Mountains, Japan. Mammal Study 27: 65–72.

Hashimoto, Y., Kaji, M., Sawada, H. and Takatsuki, S. 2003. Five-year study on the autumn food habits of the Asiatic black bear in relation to nut production. Ecological Research 18: 485-492.

Higashide, D., Miura, S., and Miguchi, H. 2012. Are chest marks unique to Asiatic black bear individuals? Journal of Zoology 288: 199–206.

Higashide, D., Miura, S., and Miguchi, H. 2013. Evaluation of camera-trap designs for photographing chest marks of the free-ranging Asiatic black bear, Ursus thibetanus. Mammal Study 38: 35–39.

Honda, T., Yoshida, Y., and Nagaike, T. 2009. Predictive risk model and map of human-Asiatic black bear contact in Yamanashi Prefecture, central Japan. Mammal Study 34: 77–84.

Horino, S. and Miura, S. 2000. Population viability analysis of a Japanese black bear population. Population Ecology 42: 37–44.

Huygens, O. C. and Hayashi, H. 2001. Use of stone pine seeds and oak acorns by Asiatic black bears in central Japan. Ursus 12: 47-50.

Huygens, O. C., Miyashita, T., Dahle, B., Carr, M., Izumiyama, S., Sugawara, T. and Hayashi, H. 2003. Diet and feeding habits of Asiatic black bears in the Northern Japanese Alps. Ursus 14: 236-245.

Huygens, O., Goto, M., Izumiyama, S., Hayashi, H., and Yoshida, T. 2001. Denning ecology of two populations of Asiatic black bears in Nagano prefecture, Japan. Mammalia 65: 417-428.

Hwang, M.-H. 2003. Ecology of Asiatic black bears and people-bear interactions in Yushan National Park, Taiwan. Thesis, University of Minnesota.

Hwang, M.-H. and Garshelis, D. L. 2007. Activity patterns of Asiatic black bears (Ursus thibetanus) in the Central Mountains of Taiwan. Journal of Zoology (London) 271: 203-209.

Hwang, M. H., Garshelis, D. L. and Wang, Y. 2002. Diets of asiatic black bears in Taiwan, with methodological and geographical comparisons. Ursus 13: 111-125.

Hwang, M-H., Garshelis, D.L., Wu, Y-H., and Wang, Y. 2010. Home ranges of Asiatic black bears in the Central Mountains of Taiwan: Gauging whether a reserve is big enough. Ursus 21: 81–96.

Hwang, M-H., Pan, Y-J., R-A. Lin, R-A. 2012. Distribution model and conservation action plan for Formosan black bears. Forestry Bureau, Taipei, Taiwan.

Islam, M.A., Uddin, M., Aziz, M.A., Muzaffar, S.B., Chakma, S., Chowdhury, S.U., Chowdhury, G.W., Rashid, M.A., Mohsanin, S., Jahan, I., Saif, S., Hossain, M.B., Chakma, D., Kamruzzaman, M. and Akter, R. 2013. Status of bears in Bangladesh: going, going, gone? Ursus 24: 83-90.

IUCN. 2016. The IUCN Red List of Threatened Species. Version 2016-3. Available at: www.iucnredlist.org. (Accessed: 07 December 2016).

IUCN. 2017. The IUCN Red List of Threatened Species. Version 2017-1. Available at: www.iucnredlist.org. (Accessed: 27 April 2017).

Izumiyama, S. and Shiraishi, T. 2004. Seasonal changes in elevation and habitat use of the Asiatic black bear (Ursus thibetanus) in the Northern Japan Alps. Mammal Studies 29: 1-18.

Japan Bear Network. 2011. The report of accidents causing injury or death by bears. Japan Bear Network, Ibaraki, Japan.

Jeong, D-H., Lee, B-K., and Kang, J-K. 2011. The status of Asiatic black bears transplanted into Jirisan National Park, South Korea. . International Bear News 20(3): 14-16.

Kanchanasakha, B, Tanhikorn, S., Vinitpornsawan, V., Prayoon, A., and Paengphupha, G. 2010. Status of large mammals in Thailand. Department of National Parks, Wildlife, and Plant Conservation, Bangkok, Thailand.

Kang, S. and Phipps, M. J. 2003. A question of attitude: South Korea's Traditional Medicine practitioners and wildlife conservation. TRAFFIC East Asia, Hong Kong.

Khan, M., Rosen, T., and Zahler, P. 2012. Status and conservation of Asiatic black bears in Diamer District, Pakistan. International Bear News 21(1): 13-14.

Kim,Y-K., Hong, Y-J., Min, M-S., Kim, K. S., Kim, Y-J., Voloshina, I., Myslenkov, A., Smith, G.J.D., Cuong, N.D., Tho, H.H., Han, S-H., Yang, D-H., Kim, C-B., and Lee, H. 2011. Genetic status of Asiatic black bear (Ursus thibetanus) reintroduced into South Korea based on mitochondrial DNA and microsatellite loci analysis. Journal of Heredity 102: 165-174.

Kishimoto, R. 2009. Status of the 2006 drastic rise of Asiatic black bear (Ursus thibetanus) intrusions into residential areas in Nagano Prefecture. In: Oi et al. (ed.), Biology of bear intrusions, pp. 35–39.

Koike, S. 2009. Fruiting phenology and its effect on fruit feeding behavior of Asiatic black bears. Mammal Study 34: 47–52.

Koike, S. 2010. Long-term trends in food habits of Asiatic black bears in the Misaka Mountains on the Pacific coast of central Japan. Mammalian Biology 75(17–28).

Koike, S., and Hazumi, T. 2008. Notes on Asiatic black bears denning in the Misaka Mountains, central Japan. Ursus 19: 80–84.

Koike, S., Kozakai, C., Nemoto, Y., Masaki, T., Yamazaki, K., Abe, S., Nakajima, A., Umemura, Y., and Kaji, K. 2012. Effect of hard mast production on foraging and sex-specific behavior of the Asiatic black bear (Ursus thibetanus). Mammal Study 37: 21–28.

Koike, S., Masaki, T., Nemoto, Y., Kozakai, C., Yamazaki , K., Kasai, S., Nakajima, A., and Kaji, K. 2010. Estimate of the seed shadow created by the Asiatic black bear Ursus thibetanus and its characteristics as a seed disperser in Japanese cool-temperate forest. Oikos 120: 280–290.

Koike, S., Morimoto, H., Goto, Y., Kozakai, C., and Yamazaki, K. 2008. Frugivory of carnivores and seed dispersal of fleshy fruits in cool-temperate deciduous forests. Journal of Forest Research 13: 215–222.

Koike, S., Nakashita, R., Naganawa, K., Koyama, M., and Tamura, A., 2013. Changes in diet of a small, isolated bear population over time. Journal of Mammalogy 94: 361–368.

Kosintsev, P. 2007. Late Pleistocene large mammal faunas from the Urals. . Quaternary International 160: 112–120.

Kozakai, C., Yamazaki, K., Nemoto, Y., Nakajima, A., Koike, S., Abe, S., Masaki, T., and Kaji, K. 2011. Effect of mast production on home range use of Japanese black bears. Journal of Wildlife Management 75: 867–875.

Kozakai, C., Yamazaki, K., Nemoto, Y., Nakajima, A., Umemura, Y., Koike, S., Goto, Y., Kasai, S., Abe, S., Masaki, T., and Kaji, K. 2013. Fluctuation of daily activity time budgets of Japanese black bears: relationship to sex, reproductive status, and hardmast availability. Journal of Mammalogy 94: 351–360.

Liu, F., McShea, W., Garshelis, D., Zhu, X., Wang, D., and Shao, L. 2010. Human-wildlife conflicts influence attitudes but not necessarily behaviors: Factors driving the poaching of bears in China. Biological Conservation 144(538–547).

Liu, F., McShea, W., Garshelis, D., Zhu, X., Wang, D., Gong, J., and Chen, Y. 2009. Spatial distribution as a measure of conservation needs: an example with Asiatic black bears in south‐western China. Diversity and Distributions 15: 649–659.

Livingstone, E., and Shepherd, C.R. 2016. Bear farms in Lao PDR expand illegally and fail to conserve wild bears. Oryx 50: 176–184.

Ministry of the Environment. 2011. A Heisei 22 fiscal year report for national survey on the natural environment – investigation of living status of the specific wild animals and investigation for establishing monitoring footing. Biodiversity Center, Minsitry of the Environment, Japan.

Mizukami, R. N., Goto, M., Izumiyama, S., Hayashi, H. and Yoh, M. 2005. Estimation of feeding history by measuring carbon and nitrogen stable isotope ratios in hair of Asiatic black bears. Ursus 16: 93-101.

Mukesh, L.K. Sharma, S.A. Charoo, and Sathyakumar, S. 2015. Conflict bear translocation: investigating population genetics and fate of bear translocation in Dachigam National Park, Jammu and Kashmir, India. PLoS ONE 10(8).

Narita, R., Sugimoto, A., and Takayanagi, A. 2006. Animal componets in the diet of Japanese black bears Ursus thibetanus japonicas in the Kyoto area, Japan. Wildlife Biology 12(375–384).

Ngoprasert, D., Reed, D.H., Steinmetz, R. and Gale, G.A. 2012. Density estimation of Asian bears using photographic capture–recapture sampling based on chest marks. Ursus 23: 117-133.

Ngoprasert, D., Steinmetz, R., and Gale, G.A. 2010. The use of chest marks to distinguish Asiatic black bear and sun bear individuals in Thailand. International Bear News 19(2): 18-20.

Ngoprasert, D., Steinmetz, R., and Gale, G.A. 2013. Estimating the abundance of Asiatic black bears and sun bears in Thailand. International Bear News 22(3): 30-32.

Ngoprasert, D., Steinmetz, R., Reed, D.H., Savini, T., and Gale, G.A. 2011. Influence of fruit on habitat selection of Asian bears in a tropical forest. Journal of Wildlife Management 75: 588–595.

Nguyen Xuan Dang. 2006. The current status and conservation of bears in Vietnam. Understanding Asian bears to secure their future., pp. 61-65. Japan Bear Network, Ibaraki, Japan.

Oi, T., and Furusawa, H. 2008. Nutritional condition and dietary profile of Japanese black bear (Ursus thibetanus japonicas) killed in western Japan in autumn 2004. Mammal Study 33: 163–171.

Oi, T. and Yamazaki, K. 2006. The status of Asiatic black bears in Japan. Understanding Asian bears to secure their future, pp. 122-133. Japan Bear Network, Ibaraki, Japan.

Ostrowski, S., Zahler, P., Dehgan, A., Stevens, K., Karlstetter, M., and Smallwood, P. 2009. The Asiatic black bear still survives in Nuristan, Afghanistan. International Bear News 18(4): 14-15.

Phelps, J., Carrasco, L.R., and Webb, E.L. 2014. A framework for assessing supply‐side wildlife conservation. Conservation Biology 28: 244–257.

Rao, M., Myint, T., Zaw, T. and Htun, S. 2005. Hunting patterns in tropical forests adjoining the Hkakaborazi National Park, north Myanmar. Oryx 39(3): 292-300.

Reid, D., Jiang, M., Teng, Q., Qin, Z. and Hu, J. 1991. Ecology of the Asiatic black bear (Ursus thibetanus) in Sichuan, China. Mammalia 55: 221-237.

Rinzin, C., Vermeulen, W.J., Wassen, M.J., and Glasbergen, P. 2009. Nature conservation and human well-being in Bhutan: an assessment of local community perceptions. The Journal of Environment & Development 177–202.: 177–202.

Sakurai, R., and Jacobson, S.K. 2011. Public perceptions of bears and management interventions in Japan. Human–Wildlife Interactions 5: 123–134.

Sangay, T., and Vernes, K. 2008. Human–wildlife conflict in the Kingdom of Bhutan: patterns of livestock predation by large mammalian carnivores. Biological Conservation 141: 1272–1282.

Sathyakumar, S. 2006. The status of Asiatic black bears in India. Understanding Asian bears to secure their future, pp. 12-19. Japan Bear Network, Ibaraki, Japan.

Sathyakumar, S. 2006. The status of Asiatic black bears in India. Understanding Asian bears to secure their future . pp. 12-19. Japan Bear Network, Ibaraki, Japan.

Sathyakumar, S., and Choudhury, A. 2007. Distribution and status of the Asiatic black bear Ursus thibetanus in India. Journal of the Bombay Natural History Society 104: 316–323.

Sathyakumar, S., and Viswanath, S. 2003. Observations on food habits of Asiatic Black Bear (Ursus thibetanus) in Kedarnath Wildlife Sanctuary, India – Preliminary evidence on the role of black bears in enhancing seed germination and dispersal. Ursus 14(95–104).

Sathyakumar, S., Bashir, T., Bhattacharya, T. and Poudyal, K. 2011. Assessing mammal distribution and abundance in intricate eastern Himalayan habitats of Khangchendzonga, Sikkim India. Mammalia 75: 257-268.

Sathyakumar, S., Kaul, R., Ashraf, N.V.K., Mookherjee, A., and Menon, V. 2012. National Bear Conservation and Welfare Action Plan. Ministry of Environment and Forests, Wildlife Institute of India, and Wildlife Trust of India, India.

Saw Htun. 2006. The status and conservation of bears in Myanmar. Understanding Asian bears to secure their future, pp. 45-49. Japan Bear Network, Ibaraki, Japan.

Schaller, G. B., Teng, Q., Johnson, K. G., Wang, X., Shen, H. and Hu, J. 1989. The feeding ecology of giant pandas and Asiatic black bears in the Tangjiahe Reserve, China. In: J. L. Gittleman (ed.), Carnivore behavior, ecology, and evolution, pp. 212-240. Cornell University Press, Ithaca, NY, USA.

Scotson, L. 2010. Distribution and status of Asiatic black bear and Malayan sun bear in Nam Et Phou Louey National Protected Area, northeast Lao PDR. International Bear News 19: 14-16.

Scotson, L. 2012. Status of Asiatic black bears and sun bears in Xe Pian National Protected Area, Lao PDR. International Bear News 21: 8-11.

Scotson, L. and Brocklehurst, M. 2013. Bear poaching in Lao PDR is exposed as an increasing threat to wild populations. International Bear News 22: 22-23.

Scotson, L. and Hunt, M. 2012. Dismantling the “wall of death”: emergency bear snare-line patrol in the Nam Kan National Protected Area, Lao PDR. International Bear News 21: 17-19.

Scotson, L., Vannachomchan,K., and T. Sharp, T. 2014. More valuable dead than deterred: crop raiding bears in Lao PDR. Wildlife Society Bulletin 38: 783–790.

Servheen, C. 2013. Bear paw smuggling into China continues. International Bear News 22(3): 24.

Servheen, C., Herrero, S. and Peyton, B. 1999. Bears. Status Survey and Conservation Action Plan. IUCN/SSC Bear and Polar Bear Specialist Groups, Gland, Switzerland.

Seryodkin, I. V., Goodrich, J. M., Kostyria, A. V., Schleyer, B. O., Smirnov, E. N., Kerley, L. L. and Miquelle, D. G. 2005. Relationship between tigers, brown bears, and Himalayan black bears. In: D. G. Miquelle, E. N. Smirnov and J. M. Goodrich (eds), Tigers of Sikhote-Alin Zapovednik: ecology and conservation, pp. 156-163. PSP, Vladivostok, Russia.

Seryodkin, I. V., Kostyria, A. V., Goodrich, J. M., Miquelle, D. G., Smirnov, E. N., Kerley, L. L., Quigley, H. B. and Hornocker, M. G. 2003. Denning ecology of brown bears and Asiatic black bears in the Russian Far East. Ursus 14: 153-161.

Sharma, L.K., Charoo, S.A., and S. Sathyakumar, S. 2010. Investigations on the Ecology and Behaviour of Asiatic Black bear using Satellite Telemetry: A case study from the Dachigam National Park, Kashmir, India. Telemetry in Wildlife Science, ENVIS Bulletin: Wildlife & Protected Areas , pp. 86–94. Wildlife Institute of India, Dehradun.

Shepherd, C.R. and Nijman, V. 2008. The trade in bear parts from Myanmar: an illustration of the ineffectiveness of enforcement of international wildlife trade regulations. Biodiversity and Conservation 17: 35-42.

Solá, S., Garshelis, D.L., Amaral, J.D., Noyce, K.V., Coy, P.L., Steer, C.J., Iaizzo, P.A., and Rodrigues, C.M.P. 2006. Plasma levels of ursodeoxycholic acid in black bears, Ursus americanus: seasonal changes. Comparative Biochemistry and Physiology, Part C 143: 204–208.

Steinmetz, R. 2011. Ecology and distribution of sympatric Asiatic black bears and sun bears in the seasonally dry forests of Southeast Asia. Smithsonian Institution Scholarly Press, Washington, DC.

Steinmetz, R., Chutipong, W. and Seauturien, N. 2006. Collaborating to conserve large mammals in Southeast Asia. Conservation Biology 20: 1391–1401.

Steinmetz, R., Garshelis, D.L., Chutipong, W. and Seuaturien, N. 2011. The shared preference niche of sympatric Asiatic black bears and sun bears in a tropical forest mosaic. PloS ONE 6.

Steinmetz, R., Garshelis, D.L., Chutipong, W., and Seuaturien, N. 2013. Foraging ecology and coexistence of Asiatic black bears and sun bears in a seasonal tropical forest in Southeast Asia. Journal of Mammalogy 94: 1-18.

Steinmetz, R., Srirattanpon, S., Mor-Tip, J. and Seuaturien, N. 2014. Can community outreach alleviate poaching pressure and recover wildlife in Southeast Asian protected areas? . Journal of Applied Ecology 51: 1469-1478.

Stubblefield, C.H., and Shrestha, M. 2007. Status of Asiatic black bears in protected areas of Nepal and the effects of political turmoil. Ursus 18: 101–108.

Takahata C, Nielsen, S.E., Takii, A. and Izumiyama, S. 2014. Habitat selection of a large carnivore along human-wildlife boundaries in a highly modified landscape. PLoS ONE 9(1).

TRAFFIC. 2014. China’s business community leads the way in stopping the gifting of threatened species products.

Vang, S., Longley, K., Steer, C.J., and Low, W.C. 2014. The unexpected uses of Urso- and Tauroursodeoxycholic Acid in the treatment of non-liver diseases. Global Advances in Health and Medicine 3: 58–69.

Vu, Q.T. 2010. An analysis of attitudes and bear bile use in Vietnam. Education for Nature, Vietnam (ENV), Hanoi.

Wang, S.W., Lassoie, J.P., and P.D. Curtis, P.D. 2006. Farmer attitudes towards conservation in Jigme Singye Wangchuck National Park, Bhutan. Environmental Conservation 33(148–156).

Wen, C., and Wang, D. 2013. Update the status of Sun Bear in Yunnan, China. Unpublished report. International Association for Bear Research and Management.

Wu, J., Kohno, N., Mano, S., Fukumoto, Y., Tanabe, H., Hasegawa, M., and Yonezawa, T. 2015. Phylogeographic and demographic analysis of the Asian black bear (Ursus thibetanus) based on mitochondrial DNA. PLoS ONE 10(9).

Yadav, B.P., Aryal, A., Poudel, D.P., Pandey, P., and Thapalia, B.P. 2012. Asiatic black bear killed in Rara National Park, Nepal. International Bear News 21(3): 20-22.

Yamada, A., and Fujioka, M. 2010. Features of planted cypress trees vulnerable to damage by Japanese black bears. Ursus 21: 72–80.

Yamamoto, T., Oka, T., Ohnishi, N., Tanaka, H., Takatsuto, N., and Y. Okumura. 2012. Genetic characterization of northernmost isolated population of Asian black bear (Ursus thibetanus) in Japan. Mammal Study 37(85–91).

Yamanaka, A., Kiyoshi, Y., Tsunenori, T., Toshiki, M., Oi, T., Seigo, K., Shimozuru, M., and Tsubota, T. 2011. Estimating the success rate of ovulation and early litter loss rate in the Japanese black bear (Ursus thibetanus japonicus) by examining the ovaries and uteri. Japanese Journal of Veterinary Research 59: 31–39.

Yamazaki, K. 2003. Effects of pruning and brush clearing on debarking within damaged conifer stands by Japanese black bears. Ursus 14: 94-98.

Yamazaki, K, Kozakai, C., Koike, S., Morimoto, H., Goto, Y., and Furubayashi, K. 2012. Myrmecophagy of Japanese black bears in the grasslands of the Ashio area, Nikko National Park, Japan. Ursus 23: 52–64.

Yusefi G.H. 2013. Noninvasive genetic tracking of Asiatic black bears (Ursus thibetanus) at its range edge in Iran — a pilot study. M.S. Thesis. Uppsala University, Sweden.

Citation: Garshelis, D. & Steinmetz, R. 2016. Ursus thibetanus. In: (errata version published in 2017). The IUCN Red List of Threatened Species 2016: e.T22824A114252336. . Downloaded on 18 June 2018.
Disclaimer: To make use of this information, please check the <Terms of Use>.
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