|Scientific Name:||Rusa unicolor|
|Species Authority:||(Kerr, 1792)|
Cervus unicolor Kerr, 1792
Most 19th and 20th century sources placed the Sambar in the genus Cervus, as C. unicolor, but Grubb (1990) resurrected the genus Rusa for this and allied species. This was followed by Groves (2003) and Grubb (2005). Groves (2006) pointed out that Chinese Sambar has not traditionally been separated, even at a subspecific level, from Indomalayan R. u. equinus, despite karyotype differences (Groves and Grubb 1987) and some clear pelage differences, indicating that taxonomic revision may be forthcoming. Later still Groves and Grubb (2011) divided Sambar into two species, Southeast Asian Sambar C. equinus of SE Asia (including NE India) and southern China, and residual Indian Sambar C. unicolor of South Asia, based on a variety of morphological differences (no mention was made of ‘Chinese Sambar’). They gave no sample sizes or information on animals in the area where the two forms abut, making it difficult to assess the validity of the proposal. This warrants priority investigation because the distributions of the two species mean that the western form is relatively secure, with large subpopulations in many well-managed protected areas, whereas the eastern form has very few apparently secure subpopulations and would, if assessed separately, warrant a Red List Category at least one level more threatened than that for the western form.
Throughout at least Indochina there is a predictable flow of reports of ‘novel’ variation in large deer, with the implication that a new species may be involved (e.g. Pham Trong Anh et al. 1996 and, particularly, surveys through local people by overseas consultants); these stem from Sambar (often young animals) with unbranched antlers.
|Red List Category & Criteria:||Vulnerable A2cd+3cd+4cd ver 3.1|
|Assessor(s):||Timmins, R., Kawanishi, K., Giman, B, Lynam, A., Chan, B., Steinmetz, R., Sagar Baral, H. & Samba Kumar, N.|
|Reviewer(s):||González, S. & McShea, W.J.|
|Contributor(s):||Duckworth, J.W., Chakma, S., Brodie, J., Brook, S.M., Fellowes, J., Gray, T.N.E., Jathanna, D., Mudappa, D., Prakash, N., Anwarul Islam, M., Evans, T. & Hedges, S.|
Sambar is listed as Vulnerable through sustained declines across its range. These vary in severity between regions, and in some areas considerably exceed the threshold for Vulnerable. In the last three generations (taken to be 24–30 years), declines in mainland South-east Asia (Viet Nam, Lao PDR, Thailand, Cambodia, Myanmar, Malaysia), Bangladesh, and possibly Borneo and Sumatra have exceeded 50%, probably by a substantial margin. Despite this Sambar remains common in some localized logged, unprotected areas on Borneo, such as the Hose Mountains of Sarawak (where a national park is proposed but not yet enforced), but only where human access is difficult. The overall decline rate in India has been less, given the presence of large populations in a fair number of well-secured protected areas which have probably remained stable, but a decline rate averaging 30% is reasonable in India outside these areas (i.e. in the less effective protected areas and outside the protected areas network), and in Sri Lanka and Nepal. The situation in China is unclear as in some areas, for example Hainan, population recovery may be occurring, whilst major declines in other regions may have taken place prior to the 24–30 year assessment window; the population on Taiwan appears to be relatively stable. Although declines seem to be reversing very locally in a few sites, these numbers are a very small proportion of the whole population. There is no indication that declines will, at the species level, slow until populations are extinguished outside well-secured protected areas, which currently comprise only a small proportion of protected areas holding the species. Current trends of wild meat and antler marketing in South-east Asia and China suggest declines have probably sped up in some areas especially Lao PDR, Cambodia and Viet Nam. Since the 2008 assessment trends in wildlife exploitation and natural habitat conversion in mainland Southeast Asia, have if anything increased, thus although the relative size of the Southeast Asian population subcomponent has probably decreased compared with that in South Asia, the rate of decline has probably increased. The global population trend is still considered to be a decline somewhere between 30 and 50 % over three generations, for the past, present and future. The fact that Sambar is at least locally common in a number of high profile protected areas, such as Khao Yai National Park, Thailand and Cat Tien National Park, Viet Nam, and is commonly kept captive and proliferates in menageries in the region, was probably a significant factor in the failure to recognize the plight of the species prior to the 2008 reassessment. These same factors no doubt still to some degree cloud the issue.
|Previously published Red List assessments:|
|Range Description:||The Sambar extends from India and Sri Lanka east along the southern Himalayas (including Nepal and Bhutan) through much of south China (including Hainan Island) to Taiwan (where it occurs in the central and eastern parts; Lin, C.-Y. and Lee, L.-L. pers. comms. 2008). Further south it occurs in Bangladesh, throughout mainland Southeast Asia (Myanmar, Thailand, Lao PDR, Cambodia, Viet Nam, West Malaysia) and many of the main islands of the Greater Sundas (excepting Java): Sumatra, Siberut, Sipora, Pagi and Nias islands (all Indonesia), and Borneo (Malaysia, Indonesia, and Brunei) (Grubb 2005). The current distribution is now highly fragmented in much of this range (see Population). Payne et al. (1985) also listed the Philippines, but the Sambar does not occur there. A record from Ujung Kulon, Java, in van Schaik and Griffiths (1996: 107) is presumably an error for Javan Deer R. timorensis. The Sambar has been introduced widely outside its native range, e.g.: San Luis Obispo Country, California; the Gulf Prairies and Edwards Plateau regions of Texas (Ables and Ramsey 1974); the St. Vincent Islands, Franklin Country, Florida (Lewis et al. 1990); Australia (Slee 1984, Freeland 1990); New Zealand (Kelton and Skipworth 1987); and Western Cape Province, South Africa (Lever 1985). These introduced populations are not included on the distribution map.|
Native:Bangladesh; Bhutan; Brunei Darussalam; Cambodia; China (Guangxi, Guizhou, Hainan, Hunan, Jiangxi, Sichuan, Yunnan); India; Indonesia (Sumatera); Lao People's Democratic Republic; Malaysia; Myanmar; Nepal; Sri Lanka; Taiwan, Province of China; Thailand; Viet Nam
Introduced:Australia; New Zealand; South Africa (Western Cape); United States (California, Florida, Texas)
|Range Map:||Click here to open the map viewer and explore range.|
Almost everywhere outside Taiwan and well-managed protected areas in India, the Sambar is in rapid decline, which has lead to very low numbers and many local-level extinctions over a wide area. The occasional healthy populations reflecting special circumstances. Few surveys specifically target Sambar, but a reasonable picture of its current status is emerging through surveys for Tiger Panthera tigris and through general wildlife surveys. Tiger-oriented camera-trapping predictably yields photographs of Sambar when it is present, and most Tiger surveys afford priority to elucidating Sambar status as a key prey, and therefore population determinant, of Tiger. Understanding Sambar status through surveys of Tigers or, sometimes, of Leopard P. pardus (e.g. Ngoprasert et al. 2007) needs care, because such surveys have generally selected the best remaining areas for very large mammals within the country or region in question, so as to maximize chances of picking up Tigers. They therefore cannot be seen as indicative of Sambar status in the wider landscape. Most importantly, in the several cases (identified below) where such surveys have found few Sambar, these indicate cause for alarm, because there is little reason to believe that there ought to be larger populations in many other areas in the country or region in question, even though large parts of it may remain unsurveyed. Occasional herds can survive in unexpected places through atypical site-specific circumstances in some countries (e.g. Tungittiplakorn and Dearden 2002). Populations outside the native range are not treated here, as they are irrelevant to assigning the Red List Category and Criteria.
In Sri Lanka, numbers have probably declined substantially through poaching which increased during the civil war. Poaching occurred widely across the country, including within protected areas, particularly where there are concentrations of resettled refugees (Santiapillai and Wijeyamohan 2003).
In other central and east Indian states Sambar is “very rare”, “extremely patchy and in severe decline” “owing to severe hunting pressures, insurgency, rapidly spreading mines (both bauxite and iron-ore)” (N. Prakash pers. comm. 2014).
The reported ecological densities of Sambar in India mostly fall within 1–10 animals per km2 within the protected area network, and depending on the varying levels of protection efficacy: Bhadra Tiger Reserve, 0.89 +/- 0.23 (SE) per km2 (Jathanna et al. 2003); Madhya Pradesh Pench National Park dry deciduous forest, 9.6 animals per km2 (Karanth and Nichols 2000); Kanha moist deciduous forest, 1.5 animals per km2 (Karanth and Nichols 2000); Nagarahole moist deciduous forest, 5.5 animals per km2 (Karanth and Sunquist 1992); Bandipur dry deciduous forest, 5.6 animals per km2 (Karanth and Nichols 2000); Tadoba-Andhari dry deciduous forest, 3.3 animals per km2 (Karanth and Kumar 2005); Melghat dry deciduous forest, 2.7 animals per km2 (Karanth and Kumar 2005); Maharashtra Pench dry deciduous forest, 5.9 animals per km2 (Karanth and Kumar 2005); Ranthambore semi-arid dry deciduous forest, 10.7 animals per km2 (Kumar 2000); and Gir semi-arid dry deciduous forest, two animals per km2 (Khan et al. 1996). Similar surveys at Kaziranga found too few Sambar to estimate populations there (Karanth and Nichols 2000), this presumably representing habitat characters rather than defective protection, given the buoyant populations of other deer at that site (Hog Deer Axis porcinus and Barasingha Rucervus duvaucelii). The recorded Bhadra density is low, reflecting poaching and forest-resource extraction (Jathanna et al. 2003), and the population density is steadily increasing following removal of these pressures in 2003 (K.U. Karanth and N.S. Kumar unpublished data as of 2008). Local population trends in well protected reserves appear to be stable and even increasing in areas recently freed from anthropogenic pressures (D. Jathanna pers. comm. 2014). But in poorly protected reserved forests subject to hunting and heavy cattle grazing, Sambar density seems to be extremely low; certainly too low to permit actual estimation of density (D. Jathanna pers. comm. 2014). Outside protected areas, Sambar is present mostly in very low numbers, although larger numbers can still be found where its habitat is almost inaccessible to people (Anonymous 2008).
In China there were major declines in Sambar over much of the twentieth century, and populations probably decreased by more than 50% in the 30 years from 1978 to 2008; records from Guangxi suggest that, there at least, the 1970s–1980s was the era of fastest decline (J. Fellowes pers. comm. 2008; B.P.L. Chan pers. comm. 2008). In some provinces populations seem now to have stabilized, and in some areas, particularly in Hainan (where several apparently stabilised populations are present, but all are small, reflecting habitat patch size: the largest may be of only a few hundred animals) and north Guangdong province (perhaps also the east of that province, where there is a nature reserve specifically for the species), populations may even have been increasing once again in the last few years. This is not so for Guizhou, Guangxi, Guangdong and Yunnan (B.P.L. Chan and M.W.N. Lau pers. comm. 2008). Further north, in the provinces of Fujian, Jiangxi, Zhejiang, Hunan and Hubei, a multi-method Tiger survey in 2001 found that Sambar is very rare overall and scattered in present-day distribution (Tilson et al. 2004). For elsewhere in China, Smith and Xie Yan (2008) mapped wide presence in Sichuan, plus isolated populations in the provinces of Qinghai, Tibet, Chongqing, and Fujian. The original sources are not clear, and R. Harris (pers. comm.) doubts that Sambar has lived anywhere in Qinghai in recent times.
Camera-trapping and sign-based survey studies in Taman Negara NP have independently corroborated declines in Sambar numbers between c. 2000 and 2010 (Kawanishi et al. 2014). Crude density estimates based of photographic capture-recapture analysis of individually recognizable stags (Kawanishi and Sunquist 2004) declined from 0.20 to 0.01 animals per km2 while the occupancy estimate declined from 0.54 to 0.19 in Taman Negara. It is possible that the Sambar density was always low in the primary rainforest but the species is now extirpated in a forest reserve and disturbed unprotected forest adjacent to the Taman Negara sampling area (K. Kawanishi pers. comm. 2014).
An analysis of potential Sambar range in West Malaysia calculated a c. >25% loss of potentially suitable forest between 1980 and c. 2010 (DWNP 2010). Serious recent declines are also corroborated by an interview survey of hunters in which over 80% of 61 interviewees from throughout Peninsula Malaysia considered declines had occurred (Goldthorpe and Neo 2011), and a decline in the number of hunting licences issued for Sambar (Kawanishi 2008, Kawanishi et al. 2014). Even within protected areas enforcement of hunting laws is lax and poaching rife, except for a very few areas including the Endau-Rompin landscape and Royal Belum State Park which are relatively intensively patrolled (Kawanishi et al. 2014). Sambar is a favoured quarry species, found on the menu in a significant number of restaurants, with evidence that poaching is increasing both in the intensity and the number of hunters involved (Kawanishi et al. 2014).
Camera-trapping between 2010 and 2012, in eight sites in Sabah and Sarawak found Sambar in every one, often reasonably common (Brodie et al. in press, J. Brodie in litt. 2014). Sambar appears to remain fairly common in three of the eight sites, the Maliau Basin and Danum Valley in Sabah, where protection from hunting is reasonably good and the Hose Mountains of Sarawak which are relatively inaccessible (Brodie et al. in press a, b, J. Brodie in litt. 2014). Sambar was found to be present but uncommon in the remaining areas of Mulu National Park (Sarawak), Pulong Tau National Park (Sarawak), the Ulu Padas region (Sabah), the Ulu Trusan region (Sarawak), and the Ulu Baram (Sarawak) (Brodie et al. in press, J. Brodie in litt. 2014). Heydon (1994) also reported good populations from Danum Valley, suggesting a reasonably stable population there. Other populations previously reported to be in reasonable condition include those in Tabin Wildlife Reserve (Matsubayashi and Sukor 2005), and Deramakot Forest Reserve (Matsubayashi et al. 2007) both in Sabah. Sambar has been extirpated or persists only at extremely low densities in Lambir Hills National Park, Sarawak, Malaysia (Azlan and Engkamat Lading 2006). An intensive survey of Batang Ai National Park, Sarawak, found Sambar only once; this was stated to be a genuine reflection of actual rarity, and to result from intensive hunting at salt-licks (Meredith 1995). Across Sarawak and to a lesser extent Sabah it is seriously reduced by hunting (Bennett et al. 2000, see Threats; A.C. Sebastian pers. comm. 2008), although persistence is probably still widespread (J. Brodie in litt. 2014).
In the Indonesian part of Borneo populations seem to be less depleted, particularly in East Kalimantan, which is believed to hold the largest Sambar populations among all Kalimantan provinces; in the Penajam Paser Utara district of East Kalimantan, approximately 60 hunted animals are sold monthly in several traditional markets (Semiadi et al. 2004, G. Semiadi pers. comm. 2008).
In Indonesia, there are various recent records from Sumatra, e.g. Bukit Barisan Selatan National Park (O'Brien et al. 2003), Gunung Leuser (van Schaik and Griffiths (1996), and Way Kambas National Park (S. Hedges pers. comm. 2008), but in these areas it was recorded rather rarely by comparison with other ungulates. Sambar was nearly six times as abundant in areas of Bukit Barisan Selatan National Park with low than with high human population density within 10 km of the park boundary, suggesting low resilience to human presence, presumably the effects of hunting, and reduced populations overall (O'Brien et al. 2003). In Way Kambas National Park the population is reportedly stable (G. Semiadi pers. comm. 2008). Overall in Indonesia (Sumatra and Borneo), Sambar is not under major threat except where forest is being converted (i.e. most of the lowlands). Reflecting this, E. Pollard (pers. comm. 2008) considered the status of Sambar, in suitable habitat, to be much more healthy there than in Cambodia and Viet Nam, although there is a significant market for Sambar antlers in Sumatra (D. Martyr pers. comm. 2008).
|Current Population Trend:||Decreasing|
|Habitat and Ecology:||No large Indian ungulate has adapted itself to a wider variety of forest types and environmental conditions than has Sambar (Schaller 1967). Within India, Sambar occurs in the thorn and arid forests of Gujarat and Rajasthan, in the moist and dry deciduous forests throughout peninsular India, in the pine and oak forests at the Himalayan foothills, and in the evergreen and semi-evergreen forests of northeastern India and the Western Ghats (Sankar and Acharya 2004, N.S. Kumar pers. comm. 2008). Outside India it extends into temperate-latitude and alpine-zone woodlands of Taiwan (Lin, C.-Y. and Lee, L.-L. pers. comm. 2008). This habitat flexibility is permitted by its broad diet: Sambar has been documented to eat 130–180 species of plants in India alone (Schaller 1967, Johnsingh and Sankar 1991, N.S. Kumar pers. comm. 2008), with food requirements less specialised than those of other deer (Schaller 1967). Sambar grazes or browses depending upon the forage available at that time (Schaller 1967, Richardson 1972, Martin 1977, Bentley 1978, Dinerstein 1979, Kelton and Skipworth 1987, Ngampongsai 1987, Sankar 1994, Semiadi et al. 1995). Across the very wide altitudinal range occupied in Taiwan, the diet varies reflecting major changes in plant communities (Lin, C.-Y. and Lee, L.-L. pers. comm. 2008). Sambar was found to live in much higher densities in moist than in dry deciduous forests of Nagarahole National Park (Karanth and Sunquist 1992) and there are no doubt also patterns of habitat selection across the rest of its range. Although the highest densities of Sambar so far recorded were in the semi-arid forests of Ranthambore (Kumar 2000), across most of its Indian range Sambar seems to thrive best in well-watered, moist deciduous hilly terrain (N.S. Kumar pers. comm. 2008).|
The Sambar occurs up to at least 3,825 m on Siouguluan Mountain, the highest peak of the Central Mountains in Taiwan; elsewhere on the island it ranges down to 150 m asl, mostly living at 2,000–3,500 m (Lin, C.-Y. and Lee, L.-L. pers. comm. 2008). It occurs up to 3,000 m on Gunung Kinabalu, Sabah, Borneo (Payne et al. 1985). In Myanmar, recent camera-trap photographs spanned the range of 0–2,150 m asl (Saw Htun pers. comm. 2008). Sambar is largely restricted to hilly terrain in the Terai Arc Landscape (Johnsingh et al. 2004), although how much this reflects real habitat selection and how much it is an artificial pattern produced by human effects (habitat conversion and hunting) is unclear. More widely in India, there does seem to be a marked preference for undulating terrain (N.S. Kumar pers. comm. 2008). Kushwaha et al. (2004) found that in Kumaon Himalaya (India), Sambar usage was greater of the higher than the lower altitude area. However, it makes wide use of plains areas elsewhere, where these have not been destroyed, e.g. the Hukaung Valley in Myanmar (J.W. Duckworth pers. comm. 2008).In Borneo, while Payne et al. (1985) considered Sambar “most common in secondary forests of gently-sloping terrain” they also knew of occurrence in “tall dipterocarp forests on steep terrain and in swamp forests”. In Thung Yai, Thailand, Sambar signs were twice as abundant in lowland forest as in montane forest, although this difference was not statistically significant (Steinmetz et al. 2008). Across seven sites in Thailand, places where sambar was detected had shallower slopes, more open habitat, were closer to streams, closer to roads and villages, and had lower rainfall (Lynam et al. 2012).In Southeast Asian regions of dense evergreen closed-canopy forest, Sambar is highly tolerant of forest degradation: indeed, much higher numbers are found in encroached stands than in pristine forests, if hunting is under control (Rijksen 1978, Heydon 1994, Stuebing 1995, Davies et al. 2001). In Sabah, Sambar was camera-trapped in both mature and young forest stands (Matsubayashi and Sukor 2005). All the remaining Lao populations are centred around areas with extensive open, or at least broken, habitat amid forest (Duckworth et al. 1999), and the general paucity of records from the interiors of large blocks of closed-canopy evergreen and semi-evergreen forests, which generally support the least depleted large mammal populations, probably reflects natural patterns of habitat occupation (R.J. Timmins pers. comm. 2008). Similarly, in extensive tracts of deciduous dipterocarp forest the species occurs primarily around patches of denser habitats, and this seems to be a natural rather than hunting-led pattern (Timmins and Ou 2001). In this sense, in Indochina Northern Red Muntjac Muntiacus vaginalis is much more tolerant and versatile than is Sambar. In southern and central India where much of the forest is deciduous, Sambar is a true forest ungulate and conspicuously avoids disturbed and open forests, and is highly sensitive to any sort of forest resource extractive activities (N.S. Kumar pers. comm. 2008). Kushwaha et al. (2004) found that in Kumaon Himalaya (India), Sambar was primarily in areas of high tree and herb density with low shrub density. O'Brien et al. (2003) found no statistically significant difference in Sambar abundance between areas within 1 km inside the boundary of Bukit Barisan Selatan National Park, Sumatra, and those deep in the interior of the park. Caution is needed in inferring that there is truly no association of Sumatran Sambar with forest edges (which would be astonishing by comparison with its habitat use elsewhere) because the study does not specify whether this ‘non-significant’ result might simply reflect methodological factors rather than a genuine lack of biological effect (see, e.g., Johnson 1999). Despite the population rises that occur in post-logging forest, there is no evidence that Sambar can survive landscape-level conversion to exotic plantations or other non-forest land-uses, although many live in coconut plantations (G. Semiadi pers. comm. 2008) and it is relatively common in immature Acacia mangium plantations within the matrix of plantation and natural forest of the Sarawak Planted Forests area, Bintulu (B. Giman pers. comm. 2008). Camera trapping in oil palm plantations adjacent to Danum Valley in Sabah suggest that the species does not utilize plantations (Yue and J. Brodie unpublished data).A study of coffee estates around Bhadra Wildlife Sanctuary, India, recorded Sambar only in those coffee areas within 1 km of the sanctuary’s boundary (Bali et al. 2007). In forest protected areas of Thailand such as Khao Yai National Park and Phu Khieo Wildlife Sanctuary, Sambar populations are often concentrated around anthropogenic grass and scrub (e.g. sites of former villages) rather than in the forest itself (Trisurat et al. 1996; Lynam et al. 2001) and this also seems to be true on remote parts of the Bolaven Plateau of south Lao PDR (Evans et al. 2000). In the Annamite mountains of Lao PDR and Viet Nam, Sambar seems often to be associated with degraded valley bottom areas, largely the result of long human influence: although the effects of a permanent water source and differences in terrain in determining distribution are difficult to disentangle (R.J. Timmins pers. comm. 2008).
Sambar regularly visits salt licks (e.g. Matsubayashi et al. 2007), perhaps especially when growing new antlers. This predictability exposes it to high levels of hunting, where this is not effectively controlled. It seems that within an area, not all sort of licks are visited. At the Seima Biodivesity Conservation Area, Cambodia, Sambar photographs were initially very few at mineral lick camera-traps. But in 2007, cameras placed on trails and at some permanent water sources (especially in semi-evergreen forest) recorded Sambar much more often. Checking tracks at more than 40 licks indicated that some were used by Sambar and Red Muntjac, but not Gaur Bos gaurus or Asian Elephant Elephas maximus, while the big ones with many cattle and elephant prints had few Sambar prints (E. Pollard pers. comm. 2008).
Sambar was considered to be mostly nocturnal by Kawanishi and Sunquist (2004), to show ‘no pattern’ (meaning unclear; perhaps intended to imply no significant variation through the 24-hour cycle, although this is itself a pattern) by O’Brien et al. (2003), and to be cathemeral by van Schaik and Griffiths (1996). In fact, its activity pattern may vary across sites, but in general it is mostly crepuscular, with significant nocturnal activity as well (Schaller 1967; J.W. Duckworth pers. comm. 2008). Sambar is essentially non-social, stable groups being at most family associations (Schaller 1967; Karanth and Sunquist 1992). However, it is often in groups, presumably temporary, of 12–30 in dry deciduous and semi-arid forests of India (e.g. Bandipur, Pench, Melghat and Ranthambore) (N.S. Kumar pers. comm. 2008), and the same is true around the secondary grasslands within Khao Yai National Park, Thailand (J.W. Duckworth pers. comm. 2008). During peak summer, such associations of up to 80–100 near large waterbodies are not uncommon in Pench in central India (N.S. Kumar pers. comm. 2008). A detailed review of information on grouping in Sambar is in Sankar and Acharya (2004). Results from many areas show a strong bias in sex ratio to females, perhaps reflecting selective predation; alternatively, stags may be more vulnerable to stress (Sankar and Acharya 2004).
Breeding is rather seasonal in most areas where studied, for example Schaller (1967) reported that in Kanha the rut spreads over a period of at least seven months with a peak in November–December. Stags during the rut sometimes can cover large distances, up to 10–20 km in one night. Further information for India is reviewed in Sankar and Acharya (2004). The bucks of Formosan Sambar have a seasonal antler cycle, and the mating season is from June to January with a peak in September–October. Males wallow and mark with scent glands in this season. Fawns are born (usually singly) from March to August, with a peak in May and June (Lin, C.-Y. and Lee, L.-L. pers. comm. 2008).
Predation appears to be the major cause of Sambar mortality. In Bandipur, Sambar is one of the most important prey in terms of the biomass taken by Tiger Panthera tigris (31%), Leopard P. pardus (8%) and Dhole C. alpinus (13%) (Andheria et al. 2007). In Bandipur Sambar remains were found in about 22.3% of Tiger faeces, 6.1% of Leopard faeces and 7.3% of Dhole faeces (Andheria et al. 2007). In adjoining Nagarahole, proportion of Sambar in Tiger’s diet was about 25–29%, derived from faeces and kill data respectively (Karanth and Sunquist 1995). In Tadoba-Andhari, Sambar together with Gaur contributed to nearly 70% of the prey biomass consumed by Tiger, whereas in Pench-Maharashtra it was 80% (Karanth and Kumar 2005). Sambar occurred in 50% of Tiger scats in Pench-Maharashtra (Karanth and Kumar 2005). In well protected forest reserves where different body-sized ungulates are abundantly available, Sambar together with Gaur are selectively predated by Tiger.
|Generation Length (years):||8-10|
|Use and Trade:||The Sambar is hunted for sport, food, medicinal products and other purposes. It is uncertain how many captive animals are kept within the native range, potentially larger herds occur in countries where introduced, and the comparative contributions of wild and captive sourced products to markets is unknown - the markets may be somewhat separate.|
Habitat encroachment and hunting are both widespread in the Sundaic region and in much of the rest of Sambar’s range. Indeed, these two threats are often associated and all Borneo’s ungulates suffer from the increased hunting that often accompanies logging (Bennett and Dahaban 1995, Bennett and Gumal 2001), such that hunting to local extinction is the chief detrimental effect of logging on ungulates in Sarawak (Bennett and Gumal 2001). This conclusion probably is applicable across the range of Sambar, within which it is heavily hunted (e.g. Duckworth et al. 1999, Walston 2001, Tungittiplakorn and Dearden 2002, Linkie et al. 2003, Santiapillai and Wijeyamohan 2003, Tilson et al. 2004, Rao et al. 2005, Steinmetz et al. 2008, Saw Htun pers. comm. 2008). It is among the most sought-after wild meats in Indonesia (Semiadi 2005), Sarawak (Belden Giman pers. comm. 2008), and Viet Nam (B. Long pers. comm. 2008), and during 1988–1993 it was a common and preferred food in rural Lao PDR (Duckworth et al. 1999, Table 1), and is probably near the top of chosen wild meats throughout most of its range (GMA Indonesia workshop); however, it is less favoured in Taiwan compared with Formosan Serow Capricornis crispus and Reeves’s Muntjac Muntiacus reevesi (Chang Shih-Wei pers. comm. 2008). However, it is now so rare in Nam Ha National Protected Area, Lao PDR, that a more recent hunting study found it to be eaten only rarely (Johnson et al. 2003). In Viet Nam, muntjac meat is now often served in wildlife restaurants as Sambar, because real Sambar meat is now so difficult to procure (B. Long pers. comm. 2008). These declines in consumption are probably representative of all Lao PDR and Viet Nam, and of increasing proportions of the rest its range, reflecting population losses (see Population).
There are major, ongoing, declines in at least Viet Nam, Lao PDR, Cambodia, Thailand, Malaysia, Myanmar, Bangladesh and Nepal, and probably Sri Lanka and Indonesia (see Populations) which can plausibly only be driven by hunting, because suitable habitat for Sambar is abundant in these countries but is almost or actually bereft of the species. Even in India, poaching has seriously depleted the abundance of large mammals in most areas; even in high-profile areas such a Corbett Tiger Reserve and Rajaji National Park there are still some instances of poaching (Johnsingh et al. 2004). An intensive study of hunting on mammals in two Hmong villages of northern Thailand classified quarry species into tiers representing the sequence of loss through overhunting; Sambar fell in the second tier (aside, e.g., big cats Panthera) in the extinction sequence (Tungittiplakorn and Dearden 2002). This study found that Sambar persisted anomalously long in one place under an “exceptional village wildlife hunting regulation promulgated by the village headman until 1994”, but was generally extinct in the landscape. A study at Nagarahole National Park compared an area which was only moderately hunted with a heavily hunted site, but found no significant difference in Sambar densities between the two areas (Madhusudan and Karanth 2002). This was speculated to reflect the greater difficulty of hunting Sambar (highly dispersed and usually in rather thick vegetation), despite it being a prized species, than, particularly, Chital Axis axis, a herding species often out in the open, and the benefit to poachers of getting in, making a kill, and getting back out again as fast as possible to reduce detection chances; therefore, this pattern seems to have arisen through hunter choice. In the context of Indochina, even the heavily-hunted site would, however, rank as lightly hunted (J.W. Duckworth pers. comm. 2008, based on visit and discussion). For these two reasons, their finding, of an apparent high resilience of Sambar to hunting, is not applicable to the rest of the species' range (particularly outside well-secured protected areas). However, somewhat reflecting this, Sambar’s status in non-Sundaic South-east Asia (still widespread but in ongoing steep decline) relative to other large deer ecologically more similar to Chital (herding; often outside dense forest), Eld’s Deer Rucervus eldii and Hog Deer Axis porcinus (extinct across most of their former range through former steep declines) does indeed suggest a broad applicability of a conclusion that Sambar is somewhat less rapidly reduced by hunting than are other sympatric deer, excepting muntjacs Munitacus spp.
Deer are hunted in India using snares, dogs, and guns (Jathanna et al. 2003; Kumara and Singh 2004) and these methods are general across their range. Some hunting is for village consumption of meat, but most (at least in South-east Asia) is probably sold commercially, to the affluent urban classes (e.g. Duckworth et al. 1999, Walston 2001, Kumara and Singh 2004), and to itinerant labourers, such as logging crews in at least Sarawak (Bennett and Gunal 2001) and gold-diggers and rattan-cutters in Myanmar (in Myanmar (A. Lynam pers. comm. 2014 based on observations in 2002, J.W. Duckworth pers. comm. 2008). Such commercially-driven hunting causes major declines (e.g. Steinmetz et al. 2008) because the market is limitless. Adult males suffer additionally because antlers are widely displayed as trophies and are used in traditional medicine (e.g. Martin 1992, Baird 1995). At least in Lao PDR, their market value means that, compared with muntjacs, a high proportion is sent to towns and traded internationally, and many are sold openly in tourist centres such as Louangphabang (Duckworth et al. 1999). In Taiwan, in the past live males were sought for farming velvet; this was far more valuable than the meat. Presently, velvet can be bought legally and cheaply from farms and hunting for velvet is now insignificant, as is, here, hunting for internal organs (Chang Shih-Wei pers. comm. 2008). Hunting pressures and patterns vary across Sambar’s range: three areas (Indochina; Malaysian Borneo; Taiwan) are profiled below, and all are very different not just from each other, but from southern and central India, where (excepting Taiwan) the species has by far the healthiest conservation status. But even across India, hunting for Sambar meat is almost ubiquitous, even occurring within well-secured protected areas, and to greater extents in other protected areas and outside the protected area system (N.S. Kumar pers. comm. 2008).
Viet Nam, Lao PDR and to a lesser extent Cambodia and northern Thailand are apparently the areas of Sambar’s range where generalised mammal hunting is heaviest. Sambar is hunted within a thriving hunting and wildlife trading culture in this area and in adjacent countries such as China and Thailand, involving many land vertebrate species, along with other forest products such as orchids and Aquilaria resin (e.g. Compton and Le Hai Quang 1998, Compton et al. 1999, Noreen and Claridge 2001, Smith and Xie Yan in press). Such hunting reaches all areas, although in large rugged mountain forest blocks trade-driven hunting of species valued only for their meat (rather than high-value, low-weight, generally medicinal products that can be carried out efficiently from even the remotest areas) is still limited by economics of accessibility. However, the ability of these areas to protect Sambar at the regional scale is questionable, because no areas of rugged evergreen forest are known with high Sambar densities: such habitat is rather marginal. The regional wild meat trade has little likelihood of abating as long as there are any of the most resilient species (pigs, muntjacs, and civets) to be hunted. The human population of Viet Nam is more than 84 million, that of China more than 1,000 million. Together, they comprise an enormous market for wildlife products. For example, tens of millions of wild turtles are imported, legally and illegally, into China annually (van Dijk et al. 2000 and papers therein). There has been no comparable study of ungulate trade levels. Within the Northern and Central Annamites, every square kilometre of Viet Namese forest and of Lao forest that is within 5 km of the Viet Namese border probably has snares capable of capturing Sambar set in it every year (Timmins et al. 2007; R.J. Timmins pers. comm. 2008). Intensity in some areas probably reaches many thousands of snare-nights per km2 per year (Timmins et al. 2007). Snaring is less intensive in Lao PDR at least away from the Vietnamese border, but is increasing dramatically (Timmins and Robichaud 2005; W.G. Robichaud pers. comm. 2007; R.J. Timmins pers. comm. 2008, 2014). Hunting intensity has in recent decades been generally lower in southern Viet Nam than in Lao PDR and northern Viet Nam, leaving many wildlife populations less depleted (e.g. Le Xuan Canh et al. 1997, Timmins and Duckworth 2000, Polet and Ling 2004 ), but the general increase in regional hunting intensity and economic wealth indicate that hunting intensity in this region must also be increasing, as suggested by a recent survey of forest in Dak Nong Province which detected Sambar only once and found many indications of extremely high hunting pressure (Timmins in press). Rapid economic development and expanding wealth, particularly Southeast Asia and China, are increasing the demand for wildlife meat and ‘medicines’ (e.g. TRAFFIC et al. 2008). Timmins et al. (2007) highlighted a common misconception, especially in documentation of development projects in the region, that poverty is a principal cause of biodiversity loss: as they pointed out for Saola Pseudoryx nghetinhensis, the main driver of threats to wild ungulates in Indochina, at least for the mid-term, is not rural poverty but increasing urban wealth in Indochina and China. In Viet Nam “the free market economy has resulted in feverish periods of trade in wild species nationwide, with negative impacts on biodiversity” (Government of the Socialist Republic of Viet Nam 2004). In Cambodia, the same factor has fostered a thriving bushmeat market and hunting of species for international wildlife trade (Timmins and Ou 2001, Timmins 2006, Maxwell et al. 2007), and the intensity of hunting there for some species (Sambar included) is likely to exceed even that in Viet Nam. This reflects the logistical ease of hunting and trading with few controls and the relative abundance of high-value quarry species (R.J. Timmins pers. comm. 2008). There is a rapid, ongoing, expansion of wealthy social strata in Lao PDR, Cambodia, and Viet Nam, directly accelerated by illegal trade in timber, wild meat, and other forest resources, and by the economics of large infrastructure projects (e.g. Nan Theun 2 hydro-electric power project), creating a significantly greater in-country demand for luxury meats such as venison (W.G. Robichaud pers. comm. 2007). Markets along major roads such as route 13 through Lao PDR (e.g. at Ban Namthon) have expanded, not contracted, in the last 15 years (up to 2008) and have a huge (albeit unquantified) turnover of wild meat; at this specific market, multiple stalls are selling dried deer meat daily. The effects of hunting in Lao PDR, Viet Nam, Cambodia and Thailand have been exacerbated during the last two decades by habitat loss and various socio-economic factors, of which the most biologically significant are discussed in the Red List account for Large-antlered Muntjac M. vuquangensis (Timmins et al. 2008). The most significant constraint to Indochina’s Sambar populations is the long-term uncertainty of success in protected areas, even in those currently effective in conservation management. Even the most successful protected areas face an uncertain future with the possibility of degazettement of conservation status of parts of them, the lack of, or possible future loss of, adequate external funding necessary to maintain high standards of management, the lack of, or possible future loss of, political support necessary to uphold high protection standards and the uncertainties of maintaining a motivated and well-trained staff.
On Borneo, Sambar is also widely and heavily hunted, largely for meat consumed in-country (Bennett et al. 2000, Mohd Azlan J. pers. comm. 2008, Belden Giman pers. comm. 2008, G.M. Fredriksson pers. comm. 2008, A.C. Sebastian pers. comm. 2008, Siew Te Wong pers. comm. 2008). Traditionally, hunters used traps, dogs and spears, and blowpipes. Hunters in remote parts of the interior still use these methods, but most animals now die by gunfire. Sarawak held 60,000 legally registered shotguns while Sabah held almost 13,000 in the mid 1990s (Bennett et al. 2000). Methods used in Indonesia include guns and spotlights along logging roads, snaring, and dogs (G.M. Fredriksson pers. comm. 2008, S. Hedges pers. comm. 2008). Snaring is still very heavy outside well-secured areas, but shotguns remain the even bigger problem (Bennett et al. 2000, Mohd Azlan J. pers. comm. 2008, A.C. Sebastian pers. comm. 2008, Siew Te Wong pers. comm. 2008). Over most of (at least) Malaysian Borneo, “in general, everyone will hunt and eat anything” (Bennett et al. 2000). Much hunting is for the market rather than local use, so there is a limitless demand. Bennett et al. (2000) and Bennett and Gumal (2001) profiled the hunting of ungulates in Sarawak in the mid 1990s thus: Sambar (along with Bearded Hog Sus barbatus and muntjacs Muntiacus) is heavily shot for wild meat trade across Sarawak, and these ungulates are the species most sought by the restaurants; Sambar in particular is an important source of meat for logging company employees in Sarawak. Wild meat is widely sold in towns, villages, restaurants and logging camps throughout Sarawak; 250 sales outlets were estimated across the state in 1996, with an annual trade worth 3.75 million USD. Along the Rejang river alone, in the mid 1980s, 1,500 Sambars were sold per year (Caldecott 1988). The market for meat is great and probably expanding. Bennett et al. (2000) considered the effects of this onslaught upon Sambar through a lengthy hunting study in February 1993 to June 1995, in both Bornean states of Malaysia (Sarawak and Sabah), each with eight study areas. Sambar constituted only 6.7% of animals killed in Sabah, but 35% by weight of wild meat; negligible numbers were taken in Sarawak, reflecting the major declines that had already reduced the species to rarity. Index counts of signs show an inverse relationship between sign index and hunting pressure so strong that the latter over-rode the effects of habitat variables in determining their densities. Hunting was so ubiquitous, even in protected areas, that in the two states, only one site (part of Danum Valley, Sabah) could be found as a control, where there was primary forest but negligible hunting levels. They concluded that “the only single factor offering any effective protection for [quarry species of] wildlife is difficulty of access”; whether animals are protected or non-protected species, inside or outside protected areas, had no significant restraint on hunting levels. There were, then, no official controls on commercial hunting of non-protected species. The Master Plan for Wildlife in Sarawak (Wildlife Conservation Society and Sarawak Forest Department 1996) introduced a strict ban on all wildlife trade, shotgun ownership and cartridge sales in the late 1990s (Bennett and Gumal 2001). Substantial numbers of Sambars are, nevertheless, still killed in the state, as they are elsewhere in Borneo. Although locally selective logging has probably benefited Sambar populations in some areas by creating more favourable habitats (e.g. Brodie in press b, c), and potentially increasing carrying capacity, the indirect effects of logging undoubtedly greately outweighs any potential benefit (Bennett and Gumal 2001). Moreover, in the interim since the Master Plan, much forest has been completely lost and Sambar populations in the smaller and more isolated areas that remain must now be even more vulnerable to local extinctions. For most Sambar populations inaccessibility is still essentially the only real protection for the species, and there are few inaccessible areas left (J. Brodie in litt 2014).
In a study area of almost half a million hectares in Sarawak Sambar detection probability declined by almost 40% between 2008-2014 (B. Giman pers. comm. 2014). This apparent decline coincided in part with harvesting of Acacia mangium although as of 2014 harvesting activity had only affected a few plantation compartments. The decline was also attributed to uncontrolled illegal hunting; prior to harvesting few people were involved in plantation activity, but for the period 2012-2014 many workers were brought in, and this resulted in many people hunting on a nightly basis. Additionally the harvesting activity destroyed an important mineral lick (B. Giman pers. comm. 2014).
Taiwan contrasts with the rest of Sambar range in that hunting has been so successfully reduced that populations are now increasing in large parts of the island. It was formerly a big problem, for venison and, for medicinal purposes, velvet and penis. The reduction during and since the 1990s reflects five factors. Hunting of Sambar was banned in 1989 through the Wildlife Conservation Act. Velvet prices fell steeply during 1985–1990 with deer TB in 1985, reducing returns from poaching absolutely an effect exacerbated by rapid economic development in 1980s leading to higher daily wages. Former logging road systems are deteriorating within protected areas, making removal of deer meat less attractive. The general awareness of ecological conservation has much enhanced. And eco-tourism through community forestry plans has given alternative employment to former hunters (all information: Lin, C.-Y. and Lee, L.-L. pers. comm. 2008).
Over many centuries, the loss of wilderness to human settlement, cultivation and industry has resulted in massive loss of potential Sambar range, particularly in the densely-settled countries of India, China, Bangladesh, Thailand, and Viet Nam. Throughout the range of Sambar, natural and semi-natural habitats (forest, shrubland and grassland) continue to be converted to anthropogenic habitats, degraded (e.g. stands are being changed in character through logging) and fragmented (broken into smaller blocks). The relative proportions of these activities vary across the range as does the percentage of former forest land so affected. The role of these habitat changes as a direct stimulant of the major declines in progress is unclear. Sambar is highly tolerant of forest degradation: indeed, much higher numbers are found in encroached stands than in pristine closed-canopy forests, if hunting is under control (Rijksen 1978; Heydon 1994; Stuebing 1995; Davies et al. 2001, Brodie et al. in press b, c). Degradation per se is unlikely to be a significant threat. Many Indian forest areas are severely encroached by exotics such as Lantana camara, Parthenium spp. and Chromolaena odorata, and these are suspected to effect major changes to forest structure (Hiremath and Sundaram 2005): but their effects on Sambar populations warrant further study. There is no evidence that Sambar can survive complete conversion of landscapes to non-forest uses such as rice paddies, and its ability to use tree plantations in the absence of natural forest is unclear. Probably, like most deer, provided strips of semi-natural vegetation survive (e.g. along streams and on steep slopes) are present, it can use them to some degree. In most of its range (parts of India excepted) it is unlikely that habitat extent is the determining factor of current Sambar numbers, because large tracts of apparently suitable habitat now support no or only tiny numbers of Sambar. By far the most serious effect of current habitat trends is that fragmentation opens up wilderness areas to people, making it easier to hunt throughout them and cheaper to remove bulk wildlife products such as Sambar meat. In both Malaysian Borneo and Lao PDR the ‘natural protection’ afforded to an area through difficulty of access has been considered to be the chief factor allowing populations of large, hunted, mammals to survive (Timmins and Duckworth 1999, Bennett et al. 2000), and this is probably widely true for Sambar outside India, Nepal and the few other areas where active protective measures are effective. Although Sambar has a wide tolerance of habitat types, numerous observations and studies have indicated that highest densities and presumably habitat preferences of the species correlate with factors such as relatively gentle terrain, river plains, stream and other wetland vicinities, habitat ecotones, and secondary formations originating from closed canopy forests (Simcharoen et al. 2014; Lynam et al. 2012, Brodie et al. in press b, c), all factors which correlate positively with ongoing anthropogenic pressures and thus suggest that optimal habitats (and thus potentially a significant proportion of the global Sambar population) are correlated in one way or another with high threat levels for the species. In sum, the proximate cause of the major ongoing Sambar declines in most of its range is hunting, for which habitat conversion and fragmentation exacerbate the effects; and these processes are resulting in an ever-smaller maximum possible population, were the hunting issues to be successfully addressed.
Threats other than hunting and, locally, habitat loss, seem to be insignificant at the species level. Hybridization with Javan Rusa Rusa timorensis has been documented (Van Mourik and Schurig 1985), and is apparently a localized threat, where the latter has been introduced into Sambar range, in Pewajam District, East Kalimantan (G. Semiadi pers. comm. 2006) and potentially more widely (Corlett 2010). Hybridization has also been suspected in Sumatra, with the introduced Chital Axis axis (G. Semiadi pers. comm. 2006). However, Sambar and Chital co-occur extensively in India without hybridizing. Sambar is an occasional crop pest in mainland China, notably around the Ailoshan range (J. Fellowes pers. comm. 2008), India (N.S. Kumar pers. comm. 2008), Lao PDR (Duckworth et al. 1999), Myanmar (J.W. Duckworth pers. comm. 2008), Sumatra (D. Martyr pers. comm. 2008), and probably throughout its range. There is no evidence that Sambar is a serious crop pest away from the fields directly abutting forests. Nonetheless, crop damage is often stated by affected farmers to lead to a requirement for lethal control. However, the ready market for meat means that this is most probably an excuse for killing that would enthusiastically be undertaken anyway (N.S. Kumar and J.W. Duckworth pers. comm. 2008): it is therefore unlikely that control of crop-degrading animals is a significant cause of the species' decline anywhere in Sambar’s range. Grazing competition with domestic stock seems to be much less of a threat to Sambar than to sympatric Gaur and Chital: in fact the key study quantifying just how serious a threat such competition is in Indian protected areas (Madhusudan 2004) found that it had negligible effects on Sambar densities, presumably because Sambar is an efficient browser. Threats to southern India’s forest ungulates by competition with domestic stock grazing within protected areas are exacerbated where dung is collected for export to adjacent coffee areas. Fuel wood removal may also be at levels sufficient to disrupt nutrient cycles of the habitat (Madhusudan 2005). In the Indian Terai Arc Landscape, lopping of tree branches for cattle fodder is a threat to Sambar as it effectively removes most browsable vegetation from the landscape (B. Long pers. comm. 2008). These are probably more serious concerns for Sambar than is grazing by domestic stock.
The Sambar is found in many protected areas throughout its range, although in most of these areas this legal status has not stemmed declines and local extinctions from hunting. Similarly, although it is protected from hunting by legislation, even outside protected areas, in most or all range states, these laws are challenging to enforce, given the trade demand for meat and antlers (GMA Indonesia Workshop). In Sarawak, Borneo, unfortunately, Sambar is not on the protected list of Sarawak Wildlife Protection Ordinance, 1998 (a,b) (B. Giman pers. comm. 2014). Currently the law has a strong protective effect in Taiwan (Lin, C.-Y. and Lee, L.-L. pers. comm. 2008) and in various protected areas of India (N.S. Kumar pers. comm. 2008).
In Southeast Asia, Sambar declines have lagged behind those of other sympatric deer (excepting muntjacs). There is no doubt that within a decade or two Sambar will be, like Hog Deer and Eld’s Deer are already, almost absent from South-east Asia unless effective protection from trade-driven hunting is instituted. In India the species’s status is less grim, and this is dependent upon continuation of the current protected areas system, and the expansion of effective threat reduction into a greater proportion of protected areas: in many Indian protected areas, poaching is rampant and in such vulnerable areas Sambar numbers are still declining. Given the major challenges combating hunting of such a desired animal, long-term survival is most realistic in large protected areas (exceeding 1,000 km2 where possible), lacking people living within them, with an adequate number of motivated and capable staff (Anak Patannavibool pers. comm. 2008, A.J. Lynam pers. comm. 2008). The precise ways for protected areas to function effectively in the conservation of large mammals depend upon their own specific circumstances, but field presence of staff, dispersed across the area, is likely to be important in almost every area. For example, Lynam et al. (2006) found in Khao Yai National Park, Thailand, that encounter rates of tracks and signs of Sambar (and other large mammals) decreased with distance from ranger substations. Deep inside the forest to the south and east, far away from ranger substations, Sambar was locally extinct. Similar patterns are shown by current Sambar distributions in other Thai protected areas such as Khao Sok, Phu Khieo and Kaeng Krachan (A.J. Lynam pers. comm. 2008). In some protected areas (recent examples being Bhadra and Kudremukh in Karnataka), formerly forest-dwelling human communities have resettled closer to markets, clinics, school and other services (Karanth and Karanth 2007). This expands habitat available to Sambar (that which was formerly fields and houses) but more significant is the removal of a source of hunters and the cessation of grazing competition with domestic stock (see Karanth et al. 2006). Such conservation interventions have helped recovery of Sambar populations in this region. Increasing development aspirations mean that outmigration is likely from further areas, e.g. Mudumalai. Most of the remaining forest within its Chinese range are already established as nature reserves (M.W.N. Lau pers. comm. 2008).
As the majority of the Sambar population is in South Asia, conservation activities are important there. It is also important that populations are maintained at least in several areas in Southeast Asia, to maintain Sambar presence through its historical range, to preserve Sambar genetic diversity and through its importance to the ecosystems within which it lives. Given the regional pattern of threats and current successes to date, implementing effective conservation interventions is considerably more challenging, and therefore a higher priority in the Southeast Asian region.
The most important conservation measure for Sambar in Cambodia is the continued strengthening and support of conservation efforts in Seima Protected Forest, Phnom Prich Wildlife Sanctuary and Mondulkiri Protected Forest and to a lesser extent support of protected area conservation management in the northern plains and central Cardamoms. Likewise in Viet Nam, the most important conservation measure is the continued support of protection efforts within Cat Tien National Park, and in Thailand it is to to expand government-funded park protection and ranger training programmes outside of the few parks which are currently well supported in the Western Forest Complex. In Myanmar the Hukaung Valley is an exceptional area of lowland plains forest, grassland, and wetlands. Through its size and mostly little-encroached condition, this is the most outstanding remaining landscape-level floodplains habitat for very large mammals remaining in tropical Asia, and although wildlife populations are highly depleted, warrants the strongest effort to conserve it. It faces a number of daunting challenges (J.W. Duckworth pers. comm. 2008). In Lao PDR, any of a large number of areas could become key Sambar conservation sites, but there is as yet no precedent in the country for effective conservation of high-trade-value large mammals. Xe Pian, Nam Et–Phou Louey, and Nakai–Nam Theun NPAs could all be highly significant areas for the species, but so could almost any other NPA; the reality is that the most success with Sambar conservation is likely to come through identifying areas with positive underlying situations to achieve conservation, rather than identifying the area with the most intrinsic importance for Sambar as the focus for efforts.
Ables, E. D. and Ramsey, C. W. 1974. Indian mammals on Texas rangelands. Journal of the Bombay Natural History Society 71: 18-25.
Andheria, A., Karanth, K.U. and Kumar, N.S. 2007. Diet and prey profiles of three sympatric large carnivores in Bandipur Tiger Reserve in India. Journal of Zoology (London) 273: 169–175.
Azlan, J. M. 2006. Mammal diversity and conservation in a secondary forest in Peninsular Malaysia. Biodiversity and Conservation 15: 1013-1025.
Bali, A., Kumar, A. and Krishnaswamy, J. 2007. The mammalian communities in coffee plantations around a protected area in the Western Ghats, India. Biological Conservation 139: 93-102.
Bennett, E. L. and Dahaban, Z. 1995. Wildlife response to disturbances in Sarawak and their implications for forest management. In: R. B. Primack and T. E. Lovejoy (eds), Ecology, conservation and management of South-East Asian rainforests, pp. 66-86. Yale University Press, New Haven, USA, and London, UK.
Bennett, E. L. and Gumal, M. 2001. The interrelationships of commercial logging, hunting, and wildlife in Sarawak. In: R. A. Fimbel, A. Grajal and J. G. Robinson (eds), The cutting edge: conserving wildlife in logged tropical forest, pp. 359-374. Columbia University Press, New York, USA.
Bentley, A. 1978. An introduction to the deer of Australia. Koetong Trust Service, Victoria, Australia.
Brodie, J.F., Giordano, A., Dickson, B., Hebblewhite, M., Bernard, H., Azlan, M., Andersen J. and Ambu L. 2015. Evaluating multispecies landscape connectivity in a threatened tropical mammal community. Conservation Biology 29(1): 122-132.
Brodie, J.F., Giordano, A.J. and Ambu, L. 2014. Differential responses of large mammals to logging and edge effects. Mammalian Biology.
Brodie, J.F., Giordano, A.J., Zipkin, E.F., Bernard, H., Mohd-Azlan, J. and Ambu, L. 2014. Correlation and persistence of hunting and logging impacts on tropical rainforest mammals. Conservation Biology 29(1): 110-121.
Corlett, R.T. 2010. Megafaunal extinctions and their consequences in the tropical Indo-Pacific. In: ANU E-Press (ed.), Terra Australis 32: Altered Ecologies: Fire, Climate and Human Influence on Terrestrial Landscapes, pp. 117-131. Canberra.
Davies, G., Heydon, M., Leader-Williams, N., MacKinnon, J. and Newing, H. 2001. The effects of logging on tropical forest ungulates. In: R.A. Fimbel, A. Grajal and J.G. Robinson (eds), The cutting edge: conserving wildlife in logged tropical forest, Columbia University Press, New York, USA.
Delacour, J. 1940. Liste provisoire des mammifères de l'Indochine française. Mammalia 4: 20-29, 46-58.
Dersu Associates. 2007. Baseline wildlife survey of the Nakai plateau, 2006–2007. Unpublished report by Dersu Associates to the Nam Theun 2 Power Company, Vientiane.
Dinerstein, E. 1979. An ecological survey of the Royal Karnali Bardia Wildlife Reserve, Nepal 2. Habitat and animal interactions. Biological Conservation 16(4): 265-300.
Duckworth, J.W., Hallam, C.D., Phimmachak, S., Sivongxay, N., Stuart, B.L. and Vongsa, O. 2010. A conservation reconnaissance survey of north-east Vilabouli district, Savannakhet province, Lao PDR. A report to Lane Xang Minerals Ltd of a June–July 2009 survey by the Wildlife Conservation Society. Wildlife Conservation Society, Vientiane.
Duckworth, J.W. In press. Wildlife of the Nam Ngum basin, Lao PDR. Integrated Watershed Management Unit, Ministry of Agriculture and Forestry, Vientiane.
DWNP. 2010. Red List of Mammal for Peninsular Malaysia. Department of Wildlife and National Parks Peninsular Malaysia, Kuala Lumpur Malaysia.
Freeland, W. J. 1990. Large Herbivorous Mammals: Exotic Species in Northern Australia. Journal of Biogeography 17: 445-449.
Goldthorpe, G. and Neo, S.H. 2011. A preliminary investigation into the effects of hunting on three large ungulate species in Peninsular Malaysia, with implications for tiger conservation. . Malayan Nature Journal 63(3): 549-560.
Government of the Socialist Republic of Vietnam. 2004. The national action plan to strengthen the control of trade in wild fauna and flora to 2010. Prime Minister’s Office, Hanoi, Vietnam.
Gray, T.N.E., Phan, C., Pin, C. and Prum, S. 2013. Establishing a monitoring baseline for threatened large ungulates in eastern Cambodia. Wildlife Biology 18: 406-413.
Gray, T.N.E., Pin, C., Phan C. and Prum, S. 2011. Establishing baseline large ungulate densities in Mondulkiri Protected Forest and Phnom Prich Wildlife Sanctuary, Cambodia. WWF-Cambodia, Phnom Penh, Cambodia.
Grieser Johns, A. (ed.). 2000. Pu Mat: a biodiversity survey of a Vietnamese protected area. Social Forestry and Nature Conservation in Nghe An Province, SFNC Project, Vinh, Nghe An Province, Vietnam.
Groves, C. 2003. Taxonomy of ungulates of the Indian Subcontinent. Journal of the Bombay Natural History Society 100(2-3): 341-361.
Groves, C. 2006. The genus Cervus in eastern Eurasia. European Journal of Wildlife Research 52: 14-22.
Groves, C. and Grubb, P. 2011. Ungulate Taxonomy. The Johns Hopkins University Press, Baltimore, USA.
Groves, C.P. and Grubb, P. 1987. Relationships of Living Deer. In: C.M. Wemmer (ed.), Biology and Management of the Cervidae, pp. 21-59. Smithsonian Institution Press, Washington, DC, USA.
Groves, C.P. and Grubb, P. 1987. Relationships of living deer. In: C. Wemmer (ed.), Biology and Management of the Cervidae, pp. 1-40. Smithsonian Institution Press, Washington, D.C., USA.
Grubb, P. 1990. List of deer species and subspecies. Deer, Journal of the British Deer Society 8: 153-155.
Grubb, P. 2005. Artiodactyla. In: D.E. Wilson and D.M. Reeder (eds), Mammal Species of the World. A Taxonomic and Geographic Reference (3rd ed), pp. 637-722. Johns Hopkins University Press, Baltimore, USA.
Heydon, M.J. 1994. The ecology and management of rain forest ungulates in Sabah, Malaysia: implications for forest disturbance. Institute of Tropical Biology, University of Aberdeen, ODA/NERC, Aberdeen, UK.
Hiremath, A.J. and Sundaram, B. 2005. The fire-lantana cycle hypothesis in Indian forests. Conservation and Society 3: 26-42.
IUCN. 2015. The IUCN Red List of Threatened Species. Version 2015-4. Available at: www.iucnredlist.org. (Accessed: 19 November 2015).
Jathanna, D., Karanth, K.U. and Johnsingh, A.J.T. 2003. Estimation of large herbivore densities in the tropical forests of southern India using distance sampling. Journal of Zoology (London) 261: 285.
Johnsingh, A. J. T. and Sankar, K. 1991. Food plants of chital, sambar and cattle on Mundanthurai plateau, Tamil Nadu, South India. Mammalia 55: 57-66.
Johnsingh, A.J.T., Qureshi, Q., Goyal, S.P., Rawat, G.S., Ramesh, K., David, A., Rajapandian, K. and Prasad, S. 2004. Conservation Status of Tiger and Associated Species in the Terai Arc Landscape, India.
Johnson, A. and Johnston, J. 2007. Biodiversity monitoring and enforcement project in the Nam Theun 2 watershed. Final report. Wildlife Conservation Society, Vientiane, Laos.
Johnson, A., Singh, S., Dongdala, M. and Vongsa, O. 2003. Wildlife hunting and use in the Nam Ha National Protected Area: implications for rural livelihoods and biodiversity conservation. Wildlife Conservation Society, Vientiane, Laos.
Johnson, A., Vongkhamheng, C., Hedemark, M. and Saythongdum, T. 2004. The status of Tiger, prey and human–Tiger conflict in the Nam Et–Phou Louey national protected area. Wildlife Conservation Society, Vientiane, Laos.
Johnson, D. H. 1999. The insignificance of statistical significance testing. Journal of Wildlife Management 63: 763–772.
Karanth, K. K., Curran, L. M. and Reuning-Scherer, J. D. 2006. Village size and forest disturbance in Bhadra Wildlife sanctuary, Western Ghats, India. Biological Conservation 128: 147-157.
Karanth, K. U. and Karanth, K. K. 2007. Free to move: conservation and voluntary resettlements in the Western Ghats of Karnataka, India. WCS Working Papers 29: 48–59.
Karanth, K.U. and Nichols, J.D. 2000. Ecological status and conservation of tigers in India. Centre for Wildlife Studies, Bangalore, India.
Kawanishi, K. 2008. Questioning the sustainability of legal hunting of deer and pig in Peninsular Malaysia. Unpublished report submitted to the Department of Wildlife and National Parks.
Kawanishi, K. and Sunquist, M.E. 2004. Conservation status of Tigers in a primary rainforest of Peninsular Malaysia. Biological Conservation 120(3): 329–344.
Kawanishi, K., Clements, G.R., Gumal, M., Goldthrope, G., Mohd Nawayai, Y. and Sharma, D.S.K. 2013. Using BAD for good: how best available data facilitated a precautionary policy change to improve protection of the prey of the tiger Panthera tigris in Malaysia. Oryx 47(3): 420-426.
Kawanishi, K., Rayan, D.M., Gumal, M.T. and Shepherd, C.R. 2014. Extinction process of the sambar deer in Peninsular Malaysia. IUCN Deer Specialist Group Newsletter 26: 48-59.
Kelton, S. D. and Skipworth, J. P. 1987. Food of sambar deer (Cervus unicolor) in a Manawatu (New Zealand) flax swamp. New Zealand Journal of Ecology 10: 149-152.
Khan, J.A., Chellam, R., Rodgers, W.A. and Johnsingh, A.J.T. 1996. Ungulate densities and biomass in the tropical dry deciduous forests of Gir, Gujarat, India. Journal of Tropical Ecology 12(1): 149.
Khan, M.A.R. 1985. Mammals of Bangladesh: a field guide. Nazma Reza, Dhaka, Bangladesh.
Kumara, H. N. and Singh, M. 2004. The influence of differing hunting practices on the relative abundance of mammals in two rainforest areas of the Western Ghats, India. Oryx 38: 321–327.
Kumar, N.S. 2000. Ungulate density and biomass in the tropical semi-arid forest of Ranthambore, India. Pondicherry University.
Kushwaha, S. P. S., Khan, A., Habibi, B., Quadri, A. and Singh, A. 2004. Evaluation of Sambar and Muntjak (sic) habitats using geostatistical modelling. Current Science 86: 1390-1400.
Lekagul, B. and McNeely, J.A. 1977. Mammals of Thailand. Association for the Conservation of Wildlife, Bangkok, Thailand.
Lever, C. 1985. Naturalized mammals of the world. Longman, London, England, UK.
Lewis, J. C., Flynn, L. B., Marchinton, R. L., Shea, S. M. and Marchinton, E. M. 1990. Part I : Introduction, study area description and Literature review. Ecology of sambar deer on St. Vincent National Wildlife Refuge, Florida, pp. 1-12. Bulletin of Tall Timbers Research Station, Tallahassee, Florida, USA.
Le Xuan Canh, Pham Trong Anh, Duckworth, J.W., Vu Ngoc Thanh and Lic Vuthy. 1997. A survey of large mammals in Dak Lak Province, Viet Nam. Unpublished report to IUCN and WWF. Hanoi, Viet Nam.
Lynam, A.J. 2003. A National Tiger Action Plan for the Union of Myanmar. Myanmar Forest Department, Ministry of Forestry, Yangon, Myanmar.
Lynam, A.J., Kreetiyutanont, K. and Mather, R. 2001. Conservation status and distribution of the Indochinese tiger (Panthera tigris corbetti) and other large mammals in a forest complex in northeastern Thailand. Natural History Bulletin of the Siam Society 49: 61-75.
Lynam, A.J., Laidlaw, R., Wan Shaharuddin Wan Noordin, Elagupillay, S. and Bennett, E.L. 2007. Assessing the conservation status of the Tiger Panthera tigris at priority sites in peninsular Malaysia. Oryx 41: 454-462.
Lynam, A.J., Rabinowitz, A., Myint, T., Maung, M., Latt, K.T. and Po, S.T.T. 2009. Estimating abundance with sparse data; implications for tigers in northern Myanmar. Population Ecology 51: 115-121.
Lynam, A. J., Round, P. D. and Brockelman, W. Y. 2006. Status of birds and large mammals in Thailand's Dong Phayayen - Khao Yai Forest Complex. Biodiversity Research and Training, Bangkok, Thailand.
Lynam, A.J., Tantipisanuh, N., Chutipong, W., Ngoprasert, D., Baker, M.C., Cutter, P., Gale, G., Kitamura, S., Steinmetz, R., Sukmasuang R. and Thunhikorn, S. 2012. Comparative sensitivity to environmental variation and human disturbance of Asian tapirs (Tapirus indicus) and other wild ungulates in Thailand. Integrative Zoology 7(4): 389-399.
Madhusudan, M.D. 2004. Recovery of wild large herbivores following livestock decline in a tropical Indian wildlife reserve. Journal of Applied Ecology 41: 858–869.
Madhusudan, M.D. 2005. The global village: linkages between international coffee markets and grazing by livestock in a south Indian wildlife reserve. Conservation Biology 19: 411–420.
Madhusudan, M.D. and Karanth, K.U. 2002. Local hunting and the conservation of large mammals in India. Ambio 31(1): 49-54.
Martin C. 1977. Status and ecology of the Barasingha (Cervus duvauceli branderi) in Kanha National Park (India). Journal of the Bombay Natural History Society 74: 60-132.
Matsubayashi, H. and Sukor, J.R.A. 2005. Activity and habitat use of two sympatric mouse-deer species, Tragulus javanicus and Tragulus napu, in Sabah, Malaysia, Borneo. Malayan Nature Journal 57: 235–241.
Matsubayashi, H., Lagan, P., Majalap, N., Tangah, J., Sukor, J.R.A. and Kitayama, K. 2007. Importance of natural licks for the mammals in Bornean inland tropical rain forests. Ecological Research 22: 742-748.
Maxwell, A., Chea Nareth, Duong Kong, Timmins, R. and Duckworth, J.W. 2007. Hog Deer (Axis porcinus) confirmed in the wild in eastern Cambodia. Natural History Bulletin of the Siam Society 54: 227–237.
Ngampongsai, C. 1987. Habitat use by the sambar (Cervus unicolor) in Thailand: A case study for Khao-Yai National Park. In: C.M.Wemme. (ed.), Biology and management of the Cervidae., pp. 289-298. Washington D.C., Smithsonian Institution Press.
Ngoprasert, D., Lynam, A. J. and Gale, G. A. 2007. Human disturbance affects habitat use and behaviour of Asiatic Leopard in Kaeng Krachan National Park, Thailand. Oryx. 41: 343-351.
Nuttall, M., Nut Menghor and O’Kelly, H. 2014. Monitoring of key species in the Seima Protected Forest. Phnom Penh: Wildlife Conservation Society Cambodia Program and the Forestry Administration.
O'Brien, T.G., Kinnaird, M.F. and Wibisono, H.T. 2003. Crouching tigers, hidden prey: Sumatran tiger and prey populations in a tropical forest landscape. Animal Conservation 6: 131-139.
Ohtaishi, N. and Gao, Y.T. 1990. A review of the distribution of all species of deer (Tragulidae, Moschidae and Cervidae) in China. Mammal Review 20(2-3): 125-144.
O’Kelly, H.J., Evans, T.D., Stokes, E.J., Clements, T.J., Dara, A., Gately, M., Menghor, N., Pollard, E.H.B., Soriyun, M. and Walston, J. 2012. Identifying Conservation Successes, Failures and Future Opportunities; Assessing Recovery Potential of Wild Ungulates and Tigers in Eastern Cambodia. PLoS ONE 7(10): e40482. doi:10.1371/journal.pone.0040482.
Pham Trong Anh, Nguyen Dang Khoi and Nguyen Thi Tang Long. 1996. Checklist of mammal collection of Da Lat Biological Subinstitute. Tap Chi Sinh Hoc [J. Biology, Hanoi] 18(1): 16-22.
Pillay, R., Johnsingh, A.J.T., Raghunath, R. and Madhusudan, M.D. 2011. Patterns of spatiotemporal change in large mammal distribution and abundance in the southern Western Ghats, India. Biological Conservation 144: 1567–1576.
Polet, G. and Ling, S. 2004. Protecting mammal diversity: opportunities and constraints for pragmatic conservation management in Cat Tien National Park, Vietnam. Oryx 38(2): 186.
Porwal, M. C., Roy, P. S. and Chellamuthu, V. 1996. Wildlife habitat analysis for 'sambar' (Cervus unicolor) in Kanha National Park using remote sensing. International Journal of Remote Sensing 14: 2683–2697.
Richardson, W. A. 1972. A natural history survey of sambar deer (Cervus unicolor) on the powerhorn ranch calhoun country, Texas. Texas A & M University.
Rijksen, H.D. 1978. A Field Study on Sumatran Orangutans (Pongo pygmaeus abelii, Lesson 1827): Ecology, Behavior, and Conservation. H. Veenman and Zonen, Wageningen, Netherlands.
Sankar, K. 1994. The ecology of three large sympatric herbivores (Chital, sambar and nilgai) with special reference for reserve management in Sariska Tiger Reserve, Rajasthan. University of Rajasthan.
Sankar, K. and Acharya, B. 2004. Sambar (Cervus unicolor Kerr, 1792). ENVIS Bulletin (Wildlife Institute of India, Dehra Dun) 7: 163–170.
Santiapillai, C. and Wijeyamohan, S. 2003. The impact of civil war on wildlife in Sri Lanka. Current Science 84: 1182–1183.
Schaller, G. 1967. The deer and the tiger. University ofChicago Press, Chicago, USA.
Semiadi, G., Adhi, I. G. M. J. and Muchsinin, M. 2004. Perburuan dan pemanfaatan rusa Sambar (Cervus unicolor) di Kalimantan Timur [The hunting and utilization of Sambar in East Kalimantan]. [In Indonesian]. Jurnal Peternakan dan Lingkungan (Univ. Andalas) 10: 25-29.
Semiadi, G., Barry, T. N., Muir, P. D. and Hodgson, J. 1995. Dietary preferences of Sambar (Cervus unicolor) and Red Deer (Cervus elaphus) offered browse, forage legume and grass species. Journal of Agricultural Science 125: 99-107.
Sheng, H.I. and Ohtaishi, N. 1993. The status of deer in China. In: N. Ohtaishi and H.I. Sheng (eds), Deer of China: Biology and Management, pp. 8. Elsevier, Oxford, UK.
Simcharoen, A., Savini, T., Gale, G.A., Roche, E., Chimchome, V. and Smith, J.L.D. 2014. Ecological factors that influence sambar (Rusa unicolor) distribution and abundance in western Thailand: implications for tiger conservation. Raffles Bulletin of Zoology 62: 100–106.
Slee, K. J. 1984. The Sambar deer in Victoria. Deer, pp. 559-72. University of Sydney, Sydney, Australia.
Smith, A.T. and Xie, Y. 2008. A Guide to the Mammals of China. Princeton University Press, Princeton, New Jersey.
Sridhar, H., Raman, S.T. and Mudappa, D. 2008. Mammal persistence and abundance in tropical rainforest remnants in the southern Western Ghats, India. Current Science 94(6): 748-757.
Steinmetz, R., Chutipong, W., Seuaturien, N. and Cheungsa-ad, E. 2008. Community structure of large mammals in tropical montane and lowland forest in the Tenasserim–Dawna mountains, Thailand. Biotropica 40: 344–353.
Steinmetz, R., Seuaturien, N., Chutipong, W., Chamnankit, C. and Phoonjampa, R. 2007. The ecology and conservation of tigers, other large carnivores, and their prey in Kuiburi National Park, Thailand. WWF Thailand and Kuiburi National Park, Bangkok, Thailand.
SUFORD. 2010. Preliminary Biodiversity Assessment and Management Recommendations of SUFORD-AF Production Forest Areas. Vientiane: Sustainable Forestry for Rural Development Project -Additional Financing (SUFORD - AF). Unpublished report.
Tilson, R., Defu, H., Muntifering, J. and Nyhus, P. J. 2004. Dramatic decline of wild South China tigers Panthera tigris amoyensis: Field survey of priority tiger reserves. Oryx 38: 40-47.
Timmins, R.J. 2006. An assessment of the biodiversity conservation significance of the Mekong Ramsar site, Stung Treng, Cambodia. Mekong Wetlands Biodiversity Conservation and Sustainable Use Programme, Stung Treng, Cambodia.
Timmins, R.J. 2009. Biodiversity significance and management of the Phou Theung forest area, Xekong Province, Lao PDR. WWF, Vientiane.
Timmins, R.J. 2014. Xe Sap Mammal and Bird Survey, May-June 2012. WWF Greater Mekong. Biodiversity surveys of Xe Sap National Protected Area. WWF Greater Mekong, Vientiane.
Timmins, R. J. and Duckworth, J. W. 1999. Status and conservation of Douc Langurs (Pygathrix nemaeus) in Laos. International Journal of Primatology 20: 469–489.
Timmins, R.J. and Duckworth, J.W. 2012. A survey of gibbons and other wildlife in the Bokeo section of Nam Kan National Protected Area, Lao PDR . Fauna & Flora International, Cambridge, UK.
Timmins, R. J. and Men Soriyun. 1998. A wildlife survey of the Tonle San and Tonle Srepok river basins in northeastern Cambodia. Fauna and Flora International and Wildlife Protection Office., Hanoi, Vietnam and Phnom Penh, Cambodia.
Timmins, R.J. and Ou Rattanak. 2001. The importance of Phnom Prich Wildlife Sanctuary and adjacent areas for the conservation of tigers and other key species. WWF Indochina Programme, Hanoi, Vietnam and Phonm Penh, Cambodia.
Timmins, R.J. and Robichaud, W.G. 2005. Birds and mammals of conservation concern in the area of the proposed Nam Theun 1 Hydropower Project – assessment and recommendations. Report to Electrowatt-Ekono Ltd.
Timmins, R.J., Do Tuoc, Trinh Viet Cuong and Hendrichsen, D.K. 1999. A preliminary assessment of the conservation importance and conservation priorities of the Phong Nha-Ke Bang proposed National Park, Quang Binh Province, Vietnam. Fauna and Flora International-Indochina Programme, Hanoi, Vietnam.
Timmins, R.J. In press a. The potential wildlife conservation significance and priority of remaining forest in northwestern Tuy Duc District, Dak Nong Province, based on a survey of birds and large mammals. Wildlife Conservation Society, Hanoi.
Timmins, R.J. In press b. Report on a survey for Saola, using leeches, in Phou Sithone Endangered Species Conservation Area, Bolikhamxai Province, Lao P.D.R. Saola Working Group and WCS Lao Program.
Timmins, R.J., Pech Bunnat and Prum Sovanna. 2003. An assessment of the conservation importance of the Western Siem Pang area, Stung Treng Province, Cambodia. WWF Cambodia, Phnom Penh, Cambodia.
Timmins, R.J., Robichaud, W.G., Long, B., Hedges, S., Steinmetz, R., Abramov, A., Do Tuoc and Mallon, D.P. 2008. Pseudoryx nghetinhensis. The IUCN Red List of Threatened Species. Version 2014.2. Available at: www.iucnredlist.org. (Accessed: 14 November 2014).
Timmins, R. J., Tuoc, D. and Viet Cuong Trinh. 2001. An assessment of the conservation importance of the Huong Son (Annamite) forest, Ha Tinh Province, Vietnam, based on the results of a field survey for large mammals and birds. Center for Biodiversity and Conservation at the American Museum of Natural History, New York, USA.
Tordoff, A.W., Timmins, R.J., Maxwell, A., Huy Keavuth, Lic Vuthy and Khou Eang Hourt (eds). 2005. Biological assessment of the Lower Mekong Dry Forests Ecoregion. pp. 192 pp.. WWF Greater Mekong Programme, Phnom Penh, Cambodia.
TRAFFIC. 2008. What’s Driving the Wildlife Trade? A Review of Expert Opinion on Economic and Social Drivers of the Wildlife Trade and Trade Control Efforts in Cambodia, Indonesia, Lao PDR and Vietnam. East Asia and Pacific Region Sustainable Development Department, World Bank, Washington, DC.
Trisurat, Y., Eiumnoh, A., Tharnchai, P. and Phongpanit, K. 1996. A geographical study of wildlife abundances in Khao Yai National Park, Thailand. Report to Thailand Research Fund by the School of Environment, Resources and Development, Asian Institute of Technology, Bangkok, Thailand.
Tungittiplakorn, W. and Dearden, P. 2002. Hunting and wildlife use in some Hmong communities in northern Thailand. Natural History Bulletin of the Siam Society 50: 57–73.
Van Mourik, S. and Schurig, V. 1985. Hybridization between Sambar (Cervus (Rusa) unicolor) and Rusa (Cervus (Rusa) timorensis) deer. Zoologischer Anzeiger 214: 177-184.
Walston, J., Karanth, K.U. and Stokes, E.J. 2010. Avoiding the unthinkable: what will it cost to prevent Tigers be-coming extinct in the wild? Wildlife Conservation Society, New York.
Walston, J. L. 2001. Biodiversity, the life of Cambodia – Cambodian biodiversity status report 2001. In: J. D. Smith (ed.), Kangaroo-rats and other mammals of Cambodia, pp. 135-152. Cambodia Biodiversity Enabling Activity, Food and Agriculture Organisation, Phnom Penh, Cambodia.
Woxvold, I.A. 2009. A wildlife survey of the Minerals and Metals Group’s Sepon Expanded Development Area (Draft). Coffey Natural Systems and The Wildlife Conservation Society, Vientiane.
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