Phylogenetic analyses group the Asian Golden Cat with the Marbled Cat (Pardofelis marmorata) and the Bay Cat (Catopuma badia; Johnson et al. 2006, O'Brien and Johnson 2007). Because of this phylogenetic grouping, both the Asian Golden Cat and the Bay Cat were proposed to be reclassified under Pardofelis (Johnson et al. 2006). However, a subsequent evaluation of skull morphology by Sicuro and Oliveira (2011) revealed that skull structure in Pardofelis was significantly different from that in Catopuma. In addition, Catopuma lacks the flexible ankle joints and elongated tail found in Pardofelis, two adaptations to arboreality. Based on these morphological differences, the IUCN SSC Cat Specialist Group retains the Asian Golden Cat and Bay Cat in Catopuma.

The Asian Golden Cat is listed as Vulnerable under Criterion A2cd. Based on a combination of direct and indirect evidence of Asian Golden Cat population and/or range declines across the approximately 20-year assessment period (generation length = ca. 6–7 years [Pacifici et al. 2013] x 3 = 20 years, ca. 2003–2022), we applied a conservative precautionary approach to this assessment. Such evidence includes the species’ apparent disappearance across large parts of its range, including from several protected areas (e.g., Nakai – Nam Theun National Park in Lao People’s Democratic Republic [PDR]), landscapes (e.g., Cambodia’s Eastern Plains), and even countries (e.g., Viet Nam) during the assessment period—with no evidence of compensatory increases in population elsewhere. However, we acknowledge the uncertainties in the available data (both past and present) and recognize that the classification of Vulnerable, as opposed to Endangered or Near Threatened, is marginal and subject to the assumptions made herein.

The Asian Golden Cat is uplisted from Near Threatened to Vulnerable under Criterion A2cd based on a suspected past population decline of 34% over the past three generations. This suspected population decline is inferred from estimated declines in area of occupancy (AOO) (i.e., -68%, Petersen et al. 2021), assuming the percent decline in mature individuals is at least half the percent decline in AOO. The assumption that the percent decline in mature individuals was less than the percent decline in AOO (i.e., a ratio between 1:2 and 1:1), is based on the premise that declines in AOO are more likely to occur in areas with lower population densities. However, without reliable range-wide population estimates, the exact ratio between declines in AOO and population is indeterminable. Depending on the ratio used, Asian Golden Cats could qualify for a range of Red List Categories under Criterion A2cd, from Near Threatened (i.e., 1:4) to Endangered (i.e., 1:1). The choice of a 1:2 ratio is conservative, as higher ratios (e.g., 1:4) are mathematically unlikely except in scenarios with highly skewed population distributions and little-to-no declines in high population density areas.

Illegal hunting appears to be the primary driver of declines in population size and AOO, rather than habitat loss. Multiple camera-trap surveys in otherwise suitable habitats have reported low numbers of detections or no detections at all (e.g., Gray et al. 2012, Willcox et al. 2014, Moo et al. 2017). However, declines in AOO are expected to decrease in the future as the species becomes increasingly restricted to a few “safe” havens, mostly located in the Eastern Himalayas, Thailand, Malaysia, and Sumatra, provided that hunting pressures remain unmitigated elsewhere (i.e., other populations will trend towards extinction; see Geographic Range / Population / Threats). Accordingly, the projected decline in area of occupancy over the next three generations was predicted to be 18% (Petersen et al. 2021), thus Criterion A3 is not triggered.

Estimating the Asian Golden Cat’s global population size is difficult, as no robust population estimates exist. Following a series of assumptions, which rely heavily on published estimates of sympatric clouded leopard (Neofelis sp.) population density and several generalizations concerning the distribution and habitat use of Asian Golden Cats, this assessment inferred a global population size of ca. 7,000 mature individuals (1,000 – 12,000; see Online Supporting Material). This population size, combined with an inferred decline in population size of 9% given a projected decline in area of occupancy of 18% over the next three generations (Petersen et al. 2021) suggests the species is close to triggering Vulnerable under Criteria C1. However, since this decline in population size is “inferred” and not “observed, estimated, or projected”, Criterion C1 cannot be triggered (IUCN Standards and Petitions Committee 2022).

Historically, the Asian Golden Cat was distributed from the Eastern Himalayas through southern and central China, mainland Southeast Asia, and the island of Sumatra (Patel et al. 2016, Smith et al. 2010; see also Supplemental Maps). Although it remains widely distributed, the species’ current distribution has become both contracted and fragmented due to extensive habitat loss and unsustainable levels of hunting across its range.
A country-by-country breakdown of the Asian Golden Cat’s current known distribution is as follows:

Bangladesh: The Asian Golden Cat is restricted to Bangladesh’s remaining tropical wet evergreen and semi-evergreen forest cover in the Chittagong Hill Tracts of southeastern Bangladesh (Chakma 2015, Creative Conservation Alliance 2016) and the northeastern forest complex along the border with the Indian state of Tripura (Rahman et al. 2021, M. Akash pers. comm. 2022).

Bhutan: Formal studies on the Asian Golden Cat’s geographic range in Bhutan have so far been limited to literature reviews (e.g., Dhendup 2016) and regional modelling efforts (e.g., Petersen et al. 2021). The findings of these studies, and others, combined with the nation’s relatively extensive forest cover and protected area network (both exceeding 50% of Bhutan’s landmass), suggest the species to be widespread. Recently published bycatch data gathered from the country’s national Tiger (Panthera tigris) survey (Penjor et al. 2021, in supplemental material Figure S18) have confirmed this conclusion, revealing widespread occurrence throughout the entire country except for areas well above the tree line and associated shrub matrices (ca. 4,000-5,000 m depending on local conditions; Miehe et al. 2007). Indeed, an informal investigation of this bycatch data suggests an elevational range from approximately 100 to 4,600 meters above sea level (rounded to the nearest 100 meters due to locational uncertainty), which closely tracks the elevational range of tree and shrub cover in the country (Miehe et al. 2007).

Cambodia: Historically, the Asian Golden Cat was presumably distributed widely throughout Cambodia’s forests. Today, best available data suggest the Asian Golden Cat is restricted to the country’s two largest remaining semi-evergreen forest landscapes: the Cardamom Mountains in the country’s southwest and Virachey National Park in the northeast. A review of 31 camera-trap studies across 23 protected areas, including both published and unpublished data and conducted for the purpose of this assessment, found Asian Golden Cats to be detected in only 8 studies and five protected areas. These areas comprised the Central Cardamom Protected Forest (Gray et al. 2017), Southern Cardamom National Park (Gray et al. 2017), Tatai Wildlife Sanctuary (Gray et al. 2017), Siem Pang Wildlife Sanctuary (Loveridge et al. 2018), Samlout Multiple Use Area (Fauna & Flora International, unpub. data), and Virachey National Park (McCann et al. 2020). The last records from the Eastern Plains Landscape, a combination of deciduous dipterocarp and mixed evergreen forests, occurred in the mid-2010s and there have been no further records from this landscape, despite extensive subsequent camera-trapping.

China: The Asian Golden Cat was once widely distributed throughout the tropical and subtropical forests of Southern, Southeastern, and Central China (Smith et al. 2010). Currently, confirmed records are available from a handful of localities in Sichuan (e.g., Gongga Mountain National Nature Reserve, Sichuan Tangjiahe National Nature Reserve), Gansu, and Shaanxi provinces, southeastern Tibet, and western and southern Yunnan (Bai et al. 2018, Shen et al. 2019, Li et al. 2020, Ma et al. 2020, Wang et al. 2022, He et al. 2023, Liu et al. 2023).

India: India’s remaining natural habitats have been more extensively camera-trapped compared with other range countries. These surveys indicate the Asian Golden Cat’s distribution is limited to the country’s northeastern region, with recent records in Sikkim (e.g., Bashir et al. 2011), West Bengal (e.g., Ghose et al. 2019), Assam (e.g., Lalthanpuia et al. 2014), Arunachal Pradesh (e.g., Mukherjee et al. 2019), Nagaland (e.g., Joshi et al. 2019), Meghalaya (e.g., Mukherjee et al. 2019), and Mizoram (e.g., Mukherjee et al. 2019). In addition, the species is presumably present in the state of Tripura given the presence of nearby records in Bangladesh’s northeastern forests (Rahman et al. 2021). Individual records are reported from Khangchendzonga Biosphere Reserve (Bashir et al. 2011), Neora Valley National Park (Chatterjee et al. 2018), Buxa Tiger Reserve (Ghose et al. 2019), Nongkhyllem Wildlife Sanctuary (Mukherjee et al. 2019), Eaglenest Wildlife Sanctuary (Mukherjee et al. 2019), Dampa Tiger Reserve (Singh and Macdonald 2017), Singchung Bugun Village Community Reserve (Mukherjee et al. 2019), Pakke Tiger Reserve (Mukherjee et al. 2019), Kachanjuri wildlife-corridor (Lalthanpuia et al. 2014), Talley Valley Wildlife Sanctuary (Mukherjee et al. 2019), Dzkou Valley Community Forests (Joshi et al. 2019), Choklangan Village Community Forests (Longchar et al. 2017), Dibang Wildlife Sanctuary (Jhala et al. 2020), Kamlang Tiger Reserve and Wildlife Sanctuary (Jhala et al. 2020), and Namdapha National Park (Jhala et al. 2020).

Indonesia: The Asian Golden Cat is still relatively widespread across Sumatra’s forests. Published records include those from Bukit Barisan Selatan National Park (Fitria et al. 2019, Weiskopf et al. 2019, Allen et al. 2020), Bengkunat Protected Forest (Khalil 2019), Batutegi Protected Forest (Huda et al. 2020), Kerinci Seblat National Park (Haidir et al. 2021), Bukit Tigapuluh Landscape (Subrata et al. 2022), Peranap (Sunarto et al. 2015), Rimbang Baling (Sunarto et al. 2015), Malampah Nature Reserve (Ladyfandela et al. 2018, SIF. 2024), Pasaman Regency (iNaturalist 2023), Batang Angkola Landscape (Ario et al. 2020), Gunung Leuser National Park, Beutong, Bengkung, Southwestern Aceh,  (Pusparini et al. 2014, MoEF, SIF, FKL, Panthera 2024), and the Ulu Masen Ecosystem (Radinal et al. 2019).

Lao PDR: Asian Golden Cats were presumably once widespread throughout the forests of Lao PDR. By 2023, the species’ geographic range appears to be greatly diminished, presumably due to intensive hunting practices (see Coudrat et al. 2014, Coudrat 2019). Recent records exist only from northern and central Lao PDR, in the provinces of Khammouane (Phou Hin Poun National Protected Area; Brakels and Souwideth, unpubl. data), Bolikhamxai (Nam Kading National Protected Area and Nam Chouane – Nam Xang area; WCS Lao PDR, unpubl. data), Houaphanh (Nam Et – Phou Louey National Protected Area; Rasphone et al. 2019), Xaisomboun (Nam Ngiep 1 Sub Catchment area; WCS Lao PDR, unpubl. data), Xaignabouli (i.e., Nam Pouy National Protected Area; WWF-Laos, unpubl. data), Louang Namtha (North Corridor between Nam Ha and Nam Kan National Parks; WCS Lao PDR, unpubl. data), and Oudomxay (La District; CCL-Laos and WWF-Laos, unpubl. data).

Malaysia: Available data indicate the Asian Golden Cat is still relatively widespread across Peninsular Malaysia. The species continues to be detected within multiple areas throughout the country’s Central Forest Spine, an approximately 53,000 km² forested landscape. Recent records from this landscape come from large forest complexes including the Bintang Hijau Forest Complex (Gunung Inas Forest Reserve, WWF-Malaysia, unpubl. data), the Main Range Forest Complex (e.g., Royal Belum State Park, Temengor Forest Reserve; Mohamad et al. 2015, Amanjaya Forest Reserve, Rayan et al. 2013, Gunan Basor Forest Reserve, Stong Utara Forest Reserve, WWF-Malaysia, unpubl. data), the Greater Taman Nagara Forest Complex (e.g., Taman Negara National Park, Jambari et al. 2019; Hulu Terengganu Hydroelectric Dam Catchment, Adyla et al. 2016, Tembat Forest Reserve, Zainol et al. 2021), and the Endau Rompin-Sedili Forest Complex (e.g., Endau Rompin National Park, Gumal et al. 2014; Lesong  Forest Reserve, Sungai Pukin Forest Reserve, Rompin State Park, Labis Utara Forest Reserve, Labis Tengah Forest Reserve, Labis Timur Forest Reserve, Mersing Forest Reserve, Lenggor Forest Reserve, Kluang Forest Reserve, Aramijaya concession, Ulu Sedili Forest Reserve, and Panti Forest Reserve, WCS-Malaysia, unpubl. data), as well as various corridors connecting these complexes (e.g., Primary Linkage 1/Taman Negara Wildlife Corridor; Razak et al. 2021, Primary Linkage 7/Kenyir Wildlife Corridor, Clements 2013, Linkage 8/Bintang Hijau Wildlife Corridor, Clements 2013).

Myanmar: Most of Myanmar’s forests are considered ecologically suitable for, and within the historical range of, Asian Golden Cats (Than Zaw et al. 2008). However, understanding of the species’ current distribution in the country remains incomplete. Recurring political instability and other logistical challenges have led to survey efforts not being uniformly distributed throughout the country. In the south, camera-trap surveys continue to document the species’ presence throughout large portions of the Dawna – Tennasarim Range including both the Kawthoolei and Tanintharyi (Moo et al. 2018, Greenspan et al. 2020, Kawthoolei Forestry Department, unpubl. data; Fauna and Flora International, unpubl. data). However, nowhere in the landscape does the species appear to be particularly common (Kawthoolei Forestry Department, unpubl. data; Fauna and Flora International, unpubl. data) and in a few seemingly suitable areas there have been no detections at all (e.g., Tu Ter Lor Wildlife Sanctuary; Moo et al. 2018, Kawthoolei Forestry Department, unpubl. data). Elsewhere, available records place the species in Bago Yoma (North Zamari Reserve Forest, WWF-Myanmar, unpubl. data) and the southern Rakhine Yoma (Rakhine Yoma Elephant Range Wildlife Sanctuary, Cremonesi et al. 2021, Ayeyarwady Region, Suzuki et al. 2019). Few to no studies have been conducted in Shan State or the northern Rakhine Yoma and Chin Hills, and in these areas the species’ continued existence remains unverified. Presence is assumed in the latter two areas though, based on records from neighbouring landscapes (e.g., Chittagong Hill Tracts of Bangladesh; Chakma 2015, Creative Conservation Alliance 2016). In the far north, the species was previously considered widespread based on records from the 1990s and early 2000s (Than Zaw et al. 2008). Few follow-up studies have been conducted in these areas though, with recent Asian Golden Cat records limited to just Hukaung Valley Wildlife Sanctuary (Naing et al. 2015), Htamanthi Wildlife Sanctuary (Naing et al. 2017), and the proposed southern extension to Hkakaborazi National Park (Lwin et al. 2021).

Nepal: The Asian Golden Cat is known only from northeastern Nepal, with recent records from Makalu-Barun National Park (Ghimirey and Pal 2009), the Tinjure-Milke-Jaljale Area (Rai et al. 2019), Gaurishankar Conservation Area (Koju et al. 2020), and the Panchthar-Ilam-Taplejung Corridor (Lama et al. 2019). 

Singapore: The Asian Golden Cat’s historical range presumably included Singapore, though published historical records are unavailable (e.g., Chasen 1925). The Asian Golden Cat, like other moderate to large sized wild cats (i.e., clouded leopard Neofelis), is considered extirpated from Singapore.

Thailand: The Asian Golden Cat appears to be widely distributed throughout Thailand’s highly fragmented forests according to the results of a recent literature review (Petersen et al. 2021). As is common elsewhere across the species range, most records in Thailand are derived from Tiger survey bycatch data; therefore, generalizations about possible occurrence in un-surveyed areas should be made cautiously. Recent published camera-trap records (2010 onwards) confirm presence in most major forest complexes (FC) including the Western FC, Kaeng Krachan FC, Khlong Saeng – Khao Sok FC; Hala Bala FC, Eastern FC, Dong Phayayen – Khao Yai FC, Phu Khieo – Nam Nao FC, and Lum Nam Pai-Salawin (FC). The species’ status in less frequently surveyed areas, however, is uncertain. Specifically, there are a lack of recent published records from the relatively unexplored forest complexes in northern (i.e., Sri Lanna – Khun Tan FC, Doi Phu Kha – Mae Yom FC, Mae Ping – Om Koi FC, and Phu Meang-Phu Thong FC), northeastern (i.e., Phu Parn FC and Phanom Dongkrak – Pha Tam), and southern Thailand (i.e., Khao Luang FC and Khao Bantad FC).

Viet Nam: Since 2005, there have been no Asian Golden Cat records, despite extensive camera-trap surveys throughout most forested areas in the country (see reviews in Willcox et al. 2013; Petersen et al. 2021). Given the industrial level hunting that continues to take place in Viet Nam, the species is presumed extirpated. Remnant populations, however, may exist in remote parts of the Annamite Range along Viet Nam’s borders with Lao PDR and Cambodia, as evidenced by recent records of other small cats in these areas (e.g., Marbled Cat, Cao et al. 2022). These occasional occurrences, if they do exist, almost certainly occur at such low population densities as to be considered functionally extinct.

It should be noted that this assessment’s distribution map was constructed with a mapping approach different from the previous assessment’s distribution map. As such, differences between the two maps do not represent genuine changes in the species’ distribution and should not be interpreted as such.

As of this assessment no robust population estimates or population trends exist for the Asian Golden Cat. This lack of data makes it difficult to accurately assess the true population status of this species. Nonetheless, available evidence in the form of published camera-trap survey results suggests there has been a substantial population decline during the assessment period as evidenced by the species’ apparent disappearance from many areas across its range (Petersen et al. 2021), including several protected areas (e.g., Lao PDR’s Nakai – Nam Theun National Park, Coudrat et al. 2014, Coudrat 2019), landscapes (e.g., Cambodia’s Eastern Plains, Gray et al. 2012), and even countries (e.g., Viet Nam, Willcox et al. 2014). Indeed, multiple camera-trap surveys in otherwise suitable habitats have reported low numbers of detections or no detections at all (e.g., Moo et al. 2017). However, declines in population are expected to decrease in the future as the species becomes increasingly restricted to a few “safe” havens, mostly located in the Eastern Himalayas, Thailand, Malaysia, and Sumatra, provided that hunting pressures do not increase in these areas and remain unmitigated elsewhere (i.e., other populations will trend towards extinction; see Geographic Range / Population / Threats).

A recent modelling paper estimated the amount of habitat where Asian Golden Cats would be expected to occur at frequencies greater than chance (defined using predicted-to-expected ratios > 1.0, following Hirzel et al. 2006) has declined by 68% between 2000 and 2020 and is projected to decline by a further 18% between 2020 and 2040 (Petersen et al. 2021). However, a decline in habitat occupied/area of occupancy (AOO) generally does not translate to a 1:1 decline in population size. Therefore, we conservatively assume for this assessment that the percent decline in mature individuals is at least half of the percent decline in habitat/AOO, resulting in a suspected past population decline of 34% and projected future decline of 9% over the previous and next three generations, respectively. The assumption that the percent decline in mature individuals was half the percent decline in AOO, is based on the premise that declines in AOO are more likely to occur in areas with lower population densities (see Assessment Rationale for justification regarding the ratio of decline).

Although reliable population estimates are lacking, educated guesses can be made using simplistic assumptions (see Online Supporting Material for assumptions and country-by-country breakdown of population size). Borrowing heavily from published population estimates of the sympatric clouded leopard (Neofelis sp.), this assessment inferred a global population of approximately 7,000 mature Asian Golden Cat individuals (plausible range: 1,000–12,000; rounded to the nearest 1,000 to emphasize the lack of precision). Assuming a 34% decline over the past twenty years suggests the global population size in 2000 was approximately 10,000 mature individuals (1,000–18,000), resulting in a naïve calculated average additive mortality of 150 mature individuals per annum. However, these estimates should be interpreted with caution due to the simplistic assumptions and high degree of uncertainty in the estimates.

The Asian Golden Cat is strongly associated with closed-canopy forested habitats and can be found in a variety of tropical, subtropical, subalpine, and degraded forests (Grassman et al. 2005, Thinley et al. 2015. Vernes et al. 2015, Petersen et al. 2021). Modern records of the species in more open-canopy forests, such as dry deciduous forests, are scarce (e.g., Gray et al. 2014). It is unclear whether this scarcity is due to these habitats being less suitable, or if it results from heighted hunting pressures in these areas, which are often more accessible to humans compared to denser, closed-canopy forests. Less frequently, the species has been recorded in more open habitats adjacent to forests, including grasslands, alpine scrub, and rocky areas (e.g., Choudhury 2007). Asian Golden Cats have been detected across a wide range of elevations, particularly in the Eastern Himalayas, where the species has been detected at elevations ranging from less than 100 meters to approximately 4,600 meters above sea level (Penjor et al. 2021). This closely matches the elevational range of tree and shrub cover in the region, which extend to approximately 4,000-5,000 meters above sea level depending on local conditions (Miehe et al. 2007). Asian Golden Cats are polymorphic, with at least six different colour morphs documented (e.g., Nijhawan et al. 2019). The degree of polymorphism present within a population appears to vary with latitude and is seemingly greatest in the Eastern Himalayas, northern Myanmar, and southwestern China and lowest in Peninsular Malaysia and Sumatra (e.g., Patel et al. 2016). This latitudinal decline in polymorphism is consistent with a southward population expansion throughout the Late Pleistocene/Early Holocene and is presumably the result of local adaptation and founder effects as subtropical and tropical habitats become increasingly more homogeneous from north to south (Patel et al. 2016, Nijhawan et al. 2019).

Little is known about the behaviour of the Asian Golden Cat. Multiple camera-trap studies from across the species’ range have found the species to be cathemeral or mostly diurnal (e.g., Lynam et al. 2013). Similar activity patterns were documented by a radio-telemetry study monitoring two Asian Golden Cat individuals in Thailand’s Phu Khiao Wildlife Sanctuary (Grassman et al. 2005).
Available evidence suggests the species likely possesses a highly variable and opportunistic diet of small-to-medium sized vertebrates (0-28 kg; e.g., Kamler et al. 2020). Prey selection presumably varies by individual and population, with habitat type, prey availability, and the presence of larger carnivores all likely mediating factors at the population level. Across all studies, small vertebrates (< 2 kg) appear to be an important component of the species’ diet (Grassman et al. 2005, Kawanishi and Sunquist 2008, Xiong et al. 2017, Kamler et al. 2020). Depending on the population, other important prey species may include muntjacs (Muntiacus; Kamler et al. 2020), chevrotains (Tragulus; Kawanishi and Sunquist 2008), porcupines (Hystricidae; Kamler et al. 2020), primates (Kawanishi and Sunquist 2008), Galliformes (Xiong et al. 2017), and small carnivores (Lim 2002, Xiong et al. 2017, Kamler et al. 2020).

Published home range estimates exist for only two individuals in Thailand’s Phu Khiao Wildlife Sanctuary (Grassman et al. 2005). These home range estimates, belonging to one female and one male inhabiting semi-evergreen forest were reported to be 33 km² and 48 km², respectively (Grassman et al. 2005). Home range sizes presumably vary by habitat and since Asian Golden Cats inhabit a variety of habitats, the representativeness of these home range estimates is uncertain. Daily distances travelled by the two Phu Khiao individuals varied significantly, particularly for the male individual which was observed moving anywhere from 0.6 km to 9.2 km in a day (Grassman et al. 2005). These daily distances travelled are consistent with an incidental observation during a 2017 camera-trap survey in southern Thailand’s Khlong Saeng Wildlife Sanctuary, where an individually identifiable male was photographed at two distinct locations, three days, and 5.3 km apart (W. Petersen, pers. comm. 2024).

The Asian Golden Cat faces multiple threats across its range, the most significant of which are habitat loss and illegal hunting. These threats, however, are not particularly well understood beyond reasonable inferences, as the species has received little dedicated research attention. As a forest dependent species, the Asian Golden Cat is threatened by the loss and degradation of forest habitats due to human activities, including agriculture, logging, mining, and infrastructure development projects. Rates of deforestation and forest disturbance across large parts of the species’ range remain the highest in the world despite improvements in environmental governance since the 1990s (Stibig et al. 2014, Liu et al. 2023). Deforestation is almost invariably accompanied by high levels of illegal hunting, either by those implementing the deforestation or by providing new access points for poachers (see discussion below). In addition, the indirect loss of functional connectivity due to habitat loss and degradation is likely impacting the viability of many individual populations. This loss of connectivity is likely to get worse in the future, particularly in Myanmar and the Eastern Himalayas where proposed infrastructure projects (i.e., hydropower, roadways, railways) are expected to become a significant issue for wildlife (e.g., Grumbine and Pandit 2013, Kaszta et al. 2020). Illegal hunting poses a significant threat to the Asian Golden Cat and likely represents the single greatest driver of population declines over the past three generations (Petersen et al. 2021).

Asian Golden Cats appear to be highly sensitive to indiscriminate wire snaring based on several lines of evidence. This is most immediately apparent considering the species’ disappearance from industrially snared areas, as documented by long-term monitoring studies (e.g., Nakai-Nam Theun National Park; Coudrat et al. 2014, Coudrat 2019). Indeed, across the species’ range there have been a number of camera-trap surveys in otherwise suitable habitats, including in large, forested landscapes (1,000+ km²), reporting low numbers of detections or no detections at all (e.g., Gray et al. 2012, Willcox et al. 2014, Moo et al. 2017). A review of 145 published camera-trap surveys from forests across the Asian Golden Cat’s range found more than half (54%) did not detect the species (Petersen et al. 2021). These negative findings were primarily concentrated in China, Viet Nam, Cambodia, and Lao PDR, countries that have experienced the most dramatic levels of trade-driven hunting and indiscriminate wire-snaring (Harrison et al. 2016, Gray et al. 2018, Tilker et al. 2019). However, significant population declines due to illegal hunting are not expected to be restricted to these countries. Indeed, in Myanmar, traders at illegal wildlife markets had expressed to surveyors that Asian Golden Cats were very rare in parts of the country as early as 2000, with the traders citing over-hunting as the cause (Shepherd and Nijman 2008). 

Additional possible threats to Asian Golden Cats that are either local in nature or require further research and analysis include, but are not limited to, retaliatory killing in response to livestock depredation (e.g., McCarthy 2013), prey depletion (Wolf and Ripple 2016), and inbreeding (Saunders et al. 1991).

It is unclear to what extent Asian Golden Cats are specifically targeted by poachers for the illegal wildlife trade. However, they are opportunistically shot (e.g., Bal et al. 2003) and caught in wire snares set for other animals (e.g., https://youtu.be/MRA2MN-TQTQ). Once harvested, Asian Golden Cats are primarily exploited for their pelts and other parts, which may be used for decoration, jewellery, and traditional medicine (Duckworth et al. 1999, Khan 2008, Aiyadurai et al. 2010, Lau et al. 2010, Pusparini et al. 2014, DoFPS 2015, Nijman and Shepherd 2015). Older sources have noted some cultural beliefs among local peoples in Southeast Asia (e.g., Thailand, Myanmar, Lao PDR), including beliefs that the fur and flesh of Asian Golden Cats possessed supernatural properties and protected against Tigers (e.g., Lekagul and McNeely 1977). However, it is not apparent that these beliefs have been significant enough to drive dedicated hunting of the species.

The Asian Golden Cat is listed under Appendix I of CITES and formally protected by national legislation over most of its range. However, in all range countries, the implementation of conservation laws faces challenges, including limited resources and governance issues.
Protected areas represent the primary means of protecting the species and its habitat. However, populations have declined even within protected areas and overlap between protected areas and areas predicted to be suitable is estimated to be low in some parts of its range (Greenspan et al. 2020, Petersen et al. 2021). Expanding protected area coverage in a significant or meaningful manner is likely not feasible for the foreseeable future. Therefore, improving the effectiveness of existing protected area management is paramount to the species’ long-term survival.
There has been an increase in camera-trap surveys across the species’ range since the last assessment. Most of these surveys have targeted large popular mammals, including Tiger, Snow Leopard (Panthera uncia), bears (Ursidae), and Saola (Pseudoryx nghetinhensis). These surveys have certainly improved our understanding of the Asian Golden Cat’s status, albeit to a limited degree. Expanding survey efforts to new areas where these ‘flagship’ species do not occur is likely to provide new insights into the Asian Golden Cat’s current distribution and population (Petersen et al. 2021).
Given that much of the Asian Golden Cat’s habitat occurs in transboundary conservation landscapes (e.g., Greenspan et al. 2020, Petersen et al. 2021) the species should be considered in transboundary conservation planning (Farhadinia et al. 2021).