|Scientific Name:||Axis axis|
|Species Authority:||(Erxleben, 1777)|
Cervus axis Erxleben, 1777
|Red List Category & Criteria:||Least Concern ver 3.1|
|Assessor(s):||Duckworth, J.W., Kumar, N.S., Anwarul Islam, M., Sagar Baral, H. & Timmins, R.|
|Reviewer(s):||Brook, S.M. & McShea, W.J.|
Chital is listed as Least Concern because it occurs over a very wide range within which there are many large subpopulations. Although it is still declining in some sites (particularly outside protected areas), at the species level any such declines are at nowhere near the rate required to qualify for listing even as Near Threatened. Historical declines may have been higher, but these occurred outside of the three generation window (<30 years) used for purposes of applying Red List Criteria. Listing as Least Concern recognizes that there are two significant conservation issues with this species. Firstly, current densities are mostly well below what the habitat could support (and have been for decades), and secondly, the long-term persistence of nearly all subpopulations is dependent upon well secured protected areas: anything which caused the breakdown of current effective protection would allow a rapid rise in hunting levels and perhaps of domestic stock-grazing. These are the factors with which current Chital numbers are in an uneasy and fragile relationship. If such changes were to occur across a significant part of the range, reassessment of Red List status would be required: without effective protection, Chital’s population trend would emulate that of Eld's Deer Rucervus eldii, another herding deer of rather open forests, but with a geographic range covering areas without long-standing effective protected areas. Regular monitoring of the status of Chital subpopulations would be prudent for this species.
|Previously published Red List assessments:|
|Range Description:||The Chital occurs over 8–30°N in India (including Sikkim), Nepal, Bhutan, Bangladesh and Sri Lanka (Grubb 2005, Raman 2013). The western distribution boundary is formed by eastern Rajasthan (e.g. Sariska, Ranthambore and Keoladeo Ghana) and Gujarat (e.g. Sasan Gir). The northern boundary runs along the bhabar-terai belt of the foothills of the Himalaya from Uttar Pradesh and Uttaranchal through Nepal, northern West Bengal and Sikkim to western Assam and the forested valleys of Bhutan below 1,100 m asl. The eastern boundary runs through western Assam (Golapara and Kamrup district as far east as the Dhunsiri River in Darrang district) to the Sunderbans of West Bengal (India) and Bangladesh. Sri Lanka is the southern limit (Gee 1964, Schaller 1967, Raman 2013). Chital occur throughout the rest of peninsular India sporadically in the forested areas (Sankar and Acharya 2004), but in Bangladesh, it now occurs only in the Sundarbans, having vanished from the central, northeast and southeast regions (Md Anwarul Islam in litt. 2008).|
Chital has been introduced to the Andaman Islands (India, during 1925–1930; Banerji 1955), Argentina, Armenia, Australia, Brazil, Croatia (islands of Brijuni; Mitchell-Jones et al. 1999), Moldova, Pakistan, Papua New Guinea, Ukraine, Uruguay and the USA (California, Florida, Hawaiian Islands and Texas; Grubb 2005, Raman 2013). These introduced subpopulations have not been mapped. Not all introductions have succeeded: for example, some were introduced to west-central Slovenia (from the Brijuni islands) in the late 1940s or in 1950, but this introduction failed and is now therefore frequently reported as having been of Fallow Deer Dama dama. One male, shot on 12 October 1950 and now in the Natural History Museum of Slovenia, proves the identification (Krystufek 1999). Managed herds occur in parks throughout the native and introduced range and in many other areas.
Native:Bangladesh; Bhutan; India (Andaman Is. - Introduced); Nepal; Sri Lanka
Introduced:Argentina; Armenia (Armenia); Australia; Brazil; Croatia; Moldova; Pakistan; Papua New Guinea; Ukraine; United States (California, Florida, Hawaiian Is., Texas); Uruguay
|Range Map:||Click here to open the map viewer and explore range.|
|Population:||Chital declined drastically throughout its range up until the first two-thirds of the 20th century (see under Major Threats). Karanth et al. (2010) documented an estimated average extinction rate of 45% over the last 50 years in the Indian sub-continent. It is however "locally" abundant in well protected parts of its range in mixes deciduous habitats. In India it occurs in 123 protected areas and forest tracts (National Wildlife Database, Wildlife Institute of India in Sankar and Acharya 2004). There are some large subpopulations in Nepal (e.g. Moe and Wegge 1994) where the population is probably currently stable and is anticipated to remain so in the immediate future (Hem Sagar Baral in litt. 2008). Thousands survive in the Sundarbans mangrove forest, Bangladesh, and there are a few introducedsub populations on coastal islands in the south (Md Anwarul Islam in litt. 2008).|
The reported ecological densities of Chital mostly fall within three to 50 animals per km2 in India: Bhadra Tiger Reserve, 4.51 +/- 1.05 (SE) per km2 (Jathanna et al. 2003); Madhya Pradesh Pench National Park dry deciduous forest, 51.3 animals per km2 (Karanth and Nichols 2000); Kanha moist deciduous forest, 49.7 animals per km2 (Karanth and Nichols 2000); Nagarahole moist deciduous forest, 50.6 animals per km2 (Karanth and Sunquist 1992); Bandipur dry deciduous forest, 20.1 animals per km2 (Karanth and Nichols 2000); Tadoba-Andhari dry deciduous forest, 3.2 animals per km2 (Karanth and Kumar 2005); Maharashtra Pench dry deciduous forest, 5.8 animals per km2 (Karanth and Kumar 2005); Ranthambore semi-arid dry deciduous forest, 38.4 animals per km2 (Kumar 2000); BRT mixed deciduous forest, 9.4 animals per km2 (Karanth 2012); Dandeli-Anshi mix of evergreen and deciduous forest, 0.6 animals per km2 (Karanth 2012); Panna dry deciduous forest, 10.2 animals per km2 (Chundawat and Karanth unpublished data); Kawal dry deciduous forset two animals per km2 (Siddique 2010), and Gir semi-arid dry deciduous forest, 50.8 animals per km2 (Khan et al. 1996). Some parts of the well-protected areas in Nagarahole and Bandipur are known to harbour densities as high as 80–100 Chital per km2 (Kumar 2010). Humar (2010) observed high spatial variation in the abundance of Chital in the 1,500 km2 of Nagarahole-Bandipur National Parks, which ranged between zero to 100 animals per km2. Kumar (2010) also found that Chital densities positively responded to higher levels of protection, forage quality, flat terrain and water availability. The highest population densities, of around 200 Chitals per km2, are reported for the Bardia National Park, Nepal (Naess and Andersen 1993, Moe and Wegge 1994) and for the reintroducedsub population in Guindy National Park, southern India (Menon 1982, Raman et al. 1996). These high densities reflect habitat and food availability in the former area (Moe and Wegge 1994), and supplementary feeding and low predation in the latter (Raman et al. 1996). Population densities in marginal habitats tend to be lower (Raman 2013; K.U. Karanth and N.S. Kumar unpublished data). Chital is the most abundant ungulate in Nagarahole, and reaches higher densities in moist than in dry deciduous forests (Karanth and Sunquist 1992). The recorded Bhadra density is low, reflecting poaching and livestock grazing (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). A study at Nagarahole National Park compared an area which was only moderately hunted with a heavily hunted site. This found respective densities of 65 and 10 Chitals per km2 (Madhusudan and Karanth 2002).
The Chital is almost completely dependent on active protection. Were this to be removed, the species' status in the 1970s suggests that rapid declines would occur. Even now, a very large proportion of its range supports subpopulations at significantly lower densities than the habitat could support.
The only subpopulation in Europe is on the islands of Brijuni (off Istria, Croatia), but B. Krystufek (pers. comm. 2008) has traced no information on its current status. Information has not been sought for this account on introduced subpopulations elsewhere, because they do not contribute to assessing the species’ Red List status.
|Current Population Trend:||Unknown|
|Habitat and Ecology:||Chital thrive in a variety of habitats, but avoid extremes such as dense moist (evergreen) forests and open semi-desert or desert. Moist and dry deciduous forest areas, especially adjoining dry thorn scrub or grasslands, appear to be optimal, and highest densities of Chital are reported from these habitats. Short grasslands of the terai, swampy meadows and glades adjoining forest areas, coastal dry evergreen forests, mixed forests or plantations with Teak Tectona grandis and Sal Shorea robusta are also used, and indeed over much of northern and southern India, its distribution closely matches that of Sal and Teak, respectively (Raman 2013). Chital is particularly frequent in grassland–forest interface, edge, and other ecotones (Krishnan 1972). Eisenberg and Seidensticker (1976) opined that dry deciduous habitats with scrub is the favoured habitat, while Karanth and Sunquist (1992) found mixed forests with teak plantations, moist deciduous patches and swampy grasslands to support high abundance of Chital. Kumar (2010) found that well-watered and well-protected moist deciduous forest patches in gently undulating terrain supported high Chital densities. Short grasslands are important because they provide little cover for predators such as Tiger Panthera tigris (Moe and Wegge 1994). The introduced subpopulation in Andaman Islands inhabits evergreen forests (Sankar and Acharya 2004) but native subpopulations are absent from the rainforest areas of the mainland. They tend to be only visitors to dense forests, to those adjoining more open habitats. Riverine forests within the Bardia National Park in lowland Nepal are highly used by the deer for shade and cover during the dry season. The forest also provides good foraging with regard to fallen fruit and leaves that are high in nutrients needed by the deer. Four factors were identified by Schaller (1967) as delineating Chital’s distribution: (1) the need for water; (2) the need for shade; (3) an avoidance of high, rugged terrain; and (4) a preference for grass as forage. Although several observers have noted that Chital occurs mostly in flat areas and avoids hills and slopes (Schaller 1967, Khan 1996), this may not hold in areas where preferred habitats or forage is also available on slopes (Raman 2013, Kumar 2010). It occurs in both hilly and flatter terrain, mainly the latter, in the Terai Arc Landscape of India (Johnsingh et al. 2004). In the Siwalik hills, Bhat and Rawat (1995) found that Chital preferred slopes of 11–30°, while slopes exceeding 30° were used less. Also, use of south, southeast, and east aspects was higher than of north, northeast, northwest, and west aspects, reflecting the warmer environment of the former aspects. There was no difference in average Chital density in the hills and plains (Bhat and Rawat 1995). A study of coffee estates around Bhadra Wildlife Sanctuary, India, recorded Chital widely, including in coffee areas up to 14 km of the sanctuary’s boundary (Bali et al. 2007).|
Habitat use varies seasonally, reflecting food availability. Chital uses more wooded habitat during the cool-dry season and early summer (November to May), where fallen fruit, leaf litter, and browse are available. In open grassland and tropical dry thorn forest, Chital density increases with the onset of monsoon rains and flush of plant growth (Mishra 1982, Moe and Wegge 1994, Khan 1996, Raman et al. 1996). In areas of their distribution with a mosaic of forest and grassland habitats, seasonal patterns in habitat use may be complex. In the Himalayan terai, Chital use of habitats with high grass availability increased substantially in the weeks following cutting and burning of grasses in January–February, attributed to fresh flush of grass growth after the burns and with the onset pre-monsoon and monsoon rains nearly two months later (Mishra 1982; Moe and Wegge 1994, 1997). Similar behaviour has been reported from the grasslands of Bandipur Tiger Reserve (Johnsingh 1983).
Chital easily habituates to human presence, and herds often congregate in open areas near habitation or forest camps to spend the night, possibly due to greater safety from predators and poachers that shy away from these areas (Raman 2013).
Chital eats a wide variety of plants: about 160–190 have been recorded from across the species' range. It is predominantly a grazer but consumes more fallen leaves, flowers and fruits in winter/dry season (Sankar 1994, Sankar and Acharya 2004, Raman 2013). In addition to plant soft matter, crabs (in the Sunderbans; Stanford 1951), mushrooms (in Nepal; Moe and Wegge 1994) and rarely, bark (Raman et al. 1996) are eaten. Close to human habitation, rubbish and even human faeces are occasionally taken (Raman et al. 1996). Antler and bone chewing is also common. In Wilpattu, Sri Lanka, all age and sex classes are osteophagous, but such feeding was more common in velvet-antlered males, doubtless reflecting mineral needs during antler growth and mineralisation (Barrette 1985). Chital usually drinks water once a day, more frequently in summer. This restricts them to forest tracts with assured presence of water, even if only widely scattered.
In lowland Nepal, an individual’s total range incorporates a core area of about 32 hectares surrounded by foraging and cover areas of about 140 ha for females and 195 ha for males (Moe and Wegge 1994). Variation in range size occurs with site, season, sex and age of the animal. The basic social unit is a matriarchal family group, normally consisting of an adult female, her offspring from the previous year, and a fawn (Ables 1974). The usual herd is composed of two or more such family units and is often accompanied by individual deer of mixed sex and age-classes. Chital exhibits a fission-fusion system, or fluid group formation and dissolution (Schaller 1967, Mishra 1982, Barette 1991). Group composition changes frequently during feeding periods, during the rut when males frequently join groups of females (Schaller 1967), and while fleeing from predators (Dinerstein 1980). These social groupings of Chital do not remain permanent (Schaller 1967, Eisenberg and Lockhart 1972). Groups may number up to 150 or more individuals (De and Spillit 1966, Schaller 1967, Eisenberg and Lockhart 1972, Krishnan 1972, Fuchs 1977, Karanth and Sunquist 1992), sometimes even more: N.S. Kumar (pers. comm. 2008) counted 211 in one group during rainy season in Nagarahole and 203 in one group at Pench-Maharashtra near a water reservoir in summer. Measured sex ratios have all been biased towards females (Sankar and Acharya 2004 and references therein). Pariwakam (2006) observed nearly 10,500 Chital in Bandipur and estimated the proportion of Chital in different age and sex classes as stags 27%, does 57% and fawns 16%. In neighbouring Nagarahole, age-sex categories of Chital were adult stags 26%, adult does 36%, yearling males 8%, yearling females 9% and young 21% (Karanth and Sunquist 1992). Breeding can occur at any time of year but there is some peaking at any given locality (Sankar and Acharya 2004 and references therein). Heavy mortality of fawns in early weeks has been observed by several workers and fawn survival appears to be a key determinant of Chital population growth (Schaller 1967). Schaller (1967) estimated an annual fawn mortality of 48% in Kanha, Sharathchandra, and Gadgil (1975) estimated a constant monthly mortality of 26% over first nine months in Bandipur, Raman (1996) estimated a mean monthly mortality of 9.7% in Guindy. Pariwakam (2006) for the first time used a rigorous photographic capture-recapture approach to estimate the fawn mortality rate, and found it to be 66% over a six week study period in Bandipur. Further information on sociality and breeding is synthesised by Sankar and Acharya (2004) and by Raman (2013). Over a 10-year time period, Karanth and Kumar (unpublished data) have observed annual fluctuations in the Chital subpopulations in Nagarahole and Bandipur ranging between population densities of 10 to 40 animals per km2.
Chital is a prolific breeder, as documented by several empirical studies of the speed of increase by newly introduced subpopulations or in those where a factor restraining subpopulations was removed (Raman 2013 and references therein). In Bhadra, following the departure from the park of human settlements and consequent removal of anthropogenic pressures on Chital and habitats, Chital subpopulations bounced back by nearly seven times in fewer than four years (K.U. Karanth and N.S. Kumar unpublished data). Karanth et al. (1999) earlier documented their empirical observations of the recovery of Chital subpopulations in Nagarahole. This and its diverse diet and habitats allow high density where threats are controlled. It is even considered to be a pest in the Andamans (Banerji 1955).
The main causes of death are predation, diseases and accidents. Occasionally, stags kill each other when fighting (Sankar and Acharya 2004 and references therein). Predation is by far the major cause of Chital mortality. Older Chital stags are more susceptible to it than are younger stags (Johnsingh 1983, Patel 1992, Karanth and Sunquist 1995). This may be due to their being less vigilant during rut, to their separation from the group after the rut, or to weakening from injuries from conflicts. In Kanha, Chital remains were found in about 52% of Tiger faeces and 59% of Leopard Panthera pardus faeces analysed (Schaller 1967). In Bandipur, Chital is the most important prey in terms of the biomass taken by Dhole (78%), Leopard (55%) and Tiger (19%; Andheria et al. 2007). Even in terms of the relative number of individuals taken, Chital is the predominant prey among the three large sympatric predators (Tigers about 33%, Leopards about 39% and Dholes about 73% in Bandipur; Andheria et al. 2007). In adjoining Nagarahole remains were found in about 31% of Tiger faeces, 44% of Leopard faeces, and 50% of Dhole faeces (Karanth and Sunquist 1995). In Sariska, around 54% of the faeces of Tiger and 21% of Leopard faeces contained Chital remains (Sankar 1994). Chital remains were found in about 53% of Tiger faeces in Pench (Biswas and Sankar 2002) and 61% of Tiger faeces in Ranthambore (Bagchi et al. 2003).
Each Chital spends a major portion of its life in foraging, resting, and wandering within its range, with the relative extent of these activities determined by season (Schaller 1967). In a day, peak feeding times are around dawn and dusk. There are usually two major resting periods, before dawn and mid-day (Sankar and Acharya 2004).
Considerable further detail on ecology, drawn from the relative wealth of studies on the species, with each item precisely referenced to source, is provided by Raman (2013).
|Generation Length (years):||10|
|Use and Trade:||Chital are hunted for food, sport, and a variety of other purposes. It is unclear as to the numbers of captive animals kept within the native range and even if such animals are used to supply the same markets as wild caught animals. Introduced subpopulations almost certainly do not supply the same markets as wild caught animals from the species native range.|
There are presently no major global-level threats to Chital, although densities are widely below ecological carrying capacity, through hunting and competition with domestic livestock. There were substantial declines and local extinctions, driven by hunting for meat, extermination as an agricultural pest, and habitat conversion, particularly during British rule of India and adjacent countries, and immediately after independence (Raman 2013). Fewer than 20 years after independence, Schaller (1967) wrote that "...the species has declined drastically throughout its range in India, and is now only locally abundant in some sanctuaries and forest tracts. The remaining populations are highly vulnerable to poaching, habitat destruction, and other forms of decimation". The habitat loss of the past few centuries means that subpopulations are now rather fragmented. Now, in India, most subpopulations appear secure within the modern protected area network (Raman 2013), but those outside (now highly localised) are under rapid decline due to habitat conversion and extensive hunting (N.S. Kumar pers. comm. 2008). A relaxation of protection can lead to rapid decreases. For example, Chital used to be numerically the most abundant large herbivore in the Wilpattu National Park (Sri Lanka), but numbers declined significantly due to poaching which increased during management breakdown during the civil war, when its meat was even being sold next to the park. Poaching has also risen, for the same reason, in several other national parks in Sri Lanka (Santiapillai and Wijeyamohan 2003). Where not prevented by effective conservation measures (active protection through patrolling and law enforcement, backed up by adequate awareness), people avidly hunt and poach Chital throughout their Indian range (Madhusudan and Karanth 2000, Madhusudan and Karanth 2002, Sankar and Acharya 2004, Bali et al. 2007) and there are occasional cases in even the best secured protected areas such as Corbett Tiger Reserve (Johnsingh et al. 2004). Many protected areas are well enough secured that the species has thrived well and, is now locally abundant (Sankar and Acharya 2004) and in such areas poaching of Chital is a more serious conservation problem for the large predators (every deer poached reduces predators’ food base; Karanth et al. 2004) than it is for Chital itself. In many other protected areas (especially those with a lower public profile) and for areas outside the conservation system, subpopulations are severely restrained by hunting. For example, densities in Bhadra Tiger Reserve are very low by comparison with what the habitat should support because of poaching with snares, dogs and shotguns, and also grazing competition with domestic stock (Jathanna et al. 2003), and the density was 87% lower in a heavily hunted area of Nagarahole National Park than in a well secured area (Madhusudan and Karanth 2000, 2002). Even though all hunting is illegal in this protected area, protection efficacy is uneven across the area. The Chital is one of the two most commonly hunted mammal species in the national park, partly because various facets of its behaviour and ecology such as herding behaviour and attachment to open habitat allow its ready detection and killing, and quick entry and exit by poachers. It is therefore exposed to far higher hunting pressure than are the ungulates which are solitary and spend much time in dense cover (Madhusudan and Karanth 2002). Poaching is probably operative to a greater or lesser extent in most subpopulations, but at low enough levels that recent decades have not seen, with Chital, the frequent local extirpations from areas of prime habitat of earlier decades.
The most serious threat, in areas where poaching and habitat conversion are well controlled, is the reduction in carrying capacity through competition with livestock, especially during the pinch season as observed in Sariska (Sankar 1994); Chital and livestock are known to have dietary overlap (Raman 2013). The problem has been documented almost throughout Chital’s range but awareness that it is a problem at all remains so low that it is not even recognised as a key conservation issue in many protected areas (e.g. Mathai 1999). In Gir Lion Sanctuary and National Park, Chital population density increased 14-fold from 3.57 animals per km2 in 1970–1971 (Berwick 1974) to 50.8 animals per km2 in 1989 (Khan 1996, Khan et al. 1996). This was attributed to the rapid and complete removal of pastoral settlements, their livestock, and a total ban on several thousand migratory livestock. Dung densities of Chital and livestock were also negatively correlated in Gir, indicating avoidance and possible competitive interaction between the species. With removal of human impact and increase in forage availability, Chital subpopulations increased, as testified by higher Chital densities in the vicinity of abandoned settlements (nesses; Sharma and Johnsingh 1995). Similarly, in Bardia National Park (Nepal), protection from livestock grazing (and logging) in 1975 increased measured Chital subpopulations from 30–34 per km2 in 1977 (Dinerstein 1980) to over 200 per km2 in the early 1990s (Naess and Andersen 1993, Moe and Wegge 1994). In Bandipur Tiger Reserve, mean densities of Chital were 11 times higher in livestock-free areas than in adjacent livestock-grazed areas. In shared grazing areas, these Chital densities declined sharply with increasing livestock densities. In the studied grazed area, halving the livestock density allowed an increase in Chital density by a factor of five (Madhusudan 2004). 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). All these pressures interact to have, overall, a major depression of Chital densities. In Bhadra, following the departure from the park of human settlements and consequent removal of anthropogenic pressures on Chital and habitats, Chital subpopulations bounced back by nearly seven times in fewer than four years (Karanth and Kumar unpublished data). Karanth et al. (1999) earlier documented their empirical observations of the recovery of Chital subpopulations in Nagarahole.
Chital are susceptible to livestock-borne diseases such as rinderpest (Schaller 1967) and foot-and-mouth disease (Sankar 1994) but the current population is too widespread for these to rank as potential global-level threats. Accidents, especially from speeding vehicles, are a cause of Chital mortality but occur rarely within protected areas and cannot be significant at the global level. Many Indian forest areas are severely encroached by exotics such as Lantana camara, Parthenium spp. and Chromolaena odorata (= Eupatorium odoratum), and these are suspected to effect major changes to forest structure (Hiremath and Sundaram 2005): but their effects on Chital warrants further study. Wild-ranging domestic dogs are also likely to be a problem (Raman 2013), but no study quantifying their effects has been traced. There are no predictable threats to the Sundarbans subpopulation of Bangladesh, but as a low-lying area extreme weather events might cause episodic major population removal, as happened with hurricane Sidr in November 2007 (Md Anwarul Islam in litt. 2008).
Chital is protected under Schedule III of the Indian Wildlife Protection Act (1972) (Sankar and Acharya 2004) and under the Wildlife (Preservation) (Amendment) Act, 1974 of Bangladesh (Md Anwarul Islam in litt. 2008). It occurs in many protected areas. Legal protection as a species and a network of functioning protected areas are the two cornerstones of its current healthy conservation status. Subpopulations exceeding 20,000 Chital probably occur in and around a handful of conservation areas within India: the belt of about 3,000 km2 between Koh river and Haldwani including the Corbett Tiger Reserve; the Gir Protected Area (about 1,400 km2); Kanha Tiger Reserve (about 2,000 km2); and the Nilgiris–Western Ghats sector including Nagarahole, Bandipur, and Mudumalai (about 5,000 km2; Raman 2013). Protected areas support more Chitals than do non-protected areas in the Terai Arc Landscape of India, although there is not currently such a great difference in densities as with the grassland species (Barasingha Rucervus duvaucelii and Hog Deer Axis porcinus; Johnsingh et al. 2004). Ongoing habitat conversion trends outside protected areas will continue to increase the relative proportion of the total Chital population that they hold, and the maintenance of an extensive network of functional protected areas will remain the foundation of this species’ healthy conservation status. Part of this responsibility is vigilance by staff and partners of illegal poaching, which takes place at varying levels in most of the species range. Some recent cases have involved high-profile public role models, such as actors, poaching Chital and these warrant heavy court penalties. There is a strong case for prevention of livestock grazing in protected areas which hold Chital, partly to reduce risks of disease transmission, but mostly to prevent artificially low densities of Chital being forced through competition (see Threat Section).
Chital subpopulations have been studied in: Corbett (De and Spillit 1966), Kanha (Schaller 1967), Bandipur (Johnsingh 1983, Kumar 2010), Nagarahole (Karanth and Sunquist 1992, Kumar 2010), Sariska (Sankar 1994), Gir (Khan et al. 1995, 1996), Guindy (Raman 1996, Raman et al. 1996), Pench (Biswas and Sankar 2002), Ranthambore (Bagchi et al. 2003) in India, Chitwan (Seidensticker 1976, Mishra 1982) and Karnali-Bardia (Dinerstein 1980; Moe and Wegge 1994, 1997) in Nepal, and Wilpattu (Eisenberg and Lockhart 1972) in Sri Lanka.
Ables, E.D. 1974. The Axis Deer in Texas. The Caeser Kleberg Research Programme and The Texas Agricultural Experiment Station. A & M University System, Texas.
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.
Bagchi, S., Goyal, S.P. and Sankar, K. 2003. Prey abundance and prey selection by tigers (Panthera tigris) in a semi-arid, dry deciduous forest in western India. Journal of Zoology (London) 260: 285-290.
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.
Banerji, J. 1955. Wild animals in the Andaman islands. Journal of the Bombay Natural History Society. 55: 256.
Barrette, C. 1985. Antler eating and antler growth in wild Axis deer. Mammalia 41: 1-34.
Barrette, C. 1991. The size of Axis deer fluid groups in Wilpattu National Park, Sri Lanka. Mammalia 55: 207-220.
Berwick, S.H. 1974. The community of wild ruminants in the Gir forest ecosystem. Yale University.
Bhat, S.D. and Rawat, G.S. 1995. Habitat use by Chital Axis axis in Dhaulkhand, Rajaji National Park, India. Tropical Ecology 36: 177-189.
Biswas, S. and Sankar, K. 2002. Prey abundance and food habit of tigers (Panthera tigris tigris) in Pench National Park, Madhya Pradesh, India. Journal of Zoology (London) 256: 411-420.
De, R.C. and Spillit, J.J. 1966. A study of the Chital or spotted deer in Corbett National Park, Uttar Pradesh. Journal of the Bombay Natural History Society 63: 576-598.
Dinerstein, E. 1980. An ecological survey of the Royal Karnali-Bardia wildlife Reserve, Nepal. Part III: Ungulate populations. Biological Conservation 16: 5-38.
Eisenberg, J.F. and Lockhart, M. 1972. An ecological reconnaisance of Wilpattu National Park, Ceylon. Smithsonian Contributions to Zoology 101: 1-118.
Eisenberg, J.F. and Seidensticker, J. 1976. Ungulates in Southern Asia: a consideration of biomass estimates for selected habitats.: 293-308.
Fuchs, E.R. 1977. Behaviour. In: E.B. Ables (ed.), The axis deer in Texas, pp. 24-52. Ceasar Kleberg, Texas.
Gee, E.P. 1964. The Wild Life of India. Collins, London, UK.
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.
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. 1983. Large mammalian prey-predators in Bandipur. Journal of the Bombay Natural History Society 80(1): 1-57.
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.
Karanth, K.K., Nichols, J.D., Karanth, K.U., Hines, J.E. and Christensen, N.L. 2010. The shrinking ark: patterns of large mammal extinctions in India. Proceedings of the Royal Society of London, B 277: 1971-1979 277:: 1971-1979.
Karanth, K.U. and Kumar, N.S. 2005. Distribution and dynamics of tiger and prey populations in Maharashtra, India. Final Technical Report. Centre for Wildlife Studies, Bangalore, India.
Karanth, K.U. and Nichols, J.D. 2000. Ecological status and conservation of tigers in India. Centre for Wildlife Studies, Bangalore, India.
Karanth, K.U. and Sunquist, M.E. 1992. Population structure, density and biomass of large herbivores in the tropical forests of Nagarahole, India. Journal of Tropical Ecology 8: 21.
Karanth, K.U. and Sunquist, M.E. 1995. Prey selection by tiger, leopard and dhole in tropical forests. Journal of Animal Ecology 64: 439-450.
Karanth, K.U., Kumar, N.S., Nichols, J.D., Link, W.A. and Hines, J.E. 2004. Tigers and their prey: Predicting carnivore densities from prey abundance. Proceedings of the National Academy of Sciences of the United States of America 101: 4854-4858.
Karanth, K.U. Meta-population dynamics of tigers in the Malenad-Mysore Landscape of Karnataka. Annual Report January-December 2011. Centre for Wildlife studies, Bangalore, India.
Karanth, K.U., Sunquist, M.E., Chinnappa, K.M., Seidensticker, J., Christie, S. and Jackson, P. 1999. Long-term monitoring of tigers: lessons from Nagarahole. Riding the tiger: Tiger conservation in human-dominated landscapes, pp. 114. Cambridge University Press, Cambridge, UK.
Khan, J.A. 1996. Factors governing habitat occupance of ungulates in Gir Lion sanctuary, Gujarat, India. International Journal of Ecology and Environmental Science 22: 73-83.
Khan, J.A., Chellam, R. and Johnsingh, A.J.T. 1995. Group size and age-sex composition of three major ungulate species in Gir Lion Sanctuary, Gujarat, India. Journal of the Bombay Natural History Society 92: 295-302.
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.
Krishnan, M. 1972. An ecological survey of the larger mammals of peninsular India. Journal of the Bombay Natural History Society 69: 322-349.
Kryštufek, B. 1999. Mammals of Slovenia [In Slovenian with English summary]. Prirodoslovni Muzej Slovenije, Ljubljana, Slovenia.
Kumar, N.S. 2000. Ungulate density and biomass in the tropical semi-arid forest of Ranthambore, India. Pondicherry University.
Kumar, N.S. 2010. Assessment of distribution and abundance of ungulate prey using spatial models in Nagarahole and Bandipure Tiger Reserves of India. A Ph. D. dissertation. Manipal Unversity.
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. 2000. Hunting for an answer: is local hunting compatible with large mammal conservation in India? In: J.G. Robinson and E.L. Bennett (eds), Hunting for sustainability in the tropics, pp. 339–355. Columbia University Press, New York, USA.
Madhusudan, M.D. and Karanth, K.U. 2002. Local hunting and the conservation of large mammals in India. Ambio 31(1): 49-54.
Mathai, M. 1999. Habitat occupancy across anthropogenic disturbances by sympatric ungulate species in Panna Tiger Reserve. Saurashtra University.
Menon, R.K. 1982. Observations on cheetal in Guindy National Park, Madras. Cheetal 24(1): 37-40.
Mishra, H.R. 1982. The ecology and behaviour of Chital (Axis axis) in the Royal Chitwan National Park, Nepal. Thesis, University of Edinburg.
Mitchell-Jones, A.J., Amori, G., Bogdanowicz, W., Kryštufek, B., Reijnders, P.J.H., Spitzenberger, F., Stubbe, M., Thissen, J.B.M., Vohralik, V. and Zima, J. 1999. The Atlas of European Mammals. Academic Press, London, UK.
Moe, S. and Wegge, P. 1994. Spacing behavior and habitat use of Axis deer (Axis axis) in lowland Nepal.
Moe, S.R. and Wegge, P. 1997. The effects of cutting and burning on grass quality and axis deer (Axis axis) use of grassland in lowland Nepal. Journal of Tropical Ecology 13: 279–292.
Naess, K.J. and Andersen, H.J. 1993. Assessing census techniques for wild ungulates in Royal Bardia National Park, Nepal. Thesis, Agricultural University of Norway.
Pariwakam, M.P. 2006. Estimation of abundance and fawn survival in chital (Axis axis) populations using photographic capture-recapture sampling. Thesis, The Manipal Academy of Higher Education.
Patel, A.H. 1992. Are Chital stags more vulnerable to dhole predation than does? Journal of the Bombay Natural History Society 89: 153-155.
Raman, T.R.S. 1996. Factors influencing seasonal and monthly changes in the group size of Chital or axis deer in southern India. Journal of Biosciences 22: 203-218.
Raman, T.R.S. 2013. The Chital (Axis axis Erxleben). University Press.
Raman, T.R.S., Menon, R.K.G. and Sukumar, R. 1996. Ecology and management of Chital and blackbuck in Guindy National Park, Madras. Journal of the Bombay Natural History Society 93: 178-192.
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. Chital (Axis axis (Erxleben, 1777)). ENVIS Bulletin (Wildlife Institute of India, Dehra Dun) 7: 171–180.
Santiapillai, C. and Wijeyamohan, S. 2003. The impact of civil war on wildlife in Sri Lanka. Current Science 84: 1182–1183.
Schaller, G.B. 1967. The Deer and the Tiger. A Study of Wildlife in India. University of Chicago Press, Chicago, USA and London, UK.
Seidensticker, J. 1976. Ungulate populations in Chitawan valley, Nepal. Biological Conservation 10: 183-210.
Sharatchandra, H.C. and Gadgil, M. 1975. A year of Bandipur. Journal of the Bombay Natural History Society 72: 623-647.
Sharma, D. and Johnsingh, A.J.T. 1995. Management of wild ungulates and lion habitats in Gir lion sanctuary. Wildlife Institute of India, Dehradun, India.
Siddique, I. 2010. Predicting tiger (Panthera tigris) densities based on prey abundance in disturbed forests of Kwal. Msc Thesis. Tata Institute of Fundamental Research, India.
Stanford, J. K. 1951. Crab-eating Chital. Journal of the Bombay Natural History Society 50: 398-399.
|Citation:||Duckworth, J.W., Kumar, N.S., Anwarul Islam, M., Sagar Baral, H. & Timmins, R. 2015. Axis axis. The IUCN Red List of Threatened Species 2015: e.T41783A22158006.Downloaded on 19 January 2017.|
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