Taxonomy [top]

Kingdom Phylum Class Order Family
Animalia Chordata Mammalia Carnivora Felidae

Scientific Name: Panthera leo
Species Authority: (Linnaeus, 1758)
Infra-specific Taxa Assessed:
Regional Assessments:
Common Name(s):
English Lion, African Lion
French Lion d'Afrique
Spanish León
Felis leo Linnaeus, 1758
Taxonomic Notes: Taxonomy currently used by the IUCN SSC Cat Specialist Group:
Panthera leo persica—Asian subpopulations

Panthera leo leo—African subpopulations.

The latest published phylogeographical study of lions shows that the traditional split between Asian and African Lions as distinct subspecies is untenable (Barnett et al. 2014). Based on Barnett et al. (2014) the Cat Classification Task Force of the IUCN SSC Cat Specialist Group has provisionally proposed a different split into two subspecies, P. l. leo of Asia and West, Central and North Africa, and P l. melanochaita from South and East Africa. However, Barnett et al. (2014) is based only on mtDNA and could reflect female philopatry. In conjunction with the African Lion Working Group, Laura Bertola and colleagues are preparing a taxonomic paper, which will include reference to new molecular data from current studies, including complete mitochondrial genomes, microsatellites, and autosomal SNPs, which strongly support this taxonomic arrangement and recognize several management units within these revised subspecies. Given the poor conservation status of some regional Lion populations, it is important that this new taxonomic arrangement is immediately available for use by the IUCN Red List to support the next stages in developing a conservation strategy for the Lion based on coherent and sound science (Barnett et al. 2006a,b, 2014; Bertola et al. 2011, submitted; Dubach et al. 2005, 2013).

Assessment Information [top]

Red List Category & Criteria: Vulnerable A2abcd ver 3.1
Year Published: 2015
Date Assessed: 2014-06-17
Assessor(s): Bauer, H., Packer, C., Funston, P.F., Henschel, P. & Nowell, K.
Reviewer(s): Hunter, L., Hoffmann, M., Breitenmoser-Würsten, C. & Breitenmoser, U.
Contributor(s): Bauer, H., Becker, M., Begg, C., Bertola, L., Chapron, G., Croes, B., Dricuru, M., Funston, P.F., Groom, R., Henschel, P., Hunter, L., Loveridge, A., Macdonald, D., Packer, C., Petracca, L., Robinson, H., Tende, T., Tumenta, P.F., Venktraman, M., White, P.A. & Winterbach, C.

The Lion population is inferred to have undergone a reduction of approximately 43% over the past 21 years (approximately three Lion generations, 1993-2014).

We infer a decline of 43% based on time trend analysis of census data for 47 relatively well monitored Lion subpopulations. These subpopulations approximately totalled an estimated 7,500 Lions in 2014 and comprise a substantial portion of the total species population, so that we feel confident in applying observed trends to the species as a whole as well as on a regional basis.

The overall classification of the Lion as Vulnerable masks a dichotomy: we observe that sample Lion subpopulations increased by 12% in four southern African countries (Botswana, Namibia, South Africa and Zimbabwe) and in India, while an observed decline of 60% in sample subpopulations outside these countries is inferred for the remainder of its African range. In other words, in the majority of its range the Lion meets the A2 criterion for Endangered with the inferred rate of decline over 50% in three generations, but this trend is numerically mitigated by a small number of subpopulations in a restricted geographical range.

This dichotomy is reflected in listings of the species in different Red Lists: in South Africa, the Lion will be categorized as Least Concern on the national Red List in preparation (Child et al. In prep.), whereas in India it is Endangered (as subspecies P. l. persica on the global IUCN Red List: Breitenmoser et al. 2008) and in the region of West Africa meets the criteria for Critically Endangered (Henschel et al. 2014, 2015).  The range state list in Table 1 (attached Supporting Material) further illustrates the high threat levels across the species’ broad geographic range, as Lions have been recently extirpated in 12 African countries and we suspect possible recent extirpation in another four.

Among the causes of decline, the most important are indiscriminate killing in defence of human life and livestock, habitat loss, and prey base depletion. Prey base depletion is partly linked to habitat loss, but more importantly to poaching and bushmeat trade (Becker et al. 2013). An emerging threat is trade in bones and other body parts for traditional medicine, both within Africa and in Asia (IUCN 2006a, b; Riggio et al. 2013). Furthermore, although trophy hunting contributes positively to Lion conservation, improvements in management practices have been recommended (Lindsey et al. 2013b, Hunter et al. 2013, Edwards et al. 2014), as when poorly regulated, it also contributes to population declines (Packer et al. 2009, 2011; Croes et al. 2011, Rosenblatt et al. 2014). While attention is currently focused on Lion hunting reforms to ensure sustainability, the leading causes of population decline are more difficult to address and are likely to continue. The observed and inferred reductions are based on direct observation; appropriate indices of abundance; declines in area of occupancy, extent of occurrence and habitat quality; and actual and potential levels of exploitation.

Several subpopulations have been stable, among them the only remaining subpopulation in Asia (surviving in the Gir Forest area of Gujarat, India) and several subpopulations in southern Africa. Subpopulations appear to be stable where management is properly funded; fencing is one of several effective conservation management techniques (Packer et al. 2013). However, many Lion subpopulations occur in areas where management budgets are low, leading to local decline and even extinction, for example in West Africa (Henschel et al. 2014).  Little is known about Lion subpopulations in Angola, Central African Republic and South Sudan, but we fear drastic declines especially for the latter two.

In conclusion, we assess the Lion as Vulnerable based on criterion A, more specifically A2abcd. Lion range and abundance exceed the Vulnerable thresholds for criteria B, C and D, respectively, so these criteria do not contribute to the present assessment, whilst criterion E was not applied. Vulnerable A2abcd is the same listing as the previous assessment but with a different underlying method. Previous assessments were based on a suspected decline of the total estimated number of Lions, which necessarily included low quality data. In the present assessment we did not use total Lion estimates, because we had a better alternative. We now have enough good quality data for a representative sub-set of Lion subpopulations to calculate an observed decline, from which we infer a decline for the species as a whole.

For further information about this species, see 15951_Panthera_leo_2015_4.pdf.
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Previously published Red List assessments:
2015 Vulnerable (VU)
2012 Vulnerable (VU)
2008 Vulnerable (VU)
2004 Vulnerable (VU)
2002 Vulnerable (VU)
1996 Vulnerable (VU)

Geographic Range [top]

Range Description: Outside sub-Saharan Africa, the Lion formerly ranged from Northern Africa through Southwest Asia (where it disappeared from most countries within the last 150 years), west into Europe, where it apparently became extinct almost 2,000 years ago, and east into India (Nowell and Jackson 1996, Sunquist and Sunquist 2002). Today, the only remainder of this once widespread northern population is a single isolated subpopulation in the 1,400 km² Gir Forest National Park and Wildlife Sanctuary. Lions are extinct in North Africa, having perhaps survived in the High Atlas Mountains up to the 1940s (Nowell and Jackson 1996, West and Packer 2013).

Lions are found in most countries of sub-Saharan Africa. The last assessment of extant Lion range is provided by Riggio et al. (2013); they identified 67 Lion areas comprising 3.4 million km², which is 17% of historical range or about 25% of savanna Africa. We took those layers as a starting point, but made a few modifications to reflect the cautionary approach used by the IUCN Red List. Like with population numbers (see Population section), Riggio et al. (2013) copied old layers in the absence of new information. De facto, this means that large swathes of land are classified as Lion range based on the group exercises led by the Wildlife Conservation Society (WCS) and the IUCN SSC Cat Specialist Group; they found 86 Lion Conservation Units (LCUs) covering 4.6 million km² or 22% of historical range (IUCN 2006a,b; Bauer 2008). Henschel et al. (2010, 2014) found that many of these LCUs in West and Central Africa no longer contained Lions, and the range map was adapted accordingly for this assessment. Similarly, the survey and mapping unit at Panthera conducted further range updates based on new survey results and other properly documented information from other regions. Furthermore, some of the mapped LCUs are located in areas where armed conflict may have had an impact on lion persistence (e.g. Central African Republic and South Sudan). Until proof of the contrary, and based on the lack of recent data to confirm Lion presence, we therefore classified such areas as Possibly Extinct but maintained Protected Areas inside them as Lion range (including many large hunting concessions, such as in the Central African Republic). Some of the areas currently mapped as Possibly Extinct could contain relict Lion subpopulations, and should be prioritized for field surveys aimed at establishing Lion status.

Areas where we consider Lion populations Possibly Extinct total 1,811,087 km², over half (52%) of the range classified as extant by Riggio et al. (2013). We estimate extant Lion range, areas where we are reasonably confident that lions persist, based on recent records, at 1,654,375 km², or 8% of historical range. This range reduction reflects a combination of recent known and inferred decline, as well as improved knowledge.
Countries occurrence:
Angola (Angola); Benin; Botswana; Burkina Faso; Cameroon; Central African Republic; Chad; Congo, The Democratic Republic of the; Ethiopia; India; Kenya; Malawi; Mozambique; Namibia; Niger; Nigeria; Senegal; Somalia; South Africa; Sudan; Swaziland; Tanzania, United Republic of; Uganda; Zambia; Zimbabwe
Possibly extinct:
Côte d'Ivoire; Ghana; Guinea; Guinea-Bissau; Mali; Rwanda; Togo
Regionally extinct:
Afghanistan; Algeria; Burundi; Congo; Djibouti; Egypt; Eritrea; Gabon; Gambia; Iran, Islamic Republic of; Iraq; Israel; Jordan; Kuwait; Lebanon; Lesotho; Libya; Mauritania; Morocco; Pakistan; Saudi Arabia; Sierra Leone; Syrian Arab Republic; Tunisia; Turkey; Western Sahara
Upper elevation limit (metres): 4200
Range Map: Click here to open the map viewer and explore range.

Population [top]


Population Trend
This assessment is based on a time trend analysis of census data from relatively well-studied Lion subpopulations (Packer et al. 2013, plus additional unpublished data provided by contributors). Census estimates were obtained by scientific research methods including total count, individual identifications, total or sample inventory using calling stations, radio telemetry, photo databases, spoor counts and density estimates based on direct observations corrected for patrol effort. These methods are rated as producing the most reliable type of Lion population estimates by background papers for the 2006 IUCN regional Lion workshops (Table 5 in Bauer et al. 2005a, b). We did not include population estimates for sites which were based on extrapolation of Lion densities obtained by research in other areas, or informed guesstimates by researchers. The minimum number of census surveys per site over the assessment time period is two, but some sites have been more regularly monitored (Table 3 - Data Points column, in Supplementary Material). In some cases census methodology varied between years, and for some surveys accuracy may have been low, but the complete data set shows an obvious trend that is unlikely to be an artefact of methodological insufficiencies.

IUCN Red List Criteria define three generations as the relevant time span for trend assessment. Lion Generation Length (GL) is based on the formulation of Pacifici et al. (2013):

       GL = Rspan*z +AFR

Where AFR = Age of first reproduction = 3.5 yrs (Packer et al. 1998)

      Rspan = 15.5 (the age when 95% of females are no longer reproductive) - AFR = 12 yrs (Packer et al. 1998)

      Z = 0.29 (a constant “depending on survivorship and relative fecundity of young vs. old individuals in the population” (IUCN 2014), calculated as the slope of the linear regression between GL and Rspan for 221 mammalian species (Pacifici et al. 2013)

Thus GL = 12*0.29 +3.5 = 6.98 yrs

To fill gaps between censuses conducted in non-consecutive years, we interpolated population sizes, assuming a linear change between years. For surveys conducted for only a few years between 1993 and 2014, we extrapolated to the beginning and end points based on an exponential rate of change taken from the observed growth rate for each respective subpopulation. However, all extrapolations are capped by the estimated carrying capacity for each reserve so that subpopulations that experienced dramatic population change were not assumed to have been at implausibly high totals in either 1993 or 2014. Subpopulations were first categorized according to whether or not the reserves were surrounded by a fence; unfenced subpopulations were further categorized according to geographical location with the exception of Niassa Reserve (Mozambique), treated as an outlier as discussed below.

In graph form (Figures 1-4 in the Supplementary Material) we summarize the repeated censuses of 46 different African Lion subpopulations using all available repeat-survey data. Figure 5 (in the Supplementary Material) addresses the 47th Lion subpopulation in our analysis, the only Asian subpopulation.

Outside parts of southern Africa, Lions in 23 unfenced reserves in 11 countries are estimated to have dropped by 62% between 1993 and 2014 (see Figure 1 in the Supplementary Material).  Although these totals only included about 4,600 Lions in the year 1993, several surveyed areas are restricted to the best-protected portions of much larger ecosystems (e.g., the phototourism areas of Selous and Serengeti).

In contrast, the total number of Lions in six unfenced reserves in Botswana, Namibia and Zimbabwe only declined by about 11% (Figure 2, Supplementary Material). Note that the overall stability in southern Africa masks considerable heterogeneity: between 1993 and 2014 the monitored Lion subpopulation in a portion of the Okavango ecosystem is estimated to have declined by 46%, whereas the much smaller subpopulations in Gonarezhou and Kunene have increased dramatically.

The striking contrast between these three countries in southern Africa and the rest of the continent is probably related to the equally striking differences in human population densities (Packer et al. 2013) in Namibia (2.5/km²), Botswana (3.4) and Zimbabwe (26) vs. Benin (78), Burkina Faso (57), Cameroon (40), Cote d’Ivoire (64), Ghana (102), Kenya (67), Nigeria (189), Rwanda (420), Senegal (68), Tanzania (48), Uganda (137) and Zambia (45).

The unfenced Niassa subpopulation is estimated to have increased by over 250% since 1993 (Figure 3, Supplementary Material); despite severe bushmeat poaching the Lions are still recovering from excessive prey depletion during civil war. In addition, on a shorter time scale, Lions have benefited from extensive ivory poaching, which has provided them with sizeable quantities of elephant meat (Colleen Begg pers. comm. 2014). Human population density in Mozambique is 74/km² with sizeable numbers of people living inside Niassa Reserve, so unless management is further strengthened, this unfenced Lion subpopulation may soon experience declining food supplies and increased human-lion conflicts. These arguments strongly suggest that the ‘boom’ in the Niassa Lion subpopulation has stopped and is unlikely to be repeated in the future. We therefore consider Niassa to be a special case and treat it as an outlier in our analyses, we believe that this offers a better understanding of trends, but we note that this does not alter the assessment (with Niassa included, the assessment would still be Vulnerable A2abcd).

The 16 fenced African subpopulations (10 in South Africa, and all but one in southern Africa) have grown by 29% since 1993, most having already reached their presumed carrying capacities by 2013 (Figure 4, Supplementary Material). Note that although these numbers now total over 3,226 lions, our data come from the great majority of fenced reserves in Africa and that little further growth can be expected in these subpopulations.

Asia is home to a single contiguous subpopulation in the Indian state of Gujarat (Figure 5, Supplementary Material). While the population has stabilized inside the Gir Reserve, the so-called “satellite” population in the surrounding countryside has expanded by ~400% in the past 21 years.

The 47 sample Lion subpopulations totalled an estimated 9,615 lions in 1993 (excluding Niassa, which is treated as an outlier as described above); that number shrank by 22% to 7,455 lions in 2014 (Table 2, Supplementary Material).  However, as described above, there are significant regional differences evident in population trend, and we use these to inform our inferences about population trend for the species as a whole. Table 2 (Supplementary Material) groups the sample subpopulations by region in Africa, following the IUCN (2006a, b) regional Lion conservation strategies, but combining West and Central Africa due to a small sample size for Central Africa.  In Southern Africa, the sample population grew by 8%, while in sharp contrast, sample populations declined by 59% in Eastern Africa and 66% in West and Central Africa.

Table 3 (Supplementary Material) shows the estimated Lion population size in 1993 and 2014 for each of the 47 sample subpopulations with percentage change, and it can be seen that most countries had a declining trend for sample Lion subpopulations, with only four countries (India, Namibia, South Africa and Zimbabwe) seeing a growth trend. Table 4 (Supplementary Material) groups these countries with Botswana, which had a relatively low average rate of decline for its sample populations; two out of three sample subpopulations increased; the decline documented in the Okavango subpopulation was restricted to only part of the protected area; and overall 2012 estimates for the national population suggest that it his increased since 2003 (C. Winterbach unpubl. data). Mozambique is not included in this group as the increasing trend in its Niassa subpopulation is treated as an outlier in this analysis. The sample Lion population in five countries (Botswana, India, Namibia, South Africa, Zimbabwe) grew by an estimated 12%, whereas the Lion population in the remaining African range countries declined by an estimated 61% (Table 4, Supplementary Material).

We infer population trend for the total Lion species population based on these two rates of change, as follows. In 2002, two separate country compilations of population estimates for Lions in Africa estimated the number of Lions in Botswana, Namibia, South Africa and Zimbabwe to comprise between 1/4 to 1/3 of the total African Lion population, as shown in Table 5 (Supplementary Material). We suspect that this proportion was somewhat lower in 1993, given that the number of Lions is inferred to have increased in these countries while decreasing in the remainder, and use a figure of 1/4 or 25% for our species population trend calculation. If 25% of the Lion population increased by 12%, and 75% decreased by 60%, this results in an inferred trend of (0.75*-60%) + (0.25*12%) = -43% between 1993 and 2014 (Table 6, Supplementary Material).

This qualifies the Lion as Vulnerable, but it is of great concern that the vast majority of the population is inferred to have declined at a rate that meets the criteria for Endangered. Since our sample subpopulations were all monitored, we suspect an even greater average rate of decline for unmonitored unfenced subpopulations across much of Africa, since lack of monitoring could suggest lack of conservation effort.

For this assessment, we do not aim to provide a new estimate of total Lion numbers, we present no new data. A recent paper summarized and updated efforts to estimate the population size of the African Lion leading to the most recent estimate of 32,000 lions in 67 Lion areas (Riggio et al. 2013). The paper presents some recent data, but where no new data were available it included unaltered numbers from earlier sources, such as Bauer and Van der Merwe (2004) and Chardonnet (2002). As a consequence, Riggio et al. (2013) include numbers from 2002 and 2004 for areas where we believe the downward trend described above occurred. We therefore consider these sources to be insufficiently precautionary for our purpose and feel that an assessment on numbers is less robust than our assessment based on trends. Considering the difficulty in interpreting Lion numbers and the availability of an alternative (see above), we decided not to use total Lion numbers for the present assessment

However, we do attempt to correct for outdated sources in the Riggio et al. (2013) estimate by application of the regional trends we found (Table 3, Supplementary Material) to the 2002 population size estimates within the respective regions (Bauer and Van der Merwe 2004, Chardonnet 2002). These are two largely independent and reasonably comprehensive sets of estimated numbers that were coherent in time. Rather than presenting these numbers as in any way current, we look at how they might be expected to have changed. We calculated estimated present Lion numbers per region (Table 7, Supplementary Material) by applying the observed trend over the subsequent 12 years, except that numbers for West Africa were taken from a comprehensive recent survey (Henschel et al. 2014) because of their greater precision. As a small modification from Chardonnet (2002) we moved the estimate for Selous ecosystem to Eastern Africa to be consistent with the regional divisions used here. The two 2002 estimates were compared in detail (Bauer et al. 2005a,b), showing the ALWG study (Bauer and Van der Merwe 2004) was more conservative and stricter on data quality. Most notably, Bauer and Van Der Merwe (2004) lacked data for Ruaha and Tarangire which may hold close to 5,000 Lions. With all these considerations, we have greater confidence in an estimate of closer to 20,000 Lions in Africa than in a number over 30,000.

Approach to Uncertainty We do not have sufficient confidence in earlier or recent species population estimates to employ them to estimate trend and for this assessment have used groupings of scientific time series site estimates as a proxy.  Although these data are more numerous for Lions than for other big Panthera cats, there is still considerable uncertainty inherent in both the data (Bauer et al. 2015) and our treatment of it to estimate species population trend. Guidelines for Using the IUCN Red List Categories and Criteria (IUCN 2014) state that, "All attitudes (towards uncertainty) should be explicitly documented.  In situations where the spread of plausible values (after excluding extreme or unlikely values) qualifies a taxon for two or more categories of threat, the precautionary approach would recommend that the taxon be listed under the higher (more threatened) category." 
As noted in Table 2 (see Supplementary Material), if the species trend is inferred directly from the total sample population trend, the result, a decline of 22%, would qualify the species as Near Threatened rather than Vulnerable. However, considering the demonstrated significant regional differences such an approach would be inappropriate. 
We treated Mozambique's Niassa subpopulation trend as an outlier and removed it from our trend analysis for reasons described above, but we also documented the effect of the exclusion. Some contributors proposed a second outlier: Tanzania’s Katavi subpopulation. Katavi has been consistently and repeatedly monitored, but the survey methodology was imprecise (vehicle transects: Caro 2011), this yielded a significant decline rate approaching 100% in a large population of over 1,100 estimated lions in the study site portion of the park in 1993 (Table 3). If Katavi would have been treated as an outlier and excluded from the analysis, inferred rate of decline would be 33%, and the rate of decline for Lions in East Africa would be 37%. Lions are still extant in Katavi (as shown in our map), although well below carrying capacity (Kiffner et al. 2008). Rather than using an arbitrary low value, we used the value documented by surveys (zero); Lions are extant but at a density so low as not to be detected. While the methodology is imprecise, it has proved reliable for carnivore monitoring in the Serengeti (Durant et al. 2011). Furthermore, the extent of decline may have been measured with lack of precision, but population decline remains uncontested. Since it is one of only two long-term monitoring programmes in Tanzania (Caro 2011) we decided that it was important to include these data and decided that there was insufficient ground to treat it as an outlier.
Another uncertainty that needs to be documented is our treatment of small fenced reserves in southern Africa. Most of the population increases have occurred in these areas where intensive management practices include translocations, stocking, contraception and euthanasia. Such management is atypical, and as pointed out by Hayward et al. (2015) the Red List Guidelines are ambiguous as to the inclusion or exclusion of fenced areas. Their exclusion from the analysis would raise the inferred Lion decline rate to 49%. Following through on our supposition that unmonitored Lion populations have undergone an even higher rate than our monitored sample, this could potentially have been interpreted as a suspected rate of decline over 50%, qualifying the Lion as Endangered. However, we did not exclude fenced populations from our assessment. Hayward et al. (2015) state that such decisions should consider the ‘type, scale, frequency and effects of the suite of management interventions’ and could be taxon specific. We consider that management of Lions in the concerned areas aims to mimic natural processes, aims to retain adaptive potential and follows a meta-population management approach. We further consider that fences have been documented as effective tools in Lion conservation (Packer et al. 2013). We find this sufficient justification for inclusion of these reserves.
National estimated rates of population change are most meaningful in practice, and these are given in Table 3 in the Supplementary Material.  We did not use national rates to gauge species decline, as the sample sizes are generally small and estimates of national Lion populations imprecise.
For further information about this species, see 15951_Panthera_leo_2015_4.pdf.
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Current Population Trend: Decreasing
Additional data:
Number of mature individuals: 23000-39000 Continuing decline of mature individuals: Yes
Population severely fragmented: No

Habitat and Ecology [top]

Habitat and Ecology: The Lion has a broad habitat tolerance, absent only from tropical rainforest and the interior of the Sahara desert (Nowell and Jackson 1996). There are records of Lion to elevations of more than 4,000 m in the Bale Mountains and on Kilimanjaro (West and Packer 2013). Although Lions drink regularly when water is available, they are capable of obtaining their moisture requirements from prey and even plants (such as the tsama melon in the Kalahari desert), and thus can survive in very arid environments. Medium- to large-sized ungulates (including antelopes, zebra and wildebeest) are the bulk of their prey, but Lions will take almost any animal, from rodents to a rhino. They also scavenge, displacing other predators (such as the Spotted Hyaena) from their kills.

Lions are the most social of the cats, with related females remaining together in prides, and related and unrelated males forming coalitions competing for tenure over prides. Average pride size (including males and females) is four to six adults; prides generally break into smaller groups when hunting. Lions tend to live at higher densities than most other felids, but with a wide variation from 1.5 adults per 100 km² in southern African semi-desert to 55/100 km² in parts of the Serengeti (Sunquist and Sunquist 2002). Pride ranges can vary widely even in the same region: e.g., from 266-4,532 km² in the Kgalagadi Transfrontier Park of South Africa (Funston 2001).

In India, the habitat of the Asiatic Lion is dry deciduous forest. The Gir National Park and Wildlife Sanctuary is surrounded by cultivated areas and inhabited by the pastoralist Maldharis and their livestock (Meena et al. 2014). Domestic cattle have historically been a major part of the Asiatic Lion's diet, although the most common prey is the Chital Deer. Mean pride size, measured by the number of adult females, tends to be smaller than for African Lions: most Gir prides contain an average of two adult females (Nowell and Jackson 1996).
Systems: Terrestrial
Generation Length (years): 6.98

Use and Trade [top]

Use and Trade: For information on Use and Trade see under Threats.

Threats [top]

Major Threat(s):

The main threats to Lions are indiscriminate killing (primarily as a result of retaliatory or pre-emptive killing to protect human life and livestock) and prey base depletion. Habitat loss and conversion has led to a number of subpopulations becoming small and isolated (Bauer et al. 2008). Furthermore, trophy hunting has a net positive impact in a some areas, but may have at times contributed to population declines in Botswana, Namibia, Tanzania, Zimbabwe (Packer et al. 2009, 2011, 2013), Cameroon (Croes et al. 2011) and Zambia (Rosenblatt et al. 2014).

The economic impact of stock raiding can be significant: Patterson et al. (2004) estimated that each Lion costs ranchers in Kenya living alongside Tsavo East National Park US$290 per year in livestock losses. Likewise, annual losses of cattle to Lions in areas adjacent to Waza National Park in Cameroon comprised only about 3.1% of all livestock losses, but were estimated to represent more than 22% of financial losses amounting to about US$370 per owner (Bauer 2003). Consequently, Lions are persecuted intensely in livestock areas across Africa; their scavenging behaviour makes them particularly vulnerable to poisoned carcasses put out to eliminate predators. Little actual information exists on the number of Lions killed as problem animals by local people, even though this is considered the primary threat to their survival outside protected areas. Implementation of appropriate livestock management measures, coupled with problem animal control measures and mechanisms for compensating livestock losses, are some of the primary responses to resolving human-Lion conflict (Frank et al. 2006, Bauer et al. 2010, Hazzah et al. 2014).

Prey depletion
Lion population density across the species’ range is known to track the biomass of principle Lion prey species; large wild herbivores (Van Orsdol et al. 1985, Hayward et al. 2007). The latter are increasingly under threat from an unsustainable and increasingly commercialized bushmeat trade, leading to collapses in prey populations across large parts of savanna Africa (Lindsey et al. 2013a). Regional Lion population trends reported in this assessment, are closely mirrored by time series data on main Lion prey species from 78 herbivore populations monitored between 1970 and 2005 in West, Eastern and Southern Africa; while herbivore population sizes increased by 24% in Southern Africa, they declined by 52% in Eastern Africa and by 85% in West Africa (Craigie et al. 2010).

Use of Lion bones and body parts and derivatives for traditional medicine
Illegal trade in Lion body parts for medicinal purposes is considered a threat to African Lion subpopulations (according to the regional Lion conservation strategies, which call on countries to prohibit [IUCN 2006a] and control [IUCN 2006b] trade in Lion bone and other parts and products) as well as to the small subpopulation in India's Gir Forest (M. Ventraman pers. comm. 2014). In West and Central Africa, Sogbohossou (2006) found many reported uses for Lion skins and bone in Benin (with fat and bones being most commonly utilized: N'Diaye 2014), and a survey carried out around Nigeria's Yankari National Park found more than 22 Lion parts considered to be of medicinal value, with most of the over 200 interviewees saying they had used Lion parts in the past, and half within the past three years (Born Free Foundation 2008). The widespread prevalence of fakes in the traditional medicinal market is indicative of a continued demand. While fakes may replace items in the market that otherwise would be illegally sourced from the wild, they could perpetuate demand and poaching when consumers aspire to the genuine wild item rather than making a conscious choice of an (often cheaper) alternative (Nowell 2014).

There appears to be increasing interest in the use of African Lion bone in Asia. There is no history of Lion bone being used in traditional medicine there, but China has permitted the use of bones from captive Lions to make medicinal wines traditionally containing Tiger bone. South Africa has reported the export of large quantities of Lion bone sourced from captive animals to China, the Lao People's Democratic Republic and Viet Nam. Legal international trade in bone reported as from captive-bred Lions could serve as a cover for illegally wild-sourced Lion (and other big cat) parts (Nowell and Pevushina 2014). There is also concern that wild Lion parts from eastern and Southern Africa could be drawn into the large illegal wildlife trade to Asia centred around elephant ivory.

Trophy hunting
Trophy hunting is carried out in a number of sub-Saharan African countries and is considered an important management tool for conserving wild land providing financial resource for Lion conservation for both governments and local communities. However, there is concern that management regimes have not always been sufficient to deter unsustainable offtakes (Packer et al. 2006). A sustainable offtake level of one male lion per 2,000 km² has been recommended (Packer et al. 2011), but offtake has been higher in many areas, which suggests that it is potentially a threat (Lindsey et al. 2013b). Trophy hunting can thus be a tool for conservation but also a threat, depending on how it is regulated and managed (Whitman et al. 2004, Loveridge et al. 2007, Packer et al. 2011). Hunter et al. (2013) cautioned that regulatory measures which reduce the profitability of Lion trophy hunting could have widespread negative impacts for wildlife-based land use, anti-poaching and tolerance of Lion outside protected areas.

Disease has also been a threat to Lion subpopulations (Munson et al. 2008, Trinkel et al. 2011). In parts of southeastern Tanzania there have been alarmingly high incidences of people killed by Lions, with up to 400 human Lion-related fatalities recorded from 1997-2007 (Ikanda and Packer 2007).

Conservation Actions [top]

Conservation Actions: Since 1975 Panthera leo has been included in CITES Appendix II, and  the Endangered Asiatic Lion subspecies P. leo persica in CITES Appendix I. CITES listing of the Lion is currently undergoing a Periodic Review process to evaluate whether this accurately reflects the present situation, with a final recommendation of the Animals Committee expected at its 28th meeting in 2015. The Animals Committee also noted recent information regarding possible changes in the nomenclature of Lions and requests its nomenclature expert to  review this information (CITES AC27 WG8).

In Africa, Lions are present in a number of large and well-managed protected areas, and remain one of the most popular animals on the must-see lists of tourists and visitors to Africa. Most range states in East and Southern Africa have an infrastructure which supports wildlife tourism, and in this way Lions generate significant cash revenue for park management and local communities and provide a strong incentive for wildland conservation.

Regional conservation strategies have been developed for Lions in West and Central Africa (IUCN 2006a) and Eastern and Southern Africa (IUCN 2006b). By setting out common priorities to guide action on both national, community and landscape levels, the regional conservation strategies have the potential for broad and significant improvement of Lion status and management (Nowell et al. 2006). These regional strategies have been used in many countries to develop Lion Conservation Action Plans. While all these documents show awareness of the threats and recognition of solutions, the continued decline in Lion range and numbers show that political priority and funding are not sufficient (Packer et al. 2013).

Classifications [top]

1. Forest -> 1.5. Forest - Subtropical/Tropical Dry
suitability: Suitable season: resident major importance:Yes
2. Savanna -> 2.1. Savanna - Dry
suitability: Suitable season: resident major importance:Yes
3. Shrubland -> 3.5. Shrubland - Subtropical/Tropical Dry
suitability: Suitable season: resident major importance:Yes
3. Shrubland -> 3.7. Shrubland - Subtropical/Tropical High Altitude
suitability: Marginal season: resident 
4. Grassland -> 4.5. Grassland - Subtropical/Tropical Dry
suitability: Suitable season: resident major importance:Yes
4. Grassland -> 4.7. Grassland - Subtropical/Tropical High Altitude
suitability: Marginal season: resident 
8. Desert -> 8.1. Desert - Hot
suitability: Unknown  
1. Land/water protection -> 1.1. Site/area protection
1. Land/water protection -> 1.2. Resource & habitat protection
2. Land/water management -> 2.1. Site/area management
2. Land/water management -> 2.3. Habitat & natural process restoration
3. Species management -> 3.1. Species management -> 3.1.1. Harvest management
3. Species management -> 3.1. Species management -> 3.1.2. Trade management
3. Species management -> 3.1. Species management -> 3.1.3. Limiting population growth
3. Species management -> 3.2. Species recovery
3. Species management -> 3.3. Species re-introduction -> 3.3.1. Reintroduction
3. Species management -> 3.4. Ex-situ conservation -> 3.4.1. Captive breeding/artificial propagation
4. Education & awareness -> 4.2. Training
4. Education & awareness -> 4.3. Awareness & communications
5. Law & policy -> 5.1. Legislation -> 5.1.2. National level
5. Law & policy -> 5.1. Legislation -> 5.1.3. Sub-national level
5. Law & policy -> 5.4. Compliance and enforcement -> 5.4.1. International level
5. Law & policy -> 5.4. Compliance and enforcement -> 5.4.2. National level
5. Law & policy -> 5.4. Compliance and enforcement -> 5.4.3. Sub-national level

In-Place Research, Monitoring and Planning
In-Place Land/Water Protection and Management
  Occur in at least one PA:Yes
In-Place Species Management
  Harvest management plan:Yes
  Successfully reintroduced or introduced beningly:Yes
  Subject to ex-situ conservation:Yes
In-Place Education
  Subject to recent education and awareness programmes:Yes
  Included in international legislation:Yes
  Subject to any international management/trade controls:Yes
1. Residential & commercial development -> 1.1. Housing & urban areas
♦ timing: Ongoing ♦ scope: Whole (>90%) ♦ severity: Rapid Declines ⇒ Impact score: High Impact: 8 
→ Stresses
  • 1. Ecosystem stresses -> 1.1. Ecosystem conversion
  • 1. Ecosystem stresses -> 1.2. Ecosystem degradation

2. Agriculture & aquaculture -> 2.1. Annual & perennial non-timber crops -> 2.1.1. Shifting agriculture
♦ timing: Ongoing    
→ Stresses
  • 1. Ecosystem stresses -> 1.1. Ecosystem conversion
  • 1. Ecosystem stresses -> 1.2. Ecosystem degradation

2. Agriculture & aquaculture -> 2.1. Annual & perennial non-timber crops -> 2.1.2. Small-holder farming
♦ timing: Ongoing    
→ Stresses
  • 1. Ecosystem stresses -> 1.1. Ecosystem conversion
  • 1. Ecosystem stresses -> 1.2. Ecosystem degradation

2. Agriculture & aquaculture -> 2.3. Livestock farming & ranching -> 2.3.1. Nomadic grazing
♦ timing: Ongoing    
→ Stresses
  • 1. Ecosystem stresses -> 1.1. Ecosystem conversion
  • 1. Ecosystem stresses -> 1.2. Ecosystem degradation

2. Agriculture & aquaculture -> 2.3. Livestock farming & ranching -> 2.3.2. Small-holder grazing, ranching or farming
♦ timing: Ongoing    
→ Stresses
  • 1. Ecosystem stresses -> 1.1. Ecosystem conversion
  • 1. Ecosystem stresses -> 1.2. Ecosystem degradation

5. Biological resource use -> 5.1. Hunting & trapping terrestrial animals -> 5.1.1. Intentional use (species is the target)
♦ timing: Ongoing    
→ Stresses
  • 2. Species Stresses -> 2.1. Species mortality

5. Biological resource use -> 5.1. Hunting & trapping terrestrial animals -> 5.1.2. Unintentional effects (species is not the target)
♦ timing: Ongoing    
→ Stresses
  • 2. Species Stresses -> 2.1. Species mortality

5. Biological resource use -> 5.1. Hunting & trapping terrestrial animals -> 5.1.3. Persecution/control
♦ timing: Ongoing    
→ Stresses
  • 2. Species Stresses -> 2.1. Species mortality

5. Biological resource use -> 5.3. Logging & wood harvesting -> 5.3.5. Motivation Unknown/Unrecorded
♦ timing: Ongoing    
→ Stresses
  • 1. Ecosystem stresses -> 1.2. Ecosystem degradation

6. Human intrusions & disturbance -> 6.2. War, civil unrest & military exercises
♦ timing: Ongoing    
→ Stresses
  • 2. Species Stresses -> 2.2. Species disturbance

8. Invasive & other problematic species & genes -> 8.2. Problematic native species
♦ timing: Ongoing    
→ Stresses
  • 1. Ecosystem stresses -> 1.2. Ecosystem degradation

9. Pollution -> 9.3. Agricultural & forestry effluents -> 9.3.4. Type Unknown/Unrecorded
♦ timing: Ongoing    
→ Stresses
  • 1. Ecosystem stresses -> 1.2. Ecosystem degradation

1. Research -> 1.2. Population size, distribution & trends
1. Research -> 1.3. Life history & ecology
1. Research -> 1.5. Threats
1. Research -> 1.6. Actions
2. Conservation Planning -> 2.1. Species Action/Recovery Plan
2. Conservation Planning -> 2.2. Area-based Management Plan
3. Monitoring -> 3.1. Population trends

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Citation: Bauer, H., Packer, C., Funston, P.F., Henschel, P. & Nowell, K. 2015. Panthera leo. The IUCN Red List of Threatened Species 2015: e.T15951A79929984. . Downloaded on 27 May 2016.
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