The size of savannah Africa: a lion’s (Panthera leo) view
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We define African savannahs as being those areas that receive between 300 and 1,500 mm of rain annually. This broad definition encompasses a variety of habitats. Thus defined, savannahs comprise 13.5 million km2 and encompass most of the present range of the African lion (Panthera leo). Dense human populations and extensive conversion of land to human use preclude use by lions. Using high-resolution satellite imagery and human population density data we define lion areas, places that likely have resident lion populations. In 1960, 11.9 million km2 of these savannahs had fewer than 25 people per km2. The comparable area shrank to 9.7 million km2 by 2000. Areas of savannah Africa with few people have shrunk considerably in the last 50 years and human population projections suggest they will likely shrink significantly in the next 40. The current extent of free-ranging lion populations is 3.4 million km2 or about 25 % of savannah area. Habitats across this area are fragmented; all available data indicate that between 32,000 and 35,000 free-ranging lions live in 67 lion areas. Although these numbers are similar to previous estimates, they are geographically more comprehensive. There is abundant evidence of widespread declines and local extinctions. Under the criteria we outline, ten lion areas qualify as lion strongholds: four in East Africa and six in Southern Africa. Approximately 24,000 lions are in strongholds, with an additional 4,000 in potential ones. However, over 6,000 lions are in populations of doubtful long-term viability. Lion populations in West and Central Africa are acutely threatened with many recent, local extinctions even in nominally protected areas.
KeywordsLion Panthera leo Africa Distribution Savannah Google Earth Threatened species Endangered species Red List Functional extinction Top predator
We define our domain of interest as being those areas of Africa that receive between 300 and 1,500 mm of rain annually. This broad and inevitably arbitrary definition encompasses a wide variety of habitats including grasslands, wetlands, dry woodlands and mosaics of all of these, but most of this area is deemed to be savannah. For our purposes we call all these areas “savannahs” for simplicity, without wishing to comment on the complexities of what determines the limits of this biome (Sankaran et al. 2005; Ratnam et al. 2011; Staver et al. 2011). Thus defined, we show below that savannahs comprise 13.5 million km2. (This compares to Cahoon et al.’s (1992) estimate of ~10 million km2.) As we define it, this domain is most of Africa south of the Sahara, excluding the tropical moist forests of West Africa, the Congo, patches of montane forests throughout East Africa, and drier areas in the Southwest, such as the Namib.
As such, the IUCN Red List entry (henceforth Bauer et al. 2008) shows that savannah Africa encompasses most of the present range of the African lion (Panthera leo leo). Lions once lived across Eurasia, but now only a remnant population of a different subspecies (Panthera leo persica) survives in India. Recent research has demonstrated that the lion in West and Central Africa is genetically different from the lion in East and Southern Africa and more closely resembles Asiatic populations (Bertola et al. 2011). Nonetheless, we consider just African populations and do so without distinction.
In Africa, lion populations once lived outside this strict savannah zone. For example, until recently a lion population was present in forest-savannah mosaics in Gabon and the Republic of Congo (“Congo-Brazzaville”) (Henschel 2009), and there are other remnant populations in forests in Ethiopia (see supplemental materials) and other non-savannah environments. However, the association between lions and savannahs is generally now quite a close one. How much of the African savannah still supports lions—and is likely to do so in the future—are the more difficult questions we address in this paper.
We evaluate the state of the African savannah with two objectives, namely estimating the areas of savannah still suitable for lion populations and estimating the lion populations themselves within these areas. If areas retain lions, the continent’s top predator, they are likely to be reasonably intact ecosystems. By considering the size of savannah Africa from the lion’s perspective, we can assess how much of it remains in large, relatively intact areas, not yet heavily modified by human influence. Clearly, smaller areas will still support less complete sets of species.
Our first objective of estimating this area is important for three reasons. (a) We provide an assessment of an ecosystem rich in biodiversity—much as one might assess the current extent of tropical moist forests, for example. (b) Discussions of how much land is set aside for protection of specified ecosystems are particularly important as nations evaluate the 2010 targets under the Convention on Biological Diversity (Jenkins and Joppa 2009). As we define them, African savannahs extend beyond protected areas into areas with low human impact. The question is: how much do savannahs extend beyond the borders of protected areas? The answer certainly includes areas with other land uses, including hunting zones that comprise a significant share of the lion’s range in Africa. (c) Some protected areas may be too small or their managers unable to stem the threats to them to retain lions or other wide-ranging species (Henschel et al. 2010). At continental scales, whether protected areas actually protect biodiversity is generally assessed by measures such as the retention of forest cover (Joppa et al. 2008) or the management of anthropogenic fires (Adeney et al. 2009). Much of the savannah zone is a fire climax (Bond and van Wilgen 1996). However, such methods do not permit direct evaluations of the protected areas’ effectiveness in conserving biodiversity. For African savannahs, the presence of large mammals, such as lions, permits such direct assessments in ways unavailable for ecosystems with less conspicuous fauna sensitive to human impacts.
Our second objective of compiling estimates of all free-ranging lion populations throughout Africa builds from three previous continent-wide population assessments: Chardonnet (2002), Bauer and Van Der Merwe (2004), and the WCS and IUCN-organised range-wide priority setting exercises held in 2005 and 2006 (IUCN 2006a, b). Those reports rightly generated considerable efforts to improve population estimates across Africa. However, a recent meeting of the African Lion Working Group in Etosha, Namibia, suggested that these regional lion conservation strategies had a poor follow-up and needed an urgent update (see Final Communiqué from the 2nd African Lion Working Group meeting http://www.largecarnivoresafrica.com/wp-content/uploads/ALWG-Etosha-public-statement.pdf). This need is particularly acute: there is evidence of rapidly declining populations of many large mammals in West and Central Africa and in East Africa (Craigie et al. 2010; Henschel et al. 2010), as well as some parts of Southern Africa. These trends may quickly invalidate any estimates and may make some of the assumptions of the regional lion conservation strategies redundant. Presenting what is known, and when, is surely the best way to show such declines.
To these prior continent-wide assessments, we add data from over 40 mainly country-specific reports and our own personal experiences. These expand on these previous compilations and provide the current best estimates of numbers, or other clarifications, of lion numbers and distribution.
Our two objectives address the need for an updated geographical framework onto which we can map the numbers of lions and the areas they occupy. Countrywide estimates of lion numbers fail to capture the size and degree of isolation and consequent population viability. Nor do they show the trans-boundary distributions of many lion populations. Here we present all known lion population data in a single map.
This map contains our best estimates of lion areas—places that, as best we can tell, likely have resident lion populations. Human impacts delineate many of these areas. How human impacts have changed—and will change—give clues needed to understand past lion population trends and allows us to speculate about their future.
The regional lion conservation strategies of 2006 defined “lion conservation units” (LCUs). These are expert-defined regions intended to classify areas suitable for lions, an idea already in use by the conservation community following Sanderson et al.’s (2002) jaguar conservation units. LCUs are areas of known, occasional or possible lion range that one could consider an ecological unit of importance for lion conservation (IUCN 2006a, b). These LCUs arose from regional workshops held in 2005 and 2006 and maps included in the regional strategy reports delineate them. However, recent lion field surveys in West and Central Africa revealed that much of the information on lion distribution used for defining these LCUs is either out of date or was not very accurate in the first place (Henschel et al. 2010). We still decided to use these LCUs, however, as a starting point and as an important international reference for lion conservation.
We created lion areas by modifying LCUs with updated information and observed land conversion or predictions of high human population density. We find broad agreement between our lion areas and LCUs. There are important differences, however. Our lion areas consider all places containing resident lion populations, not just those regions deemed important for lion conservation. In addition, our explicit habitat modelling allows for updated future assessments. It also permits us to understand where and how rapidly lion populations have become isolated, a subject we will address elsewhere.
A final component in assessing the status of lions determines which populations are “lion strongholds,” by meeting the necessary requirements for long-term viability. The concept of a lion stronghold is not new and recent calls for lion conservation action have included the need to “…identify regional strongholds for the species that have the highest probability of persistence in the long-term” (Treves et al. 2009). Defining “strongholds” is not easy, as our “Discussion” section elaborates.
Lion population assessment
We compiled all of the most current available estimates of lion populations—see supplementary materials. Three continent-wide assessments provide the core of these data (Chardonnet 2002; Bauer and Van Der Merwe 2004; IUCN 2006a, b). Supplementing these continent-wide reports, we added lion conservation strategies and action plans that highlight the status of lions in specific countries. We searched the primary articles these reports cite and newly published lion population surveys to obtain the most up-to-date data on lion numbers and distribution. Most of these reports include expert opinions on lion numbers or structured surveys, not formal counts. We also include individual personal comments from the authors and colleagues on the numbers in supplementary materials. Given how difficult it is to count lions this inevitably begs the question of how good are these expert opinions, an issue we address in “Discussion” section.
Lion area mapping
We mapped the protected areas within savannah Africa using the 2010 World Database on Protected Areas (IUCN and WDPA 2010). This database includes the six different IUCN classifications of protected areas. These range from strict protection to multiple use and extractive reserves that inter alia, permit hunting. While the delineations of national parks are usually clear, the boundaries of areas with less protection, especially hunting areas are not. In some countries, IUCN categories encompass some of these areas; in others, they do not. Hunting areas can be very extensive: for instance, Tanzania gazettes more land for hunting than for national parks. Moreover, some areas have no protection at all, but still house lions. In short, the difficult issue is to what extent lions move beyond and between the well-known protected areas.
Incorporate “permanent” lion distributions that more recent reports identify as such and, when possible, remove areas listed as having “possible, temporary, or occasional” lion populations.
Exclude areas with human population density greater than 25 people per km2. (We justify this threshold in the Results.)
Exclude areas with user-identified land conversion above a defined-threshold, which again we define.
Exclude areas where recent lion population surveys no longer detected resident lions.
Lion conservation units (LCUs). Lion conservation units are expert opinions typically produced at meetings by freehand drawing of boundaries on maps. They can combine considerable experience and profound ignorance, of course, and beg objectively defined criteria. We used existing delineations (step 1). We occasionally made small modifications to them by adding small, adjacent areas of low human impact. Since the creation of LCUs in 2005/2006, a number of detailed countrywide reports have produced updated lion range maps. We include these new data on lion distribution for the refined lion areas.
Lion strongholds. For a lion area to qualify as a stronghold, it must satisfy three qualifications: (1) contain at least 500 individuals, (2) be within protected areas or designated hunting areas, and (3) the numbers of lions must be stable or increasing as assessed by the IUCN Cat Specialist Group (IUCN 2006a, b). If a lion area has at least 250 individuals but does not satisfy either requirement (2) or (3), it is a potential stronghold. We explore these criteria in the “Discussion” section.
Independent measures of land use conversion. To identify areas of high human impact, we used the European Space Agency’s GlobCover Project (henceforth GlobCover) (ESA and UCLouvain 2010), which has regularly updated land cover maps. Of the 22 land cover classes in GlobCover, five relate to human land use conversion (post-flooding or irrigated croplands, rain-fed croplands, mosaic cropland, mosaic vegetation, and artificial surfaces and associated areas). These five classes were lumped into a single land conversion layer.
User-identified land conversion. We used Google Earth’s high-resolution global imagery to evaluate potential lion areas and possible connections between protected areas. For example, the area between Comoé National Park, in Ivory Coast (at 9.25°N and 3.75°W), and Mole National Park, in Ghana (at 9.5°N and 1.75°W), represents a potentially important corridor for lion movement. GlobCover classifies the intervening areas as a single, homogenous class—“intact woodlands”. To see that these areas are not—they are heterogeneous—is an issue of scale. We follow the definition of “scale” as the distance over which a measure is unchanged. This begs the question of how close must one inspect an area to see that it is not unchanged—i.e. continuous—woodland, as suggested by the GlobCover classification.
Google Earth provides an estimate of the altitude of the viewer examining its imagery. At high altitude, the area does look continuous, but at approximately 40 km elevation, the presence of extensive small fields cut into the dry woodland becomes apparent in this region. At 10 km, these fields, typically a few hundred metres across are readily apparent, so we surveyed extensive areas at this altitude. We hand-drew polygons around areas of land conversion, (henceforth user-identified land conversion), though typically not of the individual fields themselves.
We identified land conversion most easily if it was cropland, forest plantations, or urban areas. More difficult was highlighting intensely grazed areas (more easily identified if they were fenced-in), croplands in drier regions, and differentiating deforestation from wet savannahs. We did not identify isolated land conversion smaller than approximately 0.5 km2. In some large areas blanketed by cropland or urbanisation, we did not differentiate embedded natural areas smaller than a few square kilometres. Some areas had extensive but lower density conversion. In these situations if the 0.01 × 0.01° grid (~1 km2 at the equator, and drawn by Google Earth) was over 30 % converted, we deemed it “converted”. Despite these qualifications, we attempted to closely follow the boundaries of conversion (e.g. within ~100 m) where feasible. It was impractical to do this for the entire continent, so we limited this assessment of land conversion to all of West Africa, plus Cameroon and select locations in Central, East and Southern Africa.
To apply the user-identified land conversion layer to the creation of lion areas, we converted the Google Earth products (Keyhole Markup Language, or KML files) to a raster dataset in ArcGIS. Then, we ran the Boundary Clean tool to remove cells of data too small to have an impact on lion distribution. We converted this raster to a polygon to smooth the lion area borders. Both the original and cleaned versions of these layers are available as KML files from the authors on request.
Human population density. We used the Gridded Population of the World version 3 dataset for the year 2000 from Columbia University’s Center for International Earth Science Information Network (CIESIN) (CIESIN and CIAT 2005). These data are models of human population data, not actual counts, and are the most-up-to-date data available to us. We compared where this product predicted human populations greater than 5, 10, 25, and 50 people per km2 with our user-identified land conversion. The four areas that we chose were in West, Central, East, and Southern Africa. Compared to user-identified conversions there can be errors of omission (where the population data predict human impact, but conversions are not obvious), errors of commission (where there is conversion, but the population data suggest too few people), and areas where both measures agree. We evaluated which human population density gave the best agreement.
We estimate that there are 13.5 million km2 of sub-Saharan Africa within the rainfall limits of 300 and 1,500 mm. The more difficult question is how much of this has human action made unsuitable for lions and other wildlife. We expected to find the answer in existing land cover products. As we shall now explain, these products are not sufficient for our needs.
Calibration of land use conversion with human population density
Since GlobCover (ESA and UCLouvain 2010) is unsuitable for our purposes, we explored whether models of human population provided a better correlation with land conversion. The aim was to find an estimate of human population density that best matched extensive land conversion. We used four focus areas distributed throughout the African lion’s range to compare human population at various densities with a high-resolution satellite-based land conversion layer (Supplemental materials, Fig. S1).
We calculate the total, current potential range of free-ranging lion populations to be, at best, 3,390,821 km2 or about 25 % of the original savannah area. Removing the poorest quality data from Chad, Sudan, the western half of South Sudan, Somalia, and Angola provided an estimate of 2,466,452 km2 (18 % of the original savannah area). This compares with the IUCN’s total area of LCUs, 3,163,260 km2 (calculated in our analysis), and the estimate of 2,950,367 km2 from Chardonnet (2002). Bauer (2006) states that the range-wide priority setting exercise (IUCN 2006a, b) calculated a total current lion range of 4,612,231 km2, but this number includes areas described as containing both occasional and probable lion populations.
Lion population assessment
Lion numbers by region and by source
These numbers fall between the assessments of Bauer and Van Der Merwe (2004), who estimated ~22,000 lions, and Chardonnet (2002) who proposed ~38,000 individuals. The basic difference between Bauer and Chardonnet is that the latter aimed for a realistic estimate, filling gaps with extrapolations and best guesses, whereas Bauer and Van Der Merwe (2004) did not attempt to give an estimate but an inventory of known research data, which we can interpret as a minimum estimate. For example, they cautioned that the Ruaha and Tarangire ecosystems in Tanzania (areas they did not assess) could contain substantial numbers of lions; adding Chardonnet’s (2002) figures here would bring their estimate to 28,000—a number closer to the present study.
Lion numbers by region and population size: numbers (numbers of populations)
The IUCN (2006a, b) reports, based on regional workshops and inventories during 2005 and 2006, estimated a total lion population of approximately 33,000 individuals. These estimates are already out of date and included populations that we now know no longer exist (Henschel et al. 2010) (Table S3). On the other hand, some lion areas were overlooked and not included in LCUs (Table S4). In the supplementary materials, Table S5 highlights examples of lion populations showing differences between the major population assessments and compares them to the most recent data used for this analysis.
These estimates all used different methodologies. This precludes direct comparison and conclusions on temporal trends. While the estimates are broadly similar, there is much evidence of population decline and little to support any population increases. We do not discuss trends in lion numbers, densities, demographic indicators such as altered sex-ratios and ranging behaviour, or the impacts of trophy hunting on these factors (Yamazaki 1996; Loveridge et al. 2007; Packer et al. 2009; Davidson et al. 2011). We should consider, however, the spatial distribution of lions and how this has changed.
When the IUCN (2006b) assessed lion range in West and Central Africa, they noted 20 LCUs in the region. Henschel et al. (2010) found that more than half (11) of these LCUs most likely no longer contain lions. Bauer (2006) noted lion population declines in several national parks in West and Central Africa. We find that 18 LCUs have lost their lions since 2006, with the greatest losses occurring in West and Central Africa (Supplemental materials, Table S3). All of these extirpations came from populations of fewer than 50 lions, and all but one (Nazinga-Sissili) were classified by the IUCN as having declining populations (IUCN 2006a, b).
Finally, we asked how many of these lions are in “strongholds?” We will elaborate on the definition in the “Discussion” section. Given our simple criteria, 10 lion areas qualify. Four of these are in East Africa and six in Southern Africa (Table S1). These strongholds span eight countries, contain roughly 19,000 lions in protected areas alone (more than 50 % of the remaining lions in Africa), and over 24,000 lions in the entire lion areas as delineated. No areas in West or Central Africa qualify.
Seven additional lion areas are potential lion strongholds, which contain nearly 4,400 lions (Table S1). These include two populations in West and Central Africa. The only remaining regions with potentially large numbers of lions that could act as future lion strongholds are Angola, Somalia, and the western half of South Sudan. The data on lion populations in these regions are relatively poor, while political instability makes the protection of wildlife in some areas difficult in the near future.
The extent of savannah Africa
Global assessments of how much tropical moist forest remains are made routinely, and, in the case of the Brazilian Amazon, monthly. Comparable assessments of tropical dry woodlands and savannahs are few. Moreover, we show that broad-scale global land cover assessments massively underestimate the amount of small-scale land use conversion.
We estimate the original size of savannah Africa to be 13.5 million km2. In 1960, using the human population data sources described above, 11.9 million km2 had fewer than 25 people per km2. The comparable area shrank to 9.7 million km2 by 2000. Sub-Saharan Africa increased its human population by nearly four-fold from 1960 (229 million) to 2010 (863 million) according to CIESEN (2005). The same source expects the population to more than double by 2050 (1.753 billion). Simply, the extent of savannah Africa has surely shrunk considerably in the last 50 years and will likely shrink considerably in the next 40.
In contrast to estimates of moist forest cover, for example, that come with few direct data on the species those forests contain, there are extensive data on large mammals in savannahs. These allow us to estimate what fraction of the remaining savannahs is sufficiently intact to house lions, the ecosystem’s top predator. We estimate this area to be ~3.4 million km2 (Table S1)—only 25 % of the total savannah—highlighting the fact that many low human density savannah areas are nonetheless too small and isolated to support viable lion populations.
Of the roughly 13.5 million km2 of savannah Africa, IUCN classifies about 1.36 million km2 (~10 %) as protected areas, excluding those regions gazetted for timber extraction (IUCN and WDPA 2010). Roughly 1.08 million km2 of this area overlaps with the lion areas. (In other words, substantial areas have protected status, but have lost their lions.) Now, the IUCN categories of protected areas include several that allow extractive use—and that includes hunting. Lindsey et al. (2006) estimate the total area of sub-Saharan Africa devoted to hunting as at least 1.4 million km2, and of this, ~250,000 km2 is in Tanzania. What we cannot easily estimate is the various overlaps between areas with lions, hunting areas, and the various classes of IUCN protected land on a country-by-country basis. Some countries, such as Kenya, do not permit hunting.
To assess lions in Africa, a good map is essential
Total population estimates alone mean little in the absence of knowledge of where lions are. Our maps suggest that lion populations survive in some 67 areas, of which only 15 hold at least 500 lions. While a small fraction of these areas appear to be large and continuous on satellite imagery (e.g. the east of the Central African Republic, southeast Chad, and west South Sudan sub-populations and the Selous and Niassa populations), there are no surveys for several of those areas and their status is uncertain. The majority of sub-populations are small and isolated. Some are so isolated that quibbling over our criteria for land use change would make no difference: the animals that remain are a very long way from individuals that might rescue the population demographically or genetically.
A good map is necessary, but it is not sufficient
An obvious caveat is that areas for which we detect little conversion of savannahs to croplands may still suffer human impacts that make them unsuitable for lions. Over-hunting for trophies, poaching—of lions and of their prey species—and conflict with pastoralists may not have any visual signal to satellites. Even where there are low human population densities and areas designated as national parks, there need not be lions within them. The poor performance of even large protected areas in West Africa is striking. For example: Henschel et al. (2010) surveyed Comoé, West Africa’s largest park, a World Heritage Site that is roughly half the size of Kruger National Park in South Africa. Whilst Kruger holds nearly 1,700 lions (Ferreira and Funston 2010), and much of Comoé looks to be free of human disturbance from the high-resolution imagery that Google Earth provides, Henschel et al. (2010) found no lions, few native mammals, and extensive evidence of poaching and grazing by domestic livestock in Comoé. Size alone does not protect even the largest parks if they suffer poor management (Bauer et al. 2003).
Satellite imagery does pick up recently burned savannahs, sometimes covering hundreds of square kilometres. These could be natural or set by pastoralists to improve grazing. Analyses of the conservation consequences of anthropogenic fires are available for moist tropical forest against a backdrop of protected areas (see Adeney et al. 2009). We have not yet analysed available global data as a means to assess pastoralists’ impacts on the savannahs and how protected areas modify those impacts.
Conversely, we cannot exclude the possibility that lions might still be able to move through areas with land-use conversion, though much experience suggests that they suffer high mortality when they do. For example, Woodroffe (2000) estimated a mean human population density threshold at which lions went extinct of 26 people per km2. Many mechanisms might underpin this threshold, but land-use conversion is the most plausible. The match between her threshold and ours is striking.
Finally, even within suitable habitat, lion densities vary greatly (see Chardonnet 2002). Densities of prey also vary widely when considering the variation in rainfall and soil type across lion range (Coe et al. 1976; East 1984; van Orsdol et al. 1985; Hayward et al. 2007).
Lion population estimates
The differences between these estimates do not represent an increase in lion populations in Africa, but are a direct result of different methods. There is evidence of strong declines and even extirpation of lions in some range countries. Especially in West and Central Africa, declines have been dramatic and conservation measures are urgent. While lions are protected in some of the lion areas, in many they are not, and in others they are hunted. While user-communities express the desire to manage lions sustainably, achieving that for any long-lived species is problematic. Several studies raise concerns about the impact of trophy hunting on lion densities and demographics (Yamazaki 1996; Loveridge et al. 2007; Davidson et al. 2011, Becker et al. 2012.). As noted above, the area devoted to lion hunting is large and Lindsey et al. (2006) emphasise the importance of hunting zones for protection of lions and their habitat.
How credible are the lion estimates?
Lions have low densities, large ranges and low visibility and are intrinsically difficult to count accurately. Few of the studies we report involve statistically justified surveys. The data we report are mostly “expert opinions”. They are controversial, yet we cannot simply pretend they do not exist. We now address their strengths and weaknesses.
The process that produced estimates of lion numbers involved people with widely different experiences and motivations. Some estimates were produced at meetings where they were hardly questioned, politely assuming equal expertise to keep the process going and reporting that they were “working figures.” The IUCN-sponsored workshops had delegates that were both biologists and politicians. However dedicated and well intentioned the participants, there is at least the potential for numbers to reflect wishful thinking or national policies that put a positive spin on numbers to ensure continued funding support. Countries across savannah Africa receive disproportionate funding for conservation from the World Bank, for example (Hickey and Pimm 2011).
Bauer and Van Der Merwe’s report (2004) went through peer-review and the IUCN reviews (IUCN 2006a, b) embraced broad-scale consultation with a wide variety of sources. These two quality control mechanisms were used to a lesser extent by sources producing national estimates from the sport hunting industry (Chardonnet 2002; Chardonnet et al. 2009; Mésochina et al. 2010a, b, c; Pellerin et al. 2009).
Globally, assessments of natural resources by user-communities are consistently more optimistic than independent estimates (Pimm 2001). Whether trophy hunters and the reports they fund also consistently inflate lion numbers to ensure continued business should be detached from any heated rhetoric and viewed simply as the legitimate scientific question that it is.
Table S1 shows that various studies by Mesochina et al. (2010a, b, c), Chardonnet (2002), Chardonnet et al. (2009) and Pellerin et al. (2009) constitute the majority of the putative lions (~55 %). These studies all had similar methodologies for estimating lion populations. They used estimates from scientific studies for areas that had them (e.g. call-in stations, individual identification etc.). For areas without, they used questionnaires and interviews to determine the frequency of lion presence within the past 5 years. They developed an equation to estimate density based on the closest, well-established density figure as the baseline and corrective factors to alter that density. Tailoring the equation for each specific area based on a variety of factors, density estimates and hence overall population numbers were generated for all areas with lion presence. We find this method scientifically debatable but we do see value in presenting the speculative results of this user-community along with the other data and provide an alternative estimate that includes them.
Certainly, these methods could overestimate both lion range and numbers. Since these reports affect over half of all lions, they greatly affect the global population estimate. This concern precipitated the generation of a global population estimate with and without the hunter-funded numbers (Table 1). With the user-community funded reports, the total number of lions increases by about 8 %.
For specific examples, IUCN (2006a) estimated 5,500 lions in the Selous, 4,500 in the Ruaha—Rungwa areas and 3,500 in the Serengeti and Mara. These total 13,500 lions. In contrast, Mesochina et al. (2010b) estimated these numbers at 7,644, 3,779 and 3,465, respectively, for a total of 14,888. These IUCN estimates are 8 % lower than those the user-community funded.
In sum, the numbers are broadly similar and, given the substantial uncertainties in lion counts, surely indistinguishable. Clearly, we need many other such independent comparisons if we are to draw more detailed conclusions. This applies a fortiori to Tanzania where the numbers are highest and where there are many uncertainties.
The 67 lion areas contain some populations that are large, stable, and well-protected—and so likely to persist in the foreseeable future. They also contain those that are so small, isolated, and threatened that only immediate, energetic conservation measures can offer any hope for their survival. And, of course, there are lion areas that are everywhere in between. How one groups areas across this continuum is inevitably arbitrary. Our approach is to use three classes: strongholds, potential strongholds, and the remainder. Broadly, these correspond to areas where management appears to be working (but we should always be vigilant), where immediate interventions might create a viable population, and where present management clearly is not working.
Our threshold of 500 (see “Methods” section) comes from Björklund (2003) who assessed the risk of inbreeding in lion populations due to habitat loss. He determined that, “…to sustain a large out-bred population of lions, a continuous population of at least 50 prides, but preferably 100 prides, with no limits to dispersal is required.” We took the average lion pride as containing approximately five adults (Bauer et al. 2008). Of course, the numbers of prides to avoid inbreeding is itself an arbitrary number, not a genuine threshold. (Simply, the fewer males who contribute genes to the next generation, the more inbred the population will be.) Moreover, the mean pride size is smaller in West and Central Africa, so the W-Arly-Pendjari population might also sensibly qualify as a stronghold. (We consider it a potential one.)
From the data derived in the lion population assessment, as well as the World Database on Protected Areas (IUCN and WDPA 2010), we considered only those lions found within existing protected areas including those with IUCN categorization that allow hunting, to count towards the minimum viable population. The Tarangire lion area of Tanzania, has an estimated 700+ lions, but only ~200 in protected areas with IUCN categories I–VI. The rest are found in non-designated hunting areas that do not qualify towards stronghold status.
Finally, only lion areas that are contained within LCUs having stable or increasing lion population trends as per the IUCN (2006a, b) are lion strongholds. The single exception to this rule is the Tsavo/Mkomazi lion area (Maasai Steppe LCU), which IUCN cites as having decreasing numbers. However, while lion numbers are declining outside of protected areas, we believe that lions within the parks are usually well protected and in sufficient numbers to meet the criteria. This criterion also has its uncertainties, for in some parks—Kafue National Park in Zambia, for example—poaching of lion prey may be a cause of concern for the lion’s long-term persistence. IUCN’s statement that the populations here are “stable” may be optimistic. Similarly, intense hunting outside protected areas can also affect those populations within the reserves (Woodroffe and Ginsberg 1998). These caveats accepted, the broad conclusions of our Table S1 remains: approximately 24,000 lions are in strongholds, about 4,000 in potential ones, but over 6,000 lions are in populations that have a very high risk of local extinction.
Lion numbers have declined precipitously in the last century. Given that many now live in small, isolated populations, this trend will continue. The situation in West Africa is particularly dire, with no large population remaining and lions now absent from many of the region’s national parks. Central Africa is different in that it has a very large contiguous lion area centred in the Central Africa Republic. In view of reported declines, it still does not qualify as a stronghold. Populations in these regions are genetically distinct (Antunes et al. 2008; Bertola et al. 2011). Keeping these populations from extinction will require conservation efforts well beyond the dismal performance of the region’s other protected areas. (The World Conservation Congress, 2012, issued a formal resolution Res 5.022, specifically supporting mammal conservation initiatives in these regions, http://www.iucn.org/about/work/programmes/global_policy/gpu_resources/gpu_res_recs/)
Hunting areas are extensive, so the fate of lions depends on how well user-communities manage them. The same principle applies to lions within protected areas, with responsibility falling on protected area managers to secure these populations. Finally, lions also occur well beyond protected areas, and how well one manages lion-human conflict will determine persistence there. Yet, conflict outside protected areas can affect lion persistence within (Woodroffe and Ginsberg 1998). Good protection within a protected area is not sufficient if there is unrelenting killing of lions outside it.
Central Africa may have sizable lion and prey populations, but they are poorly known, even by African standards.
That said, independently verified census data, using statistically repeatable techniques are the rare exception, not the rule, across even relatively well-studied East and Southern Africa. The situation is particularly acute for Tanzania, which holds a large fraction of the world’s lions.
Repeated mapping of areas which have at least the potential for lions because of their low human impacts may provide the only quantifiable measures of how savannah Africa is shrinking from the lion’s viewpoint. This is necessary, but definitely not sufficient. The lack of repeated, statistically credible lion counts, for well-defined areas is a striking omission, one that must be rectified if we are to assess not only the trends in lion numbers, but our success in reversing their declines.
This project was supported by National Geographic Society’s Big Cats Initiative. We would like to thank those Interns who spent time digitizing parts of Africa: Corey Anco, Gina Angiolillo, Sam Baraso, Mike Barrett, Emily Buenger, Rachael Carnes, Megan Cattau, Jennifer Chin, Jessica Daniel, Jill Derwin, Kristana Erikson, Derek Fedak, Kristen Fedak, Colin Hutton, Emily Myron, Lisanne Petracca, Rachel Roberts, Stephanie Roe, Cooper Rosin, Victoria Shelus and Christopher Smith. We also acknowledge the support of Duke University’s Nicholas School of the Environment.
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