Systematic review of the impact of restrictive wildlife trade measures on conservation of iconic species in southern Africa
PMCID: PMC11780195
PMID: 38578131
Abstract
Abstract Trade restrictions are often advocated and implemented as measures to protect wild species threatened by overexploitation. However, in some instances, their efficacy has been questioned, notably by governments in the southern African (SADC) region, which tend to favor a sustainable use approach to wildlife management. We conducted a systematic review of published literature guided by the PRISMA process to examine the effectiveness of trade restrictions and directly related control measures in addressing threats to species conservation in the SADC region, with a focus on elephants ( Loxodonta sp.), rhinoceroses ( Ceratotherium simum , Diceros bicornis ), lions ( Panthera leo ), and pangolins ( Manis sp.). We focused in particular on the direct conservation impact of trade restrictions at species or population level, indirect conservation impact at human behavior or attitude level, and socioeconomic impact on rural livelihoods and well‐being and on national economies. Research on these topics was uneven and focused strongly on the effects of trade restrictions and law enforcement on crime‐related behavior. Research gaps include socioeconomic impacts of trade restrictions, including effects of international restrictions on local livelihoods and consequent secondary conservation impacts, and evaluations of attempts to disrupt criminal networks. Based on the reviewed impact evidence, the effectiveness of international trade restrictions depends on a range of fully aligned measures in countries of origin, transit, and consumption. For example, our results suggest positive ecological short‐term but negative or unknown long‐term socioeconomic impacts of domestic restrictions. Based on these findings, key policy requirements include more nuanced approaches to incorporate a range of appropriate measures in range, transit, and consumer countries, that focus on capacity development for early detection and apprehension of incursions inside protected areas; measures for constructive engagement with relevant local communities outside protected areas; and future research to improve understanding of the socioeconomic contribution of wildlife.
Full Text
Wild populations of iconic species, such as elephants (Loxodonta sp.), rhinoceroses (Ceratotherium simum, Diceros bicornis), lions (Panthera leo), and pangolins (Manis sp.), have been receding across many parts of Africa and are reported to be threatened by poaching for trade purposes (Bauer et al., 2016; Emslie, 2020; Emslie et al., 2016; Gobush et al., 2022; Nixon et al., 2019; Pietersen et al., 2019). Accordingly, various policy measures seek to address the perceived threat from trade. However, due to varying success rates, such measures are regularly debated. It is, thus, imperative to evaluate this threat and current attempts to mitigate it in relation to other factors that may drive wildlife decline. More specifically, there is a need to consider the effectiveness of wildlife trade restrictions as a conservation measure in the southern African (SADC) region.
Historical events have shaped the perception of trade activities as main threats to southern African wildlife, including the adoption of trade restrictions to address these. Excessive hunting for meat, other products, and sport in North America and southern Africa, especially during the second half of the 19th century, led to growing awareness of overhunting as a threat to species survival and various consequent attempts to prevent this (Beinart & Coates, 2002). However, the perception of trade as a threat to species developed differently in the 2 regions, eventually resulting in significantly divergent wildlife governance models.
The North American public associated the destruction of species, such as bison (Bison bison) and passenger pigeon (Ectopistes migratorius), with market hunting and trade, which resulted in trade‐restrictive legislation in the form of the Lacey Act as early as 1900. In contrast, after a period of consolidation through area‐based state protection, southern Africa began to embrace market‐based approaches to wildlife governance with the onset of game ranching in the 1960s. Southern African countries thus became policy outliers, allowing and even encouraging sustainable use and trade in wildlife predicated on the devolution of wildlife proprietorship and use rights (including the right to trade), which underpin the region's contemporary sustainable use approach (Abensperg‐Traun, 2009). In most other countries, wildlife is state‐owned or an open‐access resource. The corresponding absence of rights and capacities of exclusion conferred by devolved proprietorship calls for mechanisms, such as trade restrictions, to prevent overexploitation (Schlager & Ostrom, 1992).
The early 20th‐century US policy approach to wildlife trade gradually extended internationally and, embodied by a 1963 resolution by the International Union for Conservation of Nature (IUCN), provided the impetus for the Convention on International Trade in Endangered Species of Fauna and Flora (CITES), effective from 1975. The agreement aims to regulate trade across international boundaries by establishing protocols between signatory countries. It employs a listing mechanism whereby all international trade in species listed on CITES Appendix II is subject to a permitting requirement to deter unsustainable levels of exploitation. Species considered threatened with extinction are listed in Appendix I, and international commercial trade in these species is prohibited. Notwithstanding these listings, countries can apply stricter domestic measures (e.g., prohibition of imports or exports of Appendix II species). Crocodilians and spotted cats were initial concerns for CITES in the late 1970s (Wijnstekers, 2018).
Given our focus on elephants, rhinoceroses, pangolins, and lions, Figure 1 provides an overview of CITES‐related trade‐restrictive policy interventions and related indicative trends for these species from 1970 to 2020. Rhinoceroses and elephants drew attention as overexploited species for trade purposes early on (Martin, 1983; Somerville, 2016). More recently, pangolin species have similarly gained prominence (Heinrich et al., 2016), and there are growing concerns about possible trade impacts on African lions (Panthera leo) (Williams et al., 2017a). A surge in poaching and trafficking of these species in the late 2000s (Figure 1) (and the concomitant emergence of a new legal export trade of lion body parts from South Africa) prompted governments and nongovernmental organizations (NGOs) to take action, which included promoting and implementing further trade restrictions (’t Sas‐Rolfes, 2017). These responses are ongoing, and wildlife trade (both illegal and legal), especially in the charismatic mammalian species, features as a controversial and fiercely debated issue on global conservation policy and research agendas. Although CITES provides an overall framework for regulating or restricting trade, governments have employed a range of additional restrictive or restriction‐supportive policy measures throughout the trade chain, including law enforcement and efforts to reduce consumer demand through behavior change interventions.
With this in mind, we conducted a comprehensive and systematic review of scientific and gray literature to provide a clear and structured synthesis of the existing evidence on the impact and effectiveness of international wildlife trade restrictions for conservation in SADC countries from 1970 to 2020. The review purposefully excluded any developments during the COVID‐19 pandemic due to its unique and substantial influence on trade patterns, incomparable to the previous decades. Our results are based on a project funded by the U.S. Agency for International Development (USAID) with a broader focus (but limited to the specified iconic species), including measures aimed at indirectly influencing or controlling trade, such as resource rights regimes (’t Sas‐Rolfes & Hiller, 2020). The review framework builds on earlier work that evaluated the conservation effectiveness of trade‐related policy interventions at the global level (Cheng et al., 2017; UNEP, 2019) but concentrates more specifically on the impact of trade restrictions on the conservation of elephants, rhinoceroses, pangolins, and lions in SADC countries.
We analyzed and synthesized the results of 46 studies that qualified as impact assessments of trade restrictions undertaken from 1970 to 2020 guided by the Preferred Reporting Items for Systematic Reviews and Meta‐Analyses framework (PRISMA) (Moher et al., 2009). We selected the studies based on an analytical framework for evaluating wildlife trade restrictions on conservation outcomes and employed a rigorous review protocol, as described below and guided by previous relevant literature (Galvin et al., 2018; Partelow et al., 2017; Soliku & Schraml, 2018).
We initially developed a basic analytical framework of influencing and outcome variables consistent with the review scope (Figure 2). The framework shows the influencing factors on the left of the diagram and the outcome variables on the right. The input factors were structured according to a simplified trade chain (’t Sas‐Rolfes et al., 2019). We synthesized categories used in previous frameworks to account for relevant impact factors along these trade‐chain dimensions (Cheng et al., 2017; UNEP, 2019).
Guided by the analytical framework, we conducted an extensive search on Web of Science (6 May 2020), Scopus (8 May 2020), and Google Scholar (19 May 2020). We used the Boolean search terms (Table 1), specifying geographical areas, animal species, and trade‐restriction‐related keywords. Our search further targeted specialist websites and databases during the specified time frame to account for relevant nonpeer‐reviewed studies (i.e., gray literature, including reports of NGOs, government agencies, or other relevant institutions) (Appendix S1). Where appropriate, we applied a snowball approach during our screening process (i.e., using references of selected papers to find additional sources) and combined all search results into a single data set. Compared with peer‐reviewed literature, it was impossible to conduct gray literature searches with the same rigor. Hence, our results might not represent all evidence‐based data available at the point of the literature search.
After implementing the search strategy and eliminating duplicates, all papers (originally 5667 without duplicates) were subjected to a multistep screening process, initially screening titles, then abstracts, and finally evaluating full publications (Figure 3). We excluded all articles unrelated to our study topic, outside the geographical location, ineligible publication types (e.g., editorials, commentaries, etc.), and papers not in English during the title‐screening phase. During abstract screening, studies incompatible with the analytical framework were removed. Finally, we read the main texts and rejected all papers that did not qualify as evidence‐based impact evaluations. We only included experimental and quasi‐experimental studies that analyzed cause‐and‐effect relationships and considered confounding factors, along with qualitative studies that applied rigorous validity and reliability measures such as triangulation or intercoder reliability, in addition to systematic reviews and multiregression models testing the sensitivity of results to potential confounders. In other words, we excluded publications that did not examine the effects of at least one influencing factor on at least one outcome variable of the framework beyond monitoring approaches (Cheng et al., 2017) or exhibited no counterfactual thinking (Baylis et al., 2016). This screening process resulted in a total of 46 accepted studies.
For data analyses and synthesis purposes based on qualitative thematic analysis (Braun & Clarke, 2006), we prepared a coding sheet and data extraction protocol (Appendix S2) and added relevant information to the data set in Microsoft Excel 2110 accordingly. We ascertained evidence‐based research for each combination of influencing factors and outcome variables, resulting in clusters of studies for these combinations with reference to species and countries. We used open, manual coding to analyze this qualitative data inductively, inferring evidence for the impacts of influencing factors on outcome variables (Drury et al., 2011; Newing et al., 2011). We further synthesized the themes of findings and insights of the study clusters by grouping similar codes together to form themes (Gioia et al., 2013; Khan, 2014). The themes described particular levers or determinants wielding a specific effect on outcome variables. Based on these levers, we refined our synthesis through verbal discussions relating and contrasting the themed insights from the various studies, resulting in an organized overview of the existing research (Tables 2, 3, 4).
Risk of uncontrolled meat poaching and human encroachment by rural communities due to loss in livelihood and human well‐being in cases of longer‐term restrictions (Mweetwa et al., 2018; Rosenblatt et al., 2014).
Elephant: Prohibition of elephant hunting in Botswana (introduced 2014): Poaching intensified significantly between 2014 and 2018 (Schlossberg et al., 2019).General: Hunting moratorium of 2014 in Botswana: Progressively antagonistic attitudes of towards wildlife of villagers of community‐based natural resource management programs (CBNRM) and perceived rise of poaching levels (Gaodirelwe, Masunga, et al., 2020; Gaodirelwe, Motsholapheko, et al., 2020).
Incentivizes hunters toward older trophies; reduced risk of hunting young, reproducing male lions; fewer trophies per annum overall (Begg et al., 2018).
Stabilized elephant numbers in Luangwa Valley in Zambia (Jachmann & Billiouw, 1997).
Lion: Reserves with the largest management budget: Highest lion populations (Packer et al., 2013).
Rhinoceros & Elephant: Small antipoaching field staff units in Zambia's Luangwa Valley (low manpower) and mild prison sentences for offenders: Unabated rhinoceros and elephant population declines due to illegal activity (1979–1985); effective at capturing poachers, but ineffective at protecting the large elephant populations over the vast area (Leader‐Williams, 1996; Leader‐Williams et al., 1990).
Elephant: Government effectiveness and human development: Impact on poaching levels measured as the Proportion of Illegally Killed Elephants (PIKE) at the country level (Burn et al., 2011).
Elephant: Significant increases of law enforcement staff in Zimbabwe's Gonarezhou National Park between 2000 and 2010: Minimized illegal hunting, despite an expected increase in poaching due to the country's economic collapse (Gandiwa et al., 2013).
Rhinoceros: Law enforcement efforts in the Lower Zambezi Valley in Zimbabwe: No apparent reduction in illegal activity with estimates that a 2% elephant population growth rate needs triple the field staff (Martin, 1993).
Rhinoceros: Rapid response measures: identified as a suitable means to recover rhinoceros horns (Milledge, 2007).
Rhinoceros: Generalized linear model factors (i) GDP per capita in Far East Asia, (ii) fine upon conviction, and (iii) antipoaching efforts most sensitive predictors of: Rhinoceros poaching levels in South Africa, emphasizing suitable law enforcement measures as vital to curb rhinoceros poaching under increasing wealth scenarios in the Far East (Di Minin et al., 2015).
Rhinoceros: Focus on leadership and intelligence, with sufficient funding most influential for: low rhinoceros poaching levels in a Zimbabwean reserve, largely due to highly committed, loyal, and long‐term staff workforce limiting the access of poachers to inside knowledge of security systems and flipping antipoaching activities from reactive to proactive (Ball et al., 2018).
General: Increased capacity and capability of well‐paid law enforcement village scouts with superior knowledge of the surrounding area in Zambia's Lupande Game Management Area: Dramatic increases in arrests and firearm confiscations; more protective attitude of villagers for wildlife (Lewis et al., 1990).
General: First 10 days of patrol periods of patrol teams: Most effective for encountering illegal activities and making arrests (Siamundaala et al., 2009).
Elephant/Rhinoceros: Strong law enforcement more effective than variable or fixed penalties according to an economic model on black rhinoceroses and elephants in Zambia's Luangwa Valley (1979–1985) to deter organized crime gangs because potential penalties for poaching would need to be raised exponentially to counter the vast gains, including a shoot‐to‐kill policy to constitute an effective deterrent (Leader‐Williams & Milner‐Gulland, 1993; Milner‐Gulland & Leader‐Williams, 1992).
Elephant: The probability of interception strikingly more effective than lowering black market ivory prices according to a bioeconomic model to: reduce the planned number of poaching expeditions (Lopes, 2015).
Pangolin: Stark increase in the number of confiscated ground pangolins (Smutsia temminckii) in Zimbabwe (2010–2015) combined with severe penalties: pangolins taken from the wild for the black market limited (Shepherd et al., 2017).
General: Dramatic increase of poaching costs (willingness to implement shoot poachers on sight policies) according to an economic model of poaching constitutes: The only way to protect endangered species when nonpoaching wages are low and the economic benefits of poaching are high (Messer, 2010).
General: Law enforcement/park ranger presence, dangerous wildlife and fines in Tanzania: Negligible probabilities of any harm (fines or injury) when hunting illegally; perceived higher number of hours a poacher needs to remain concealed to avoid detection (Knapp, 2012).
Elephant: Based on DNA‐matching technology poaching affects: the social structure of elephant populations (Mondol et al., 2014).
General: New technologies such as thermal imaging (Hart et al., 2015), remotely piloted aircraft systems fitted with cameras, AI‐based applications (Bondi et al., 2018; Mulero‐Pázmány et al., 2014), and GIS and remote sensing to monitor poaching activities (Sibanda et al., 2016) suggest: Advanced poaching detection rates under experimental conditions.
Elephant: Continued investment in law enforcement needs to be combined with interventions targeting ivory demand reduction, corruption, and poverty alleviation to: reduce elephant poaching (Hauenstein et al., 2019).
Elephant: Levels of regional legal protection and other factors, in particular human access, the corruption perception index, and ecosystem type being affected: elephant poaching levels (CITES Secretariat, 2007).
Rhinoceros: Insufficient or complicit law enforcement in South Africa attributed to explain: higher levels of patrol efforts around poaching hotspots before rhinoceros poaching incidents, that is, field rangers were at the right place, but at the wrong time, suggesting that even high presence in a poaching area does not deter organized rhinoceros poaching gangs (Barichievy et al., 2017).
General: Regular monitoring of animal populations to: identify poaching hotspots and worrying trends as a crucial element for law enforcement success (Bauer et al., 2015; Ferreira et al., 2017).
Horns increasingly evading law and enforcement reaching illegal markets (from 2001) (Cheteni, 2014).
Rhinoceros: CITES Appendix 1 Listing followed by additional legal restrictions in South Africa: escalation of illegally killed rhinoceroses from 2007 despite substantial supporting law enforcement efforts (Emslie et al., 2016; Ferreira et al., 2018).
Pangolin: Immediate onset of CITES imposed zero‐quota policy in 2000: a spike in pangolin trade in Asia; a clear transfer of the preban trade volume to illicit markets (Challender et al., 2015).
Lion: Anticipated restrictive (zero) export quota for lion products, imposed at CITES CoP17: surge in legal exports of lion skeletons from South Africa in 2016 and rising concerns of emerging black markets for lion products (Williams et al., 2017a).
Elephant: restricted ivory supply due to CITES Appendix I listing (1989) compounded by Chinese ivory trafficking interception measures (2011–2012): quick rise of illegal ivory prices accelerating elephant poaching rates (Zhou et al., 2018).
Short‐term reduction of poaching pressure on many populations (Stiles, 2004; Zhou et al., 2018); however, persistent poaching increasing markedly from 1998 in countries with widespread corruption, civil unrest, or poor wildlife management, leading to further declining elephant numbers, particularly in West and Central Africa (Stiles 2004; Underwood et al., 2013).
Elephant: CITES ivory ban: reversing overall decline of African elephant numbers between 1989 and 2007, except in countries with unregulated postban ivory markets (Lemieux & Clark, 2009).
Rhinoceros: Social network analyses for trafficking network close to Kruger National Park: Crucial element to disrupt transnational trafficking networks effectively (Haas & Ferreira, 2015).
Rhinoceros: Lack of coordinated intelligence activities and inadequate legislation for prosecution: organized crime dealers and kingpins favor efficiency over security, as the risks of being caught and prosecuted are minimal, and security plans for crime syndicate members and their families exist (Hübschle, 2017).
General: Antihunting regulations in Namibia and Mozambique: negative attitudes of most study participants due to wide‐ranging negative effects on their well‐being (food, assets, direct income [from illegal rhinoceros hunting]) (Strong & Silva, 2020).
General: hunting moratorium of 2014 in Botswana: negative effects on household well‐being due to increased crop‐raiding and predation, job losses, and decline in income (Gaodirelwe, Masunga, et al., 2020; Mbaiwa, 2018).
General: Zambian hunting moratorium (2013–2014): adverse livelihood and well‐being effects in already poverty‐stricken areas due to lost meat and (seasonal) income possibilities through sport hunting (White & Belant, 2015).
General: Restrictive hunting legislation in Botswana: unwillingness of the Basarwa to submit to external controls over wildlife use and hunting, as wildlife is part of Basarwa's diet due its association with their heritage (Taylor, 2007).
pros for local people: (financial) security, indirect benefits like basic roads, water wells, and so forth from rhinoceros poachers and kingpins, whereas the state and private/public partnerships have failed in achieving tangible benefits and a sense of security; (ii) cons especially for women: impaired social fabric of village life and cause for fear of losing relatives through law enforcement (Hübschle, 2017).
Poor community members (i) dislike poachers due to perceived threat to the community's social security and (ii) struggle with enforcement officials due to perceived antipoor enforcement of conservation‐prone, restrictive policies for protected area, despite a generally positive attitude toward the protected area (Vundla, 2019).Rhinoceros: Militarization of antipoaching in Mozambique's Limpopo National Park: villagers fear further violent antipoaching tactics of park officials and rhinoceros poachers, such as burning houses of villagers rightly or wrongly associated with poaching; villagers suspect reenvisioned resettlement strategy to achieve conservation outcomes (Witter & Satterfield, 2019).
Effective anti‐ivory campaigns in conjunction with the ivory trade ban in 1989 are associated with stigmatizing buying or possessing ivory in America, Europe, and Japan, reportedly reducing demand in these countries, resulting in smaller postban ivory markets throughout Africa, except for Nigeria (Stiles, 2004).
Thailand limiting domestic ivory trade exclusively to products coming from registered captive Asian Elephants (Elephas maximus) in 2015 while banning the import, export, and trade in African Elephants (Loxodonta africana) resulted in a significant reduction of legal ivory trade in Bangkok, inferred from a downward trend in the number of shops selling ivory and the number of traded ivory products (Krishnasamy et al., 2016).
Powerful campaigns of the Chinese government using Radio, Film, and Television showed effects in reducing extravagant consumption and developing negative attitudes toward buying ivory products of the younger generation, while the campaigns are thought to have contributed to a drop in the price of illegal ivory (Zhou et al., 2018).
‐ A pre‐ and postban survey in Chinese cities related to China's shutdown of all licensed ivory carving factories and retailers at the end of December 2017 indicated both a significantly grown proportion of ivory rejectors and a decline in ivory purchases, despite a persistent residuum of “Diehard Buyers” indicating that demand might not be completely preventable (Meijer et al., 2018).
‐ A generalized linear model of rhinoceros poaching in South Africa suggests that in addition to increasing antipoaching efforts and monetary fines upon conviction, governance improvements in Vietnam would be crucial to maintaining rhinoceros populations by helping to reduce poaching (Di Minin et al., 2015).
The literature search and systematic review yielded 46 wildlife trade‐related impact studies relevant to the SADC region, focusing on the highlighted species. We found a strong focus on impact studies investigating supply‐side and transaction‐chain wildlife trade measures as input variables and the effects of monitoring and enforcing these measures as output variables (Figure 4) (references to corresponding studies with emergent thematic clusters in Appendices S3–S7).
The following main research areas emerged (Figure 4): law enforcement measures impacting human behavior (especially illegal hunting) or human attitudes toward wildlife crimes, particularly among rural communities (n = 20); the effects of law enforcement on wildlife conservation outcomes at the species or population level (n = 6); and the impact of international trade restrictions (in the form of CITES Appendix I listings) on wildlife conservation outcomes (n = 6). Furthermore, some research was conducted on the impact of legal supply restriction measures (including laws, policies, and regulations for spatial or species‐related constraints, such as quotas) on wildlife conservation (n = 7) and rural livelihoods (n = 3) and of demand‐side measures on conservation‐related behavior or attitudes (n = 5) (Figure 4).
The effects of the identification and disruption of actor networks and demand‐side measures were underresearched (Figure 4). Furthermore, none of the identified studies evaluated the impact of demand‐side legal measures to reduce the purchase, consumption, and possession of wild animals or wildlife products domestically (i.e., in SADC range states). However, few studies assessed the effectiveness of demand‐related restrictions in the target consumer countries, mainly in Southeast Asia. Further apparent gaps included a lack of research on the socioeconomic impacts of wildlife trade restrictions on rural livelihoods and national economies (Figure 4).
The following subsections summarize the themes emerging from our qualitative analysis of the identified impact studies (detailed thematic analysis in Tables 2, 3, 4). For the areas with the most obvious research gaps highlighted above, we briefly discuss the existing insights and evidence in the final 2 subsections (i.e., impact studies on rural livelihoods, well‐being, and national economies and insights into demand reduction for wildlife products of SADC origin).
International trade restrictions tend to be guided by CITES listings and include measures such as restrictions on cross‐border trade for primarily commercial purposes, permitting requirements, and quotas. Our qualitative analysis generated 4 themes in relation to international trade regulations. All themes relate to the effectiveness of CITES trade bans (i.e., Appendix I listings) (Table 2, T‐C1–T‐C4). (Theme codes in parentheses here in “Results” refer to summarized conservation‐related research findings in Table 2.) The themes highlighted the ambiguity and uncertainty of the effectiveness of such measures for wildlife conservation. The results of the few existing impact evaluations varied considerably in their assessment of the ecological, human behavioral, and economic effects at the macro level. This substantially compromised our ability to infer direct links relating to the impact of international‐level regulations.
Impact studies on rhinoceros and pangolin species as well as on lions confirmed concerns that some international trade bans may simply drive markets underground instead of exerting a discernible positive influence on species populations (theme code T‐C1 [Table 1]) (Conrad, 2012). Furthermore, evidence‐based research on African elephants suggested that unregulated markets, widespread corruption, civil unrest, or poor wildlife management increase the likelihood of rendering trade bans ineffective (T‐C2). These findings need to be considered in the light that some countries might rather need to address an elephant overpopulation challenge. An early economic model based on data from Zambia reflected that optimal elephant stock was consistently lower than the estimates of elephant populations for both trade‐ and no‐trade scenarios, suggesting that such countries might need to reduce those levels actively (through culling) or passively (through underinvestment in protection) (Bulte & van Kooten, 1999).
We found examples of short‐term trade bans benefitting conservation in conjunction with further conditions (T‐C3). However, we noted a persistent debate over the role of post‐ban efforts to enable subsequent use and trade, based on cases lauded as trade‐ban successes, notably crocodilians (Crocodilia) and the vicuňa (Vicugna vicugna), for which CITES coupled strict trade restrictions with efforts to support nations in establishing sustainable use programs (Lichtenstein, 2010; Moyle, 2013; Thorbjarnarson, 1999). One theoretical model suggested a trade ban was likely to positively affect elephant populations if it achieved the following: a widespread moral demand‐reducing effect; improved interception of smuggled products; limited increases of ivory stockpiles from official production; and no reduction in law enforcement efforts (Heltberg, 2001). Another theoretical model indicated that a successful trade ban would need to deal effectively with the so‐called free‐rider problem, whereby nations placing a high existence value on elephants without actively investing in their survival are classified as free riders (Khanna & Harford, 1996). The authors argue that an international transfer payment mechanism would support conservation strategies in the producer countries.
Intelligence‐led, proactive interruption and inhibition of illegal hunting activities were regularly emphasized as measures to render international trade restrictions effective (Hübschle, 2016). However, corresponding evidence‐based impact studies were few. The only emerging theme from the qualitative analysis was a lack of collaborative approaches across jurisdictions (T‐C4). As a result, very few large‐scale seizures prompted successful investigations or arrests and almost no convictions. Research suggested that failure to disrupt criminal networks more effectively may result from missing federated criminal evidence data and trust as a basis for legal prosecuting provisions between different jurisdictions (Haas & Ferreira, 2015; Nanima, 2019); a lack of complements, such as scanners, X‐ray devices, sniffer dogs, and so forth (Milliken, 2014); a lack of coordinated intelligence activities; and inadequate legislation to prosecute individuals (Hübschle, 2017; Nanima, 2019).
Studies investigating the impact of domestic laws, policies, and regulations to restrict wildlife harvesting and supply on wildlife conservation outcomes elicited 3 synthesized themes (Table 2, S‐C1–S‐C3). Wildlife hunting bans, moratoria, and quotas constituted the typical domestic restriction measures in the identified impact studies. Studies of hunting prohibitions on lions and elephants suggested that these measures only benefited strained animal populations in the short term (S‐C1). The associated loss of livelihood and human well‐being for rural communities during the hunting suspension led to uncontrolled meat poaching and human encroachment and an even greater risk for wild animal populations in the longer term. A second theme indicated detrimental consequences for social animal structures, such as elephants, when hunting quotas across national borders were uncoordinated (S‐C2). Another theme suggested that restrictions were more effective at modulating human behavior in favor of wildlife conservation when framed as permissions rather than prohibitions (S‐C3).
Most evidence‐based research on dedicated trade‐restriction measures examined the impact of efforts to monitor and enforce trade‐restrictive laws, policies, and regulations on conservation‐related outcomes (Figure 2). Studies on measures such as patrol efforts, sentencing strategies, or intelligence elicited 5 corresponding themes (Table 2, S‐C4–S‐C8).
Numerous studies suggested that sufficient high‐quality and proactive law enforcement efforts are beneficial for wildlife conservation, both directly (on species or population level) and indirectly (on human behavior level) (S‐C4). In other words, impact studies showed positive effects of law enforcement measures to combat wildlife crime or achieve species conservation when these efforts were well‐resourced both quantitatively, in terms of human and financial capacities, and qualitatively, in terms of the capabilities of field rangers and leadership, even in cases when illegal hunting and fishing soared in countries experiencing economic hardship, such as in Zimbabwe after its economic collapse (Lindsey et al., 2011). Approaching monitoring and enforcement in a proactive rather than a reactive way (i.e., a shift from patrolling efforts to intelligence‐based approaches) was also found to positively influence conservation outcomes. Conversely, this theme included findings that poaching remained a constant and severe problem in cases of insufficient or incapable resources (S‐C4). The effectiveness of law enforcement efforts was sometimes measured in terms of discovering illegal activities ex post when the lives of targeted animals had already been lost, such as in Milledge (2007) who reported a 42% rhinoceros horn recovery rate through measures ranging from rapid response in protected areas to investigations and confiscations in urban centers in 9 African countries.
The research also showed that effective law enforcement hinges more on detection risk than on harm or loss (S‐C5). In other words, although measures to increase detection risk, such as patrol efforts, showed positive impacts on conservation outcomes, the potential harm or loss in case of detection (through prison sentences, fines, or other forms of financial loss) did not constitute a comparable deterrent, unless such penalties were raised to extreme levels, such as a shoot‐on‐sight policy for poachers. Furthermore, large‐scale prosecutions for wildlife crimes tended to be rare globally (Nowell, 2012). A third theme emerged, suggesting that new technologies show promise to enhance detection risk for illegal hunters (S‐C6). However, evidence‐based studies investigating the impact of these technological developments on conservation outcomes were rare (Figure 2). Most relevant studies were confined to field tests of various tech solutions under experimental conditions (Pimm et al., 2015).
Several authors argued that measures to change human behavior and attitudes for wildlife conservation purposes must couple law enforcement measures with other efforts to mitigate negative consequences for socioeconomic development (S‐C7). The identified impact studies suggested that such measures might need to address consumer demand, corruption, and poverty and be supplemented by regular monitoring of animal populations. The final theme linked the effectiveness of law enforcement to nonmarket‐related social constructs of a society's relationship with an animal species (S‐C8). Evidence‐based investigations highlighted the significance of social legitimacy factors in supporting or undermining domestic law enforcement efforts (Hübschle, 2017).
The synthesized themes relating to this topic are summarized in Table 3 (with theme codes appearing below in parentheses). We found evidence‐based impact studies of restrictive measures along the trade chain on socioeconomic development outcome variables were sparse in comparison with conservation‐related outcomes (Figure 2). Consequently, the qualitative thematic analysis of findings was limited to a small number of studies, even though such impacts could plausibly be significant and lead to adverse secondary conservation outcomes.
Our analyses elicited the potential of trade bans to significantly harm wildlife economies as the only theme for the socioeconomic impact of international trade restrictions (T‐SE1). Any effects of measures restricting trade activities on rural livelihoods were researched on a domestic level. Domestically, hunting restrictions overwhelmingly demonstrated adverse impacts on rural livelihoods and well‐being (S‐SE1). Imposed costs included lost food sources, assets, jobs, or other forms of income, thereby aggravating already poverty‐stricken areas. This theme was supported by other research emphasizing the complementary benefits of both tourism and hunting for rural communities in Namibia because the benefits occurred at different times, appeared in different places, and reached different sections of local communities (Naidoo et al., 2016). Similarly, a survey on the effects of the US suspension on imports of captive lion trophies from South Africa highlighted alleged job losses in rural areas, thereby indicating the impact of trade restrictive measures on livelihood outcomes (Williams & ’t Sas‐Rolfes, 2019).
In addition to material hardship, researchers identified how law enforcement measures can result in other detriments for rural communities, such as a loss of the social fabric in a village (S‐SE2). The studies in this theme highlighted how rural communities experience both benefits and costs through illegal hunting, especially when the state failed to deliver basic public services in poverty‐stricken areas (S‐SE2). However, this research also highlighted the ambiguous relationships of rural communities with poachers and law enforcement officers. Although poachers can be seen to threaten secure village life, there was also evidence of adverse treatment of villagers by law enforcement staff and associated fear of violent antipoaching tactics, despite the fact that entire villages are not necessarily involved in or complicit with illegal hunting of high‐value species. In their most extreme form, conservation‐related enforcement measures were reportedly used as a means for renewed dispossession and displacement of rural communities (Massé & Lunstrum, 2016).
Our review did not elicit evidence‐based research studies assessing direct links between demand‐side measures to restrict trade‐related activities and their effect on wildlife conservation or socioeconomic development in SADC range states (Figure 2; Table 4). Reductions in consumer demand were often presented as a proxy outcome variable to infer themes for reduced threats to species by means of legal measures to restrict activities along the trade chain. However, consumer demand reduction as an outcome variable was challenging to ascertain, partly because illegal purchases and consumption are clandestine and partly because demand is multidimensional and difficult to measure by a single attribute. Both sale volumes (quantities of goods sold per unit of time) and product prices would be relevant, especially the latter. Due to the ambiguity of the net effects of declining volumes accompanied by increasing prices, depending on the price elasticity of demand (’t Sas‐Rolfes, 2012), the only certain measure of declining demand would have been a confirmed simultaneous decline in both consumer sales volumes and prices.
Coupling law enforcement with consumer‐targeted government campaigns emerged as the one theme to enhance the potential of reducing demand in consumer countries (with a focus on ivory) (D‐D1). The relevant studies emphasized the potency of combining trade bans with enforcement measures and consumer campaigns to stigmatize the purchase or possession of ivory to effectively reduce demand. However, some researchers suggested that media campaigns and changing fashion alone provide a plausible alternative explanation for reversing the decline in Africa's elephant population (Challender et al., 2015). Overall, the full impact of regulatory interventions in China in late 2011 remained somewhat unclear (Gao & Clark, 2014), as did Vietnam's penal code revisions. The evidence for successful demand reduction of other relevant species products was less compelling. Although the domestic trade restrictions in Asian rhinoceros horn consumer countries in the early 1990s are believed to have been effective, the subsequent obvious surge in East Asian consumer prices in the early 21st century suggested that the effects were, in part, only temporary (’t Sas‐Rolfes, 2012).
To support regulation, NGOs made attempts at voluntary consumer demand reduction. These attempts applied a range of techniques, from public awareness campaigns and celebrity endorsements to more targeted social marketing techniques. Independent assessments of these attempts pointed to various and significant shortcomings (Dang Vu et al., 2020; Olmedo et al., 2020, 2018; Veríssimo & Wan, 2019), and their ultimate impact to date remains uncertain. There have been relatively few demand reduction interventions grounded in appropriately structured consumer research guided by behavioral science and even fewer robust impact evaluations of such interventions (UNEP, 2019).
The role of trade in relation to other factors driving wildlife species decline remains a somewhat uncertain and contested issue. The relatively low number (46) of studies that constituted acceptable evidence‐based evaluations related to this question was striking. Although wildlife trade has recently gained further significant prominence as both a perceived threat and a catalyst for conservation activism (’t Sas‐Rolfes et al., 2019), many assessments of species decline pointed to habitat loss and fragmentation as the most salient long‐term drivers. At the time of the 1989 CITES ivory trade ban, economists contemplated whether it would serve as a long‐term solution for African elephant conservation and concluded that it would not (Barbier et al., 1990). Around the same time, Wilson (1989) highlighted the main factor driving 20th‐century biodiversity loss as anthropogenic habitat destruction, fueled by the rapid growth of the global human population and associated economic activity.
In a subsequent analysis, Swanson (1994) argued that trade restrictions are most appropriate for genuine open‐access resources (e.g., marine species) because they provide a deterrent effect to slow down the rate of harvesting. However, for terrestrial species that occupy land with other potential uses and require the active investment of resources to manage and protect them, the associated opportunity costs with trade restrictions can undermine the long‐term economic case for conserving such species. If illegal consumer markets for their harvested products persist, they become increasingly costly to protect from commercial poaching. They may eventually be viewed as economic liabilities rather than assets, especially in the case of species that pose potential threats to the lives and livelihoods of local people. In such instances, reestablishing controlled and sustainably supplied legal trading regimes may be a better long‐term option to ensure species persistence.
Following a broader dialogue with inputs from both ecologists and economists, Swanson (1995) noted deep ideological differences over whether biodiversity conservation is best achieved through shielding nature from human development or through human development, which may also influence the perceptions of both relative threats to wildlife and the most appropriate measures to address these. Such differing emphases were reflected in recent global assessments of species threats. For example, one claimed that overexploitation is the most prevalent threat currently facing species (Maxwell et al., 2016), whereas another identified habitat loss as the more salient factor (Tilman et al., 2017). Nevertheless, it is notable that of the 11 categories of the IUCN Red List's current threat classification system, only 2—biological resource use and spread of invasive and problem species, pathogens, and genes—are (indirectly) associated with wildlife trade.
The IUCN Red List assessments identified illegal harvesting for international trade as the central threat to the 2 rhinoceros species (Emslie, 2020; Emslie et al., 2016) and a growing threat to pangolins, which are also harvested for domestic consumption and trade and threatened by habitat loss (Nixon et al., 2019; Pietersen et al., 2019). However, the African elephant assessment emphasized that although illegal hunting for ivory and meat remains a key factor in specific areas, the most important perceived threat is habitat loss and fragmentation, aggravated by increasing human–elephant conflict (Gobush et al., 2021). The lion assessment listed indiscriminate killing and prey depletion, accompanied by habitat loss and fragmentation, as key factors, with a minor role of poorly managed trophy hunting in some instances (Bauer et al., 2016). It noted only a small role for domestic trade and some concern over a potential future international trade in lion body parts.
Our review results indicated that CITES listings, when viewed as a stand‐alone measure, offered limited protection to these species, constrained by varying perceptions of social legitimacy among market actors and with potentially even detrimental conservation and socioeconomic outcomes. Announcements of unconditional or wide‐ranging trade restrictions, such as export or import bans, might even abruptly increase species threats by signaling scarcity in the marketplace, resulting in higher prices and increased incentives for illegal activity, which may persist (Hall et al., 2008; Rivalan et al., 2007). Our results suggested that, to be effective, CITES listings must be supported by a fully aligned range of appropriate measures in range, transit, and consumer countries. The CITES trade restrictions for rhinoceros, elephant, pangolin, and lion alike supported this insight that stand‐alone Appendix I listings tend to be ineffective in the longer term.
The 1977 CITES Appendix I rhinoceros listings failed to prevent the further poaching and decline of Africa's black rhinoceros. At the continental level, populations only started to recover after 4 key Asian consumer countries agreed to take measures to outlaw their domestic markets in 1993, following direct diplomatic pressure from the United States. Even so, under complete ban conditions, rhinoceros poaching resurged significantly from 2007 onward, not only slowing and threatening the recovery of black rhinoceros populations but also starting to reverse the previously impressive southern white rhinoceros (Ceratotherium simum simum) recovery. Uninterrupted since the 1960s, the latter recovery took place with the support of some legal trade measures for live animals and hunting trophies (’t Sas‐Rolfes et al., 2022). Importantly, the Appendix I listings also failed to prevent the loss of 2 subspecies, the northern white rhinoceros (Ceratotherium simum cottoni) and the northwestern black rhinoceros (Diceros bicornis longipes) (neither of which occurred in the SADC region).
Despite a reasonable body of research on the topic, the role of CITES in protecting African elephants continues to be disputed. Although it is widely agreed that the 1989 Appendix I listing suppressed key consumer markets and slowed the rate of poaching at the time, it is also clear that the subsequent benefits of the ivory ban under the CITES regime have been unevenly distributed and that local law enforcement efforts remain critical (Jachmann & Billiouw, 1997). Certain countries with adequately protected and sizable populations carry a disproportionately high burden in the form of management and opportunity costs. Attempts to address this imbalance by way of split listing (i.e., downlisting populations of well‐performing countries to Appendix II and then allowing one‐off ivory sales) have created confusion and tension. Critics blamed these on resurgent consumer demand in the early 21st century (’t Sas‐Rolfes et al., 2014). As a result, no further sales are currently contemplated, and ivory trade policy continues to be fiercely debated. However, recent analyses confirmed the importance of other domestic factors (e.g., poverty and corruption) in influencing elephant conservation performance (Kuiper et al., 2023). Furthermore, a comprehensive study of historical ivory prices (Do et al., 2021) suggested that elephant poaching is relatively inelastic. This implies that the overall effect of the CITES ban itself is relatively neutral, neither encouraging nor discouraging poaching significantly. This result appears to be supported by another recent study that showed fairly persistent poaching levels, especially in the southern African region (Schlossberg et al., 2020).
The socioeconomic impacts of CITES listings at national and, especially, local community levels were inadequately researched, and the opportunity costs imposed on the countries with good conservation track records that oppose them are potentially substantial. This is a cause for concern, especially given the current lack of long‐term vision for elephant ivory and rhinoceros horn trade. Both will continue to accumulate in collected stockpiles as long as populations of elephants and rhinoceroses continue to survive and naturally produce these harvestable and storable products. Furthermore, with evidence of persistent residual demand in consumer countries despite domestic trade bans, all indications were that these species will require the continued allocation of significant resources to protect them from poaching. Given the budgetary constraints facing many SADC governments, likely aggravated by the economic impacts of the COVID‐19 pandemic, it is unclear whether these resources will be available at adequate levels. Consistent reports of severe shortfalls in conservation funding suggest that there will be an ongoing, if not increasing, dependence on external donor support, which may be insufficient and insecure (Lindsey et al., 2018; McCarthy et al., 2012). Furthermore, significant proportions of the SADC populations of elephants, rhinoceroses, and lions are found on working lands rather than protected areas and may be replaced by domestic species or other forms of land use if they represent a socioeconomic burden.
Whether permanent bans or legal trading regimes are the best long‐term option for various species remains a highly contested and poorly understood issue, necessitating further neutral investigation by appropriately qualified analysts. Given the findings of Do et al. (2021), it seems likely that, at least for elephants, there can be no clear answers. Conservation success will variably depend largely on other local factors, regardless of whether legal trade takes place or not (unless legalizing trade creates direct and meaningful local benefits). For other species, if legal trade is to succeed as a conservation measure, it will likely depend on creating bespoke institutional arrangements (e.g., strong property rights and suitably competitive market mechanisms) with appropriate control measures, such as single‐channel marketing systems, accompanied by source certification and traceability measures to support enforcement and deter laundering of illegal products. Supporting technologies for such approaches have already been developed, such as the RhODIS DNA tracking system for rhinoceroses (Harper et al., 2018), and further research is being conducted to assess the effectiveness of chain‐of‐custody systems for lion bone exports from South Africa (Williams et al., 2021). However, for SADC states that may benefit from legal trade to win over others that may not, further investigation of supporting measures and other necessary assurances will be required. Such research should include likely consumer demand responses, following the example of Hanley et al. (2018), who conducted choice modeling of rhinoceros horn demand in Vietnam and identified preferences for humanely harvested wild horn from the least rare species.
Species with valuable harvestable products may be threatened by poaching incursions into protected areas; outside of these publicly funded areas (i.e., on privately funded working lands), such species are most likely to survive in situations where they provide meaningful net benefits to landholders. This suggests that, in the context of developing SADC economies, realistic achievement of species conservation outside of protected areas must embrace inclusive and innovative wildlife management practices to achieve human development goals. In other words, although protected area managers may be mandated to shield conservation from development, this luxury is largely absent outside these areas. In a post‐COVID‐19 world economy, these pressures are only likely to increase (Lindsey et al., 2020; Roe et al., 2020).
Sections
"[{\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0007\", \"cobi14262-bib-0024\", \"cobi14262-bib-0025\", \"cobi14262-bib-0033\", \"cobi14262-bib-0079\", \"cobi14262-bib-0087\"], \"section\": \"INTRODUCTION\", \"text\": \"Wild populations of iconic species, such as elephants (Loxodonta sp.), rhinoceroses (Ceratotherium simum, Diceros bicornis), lions (Panthera leo), and pangolins (Manis sp.), have been receding across many parts of Africa and are reported to be threatened by poaching for trade purposes (Bauer et\\u00a0al., 2016; Emslie, 2020; Emslie et\\u00a0al., 2016; Gobush et\\u00a0al., 2022; Nixon et\\u00a0al., 2019; Pietersen et\\u00a0al., 2019). Accordingly, various policy measures seek to address the perceived threat from trade. However, due to varying success rates, such measures are regularly debated. It is, thus, imperative to evaluate this threat and current attempts to mitigate it in relation to other factors that may drive wildlife decline. More specifically, there is a need to consider the effectiveness of wildlife trade restrictions as a conservation measure in the southern African (SADC) region.\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0010\"], \"section\": \"INTRODUCTION\", \"text\": \"Historical events have shaped the perception of trade activities as main threats to southern African wildlife, including the adoption of trade restrictions to address these. Excessive hunting for meat, other products, and sport in North America and southern Africa, especially during the second half of the 19th century, led to growing awareness of overhunting as a threat to species survival and various consequent attempts to prevent this (Beinart & Coates, 2002). However, the perception of trade as a threat to species developed differently in the 2 regions, eventually resulting in significantly divergent wildlife governance models.\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0001\", \"cobi14262-bib-0093\"], \"section\": \"INTRODUCTION\", \"text\": \"The North American public associated the destruction of species, such as bison (Bison bison) and passenger pigeon (Ectopistes migratorius), with market hunting and trade, which resulted in trade\\u2010restrictive legislation in the form of the Lacey Act as early as 1900. In contrast, after a period of consolidation through area\\u2010based state protection, southern Africa began to embrace market\\u2010based approaches to wildlife governance with the onset of game ranching in the 1960s. Southern African countries thus became policy outliers, allowing and even encouraging sustainable use and trade in wildlife predicated on the devolution of wildlife proprietorship and use rights (including the right to trade), which underpin the region's contemporary sustainable use approach (Abensperg\\u2010Traun, 2009). In most other countries, wildlife is state\\u2010owned or an open\\u2010access resource. The corresponding absence of rights and capacities of exclusion conferred by devolved proprietorship calls for mechanisms, such as trade restrictions, to prevent overexploitation (Schlager & Ostrom, 1992).\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0221\"], \"section\": \"INTRODUCTION\", \"text\": \"The early 20th\\u2010century US policy approach to wildlife trade gradually extended internationally and, embodied by a 1963 resolution by the International Union for Conservation of Nature (IUCN), provided the impetus for the Convention on International Trade in Endangered Species of Fauna and Flora (CITES), effective from 1975. The agreement aims to regulate trade across international boundaries by establishing protocols between signatory countries. It employs a listing mechanism whereby all international trade in species listed on CITES Appendix II is subject to a permitting requirement to deter unsustainable levels of exploitation. Species considered threatened with extinction are listed in Appendix I, and international commercial trade in these species is prohibited. Notwithstanding these listings, countries can apply stricter domestic measures (e.g., prohibition of imports or exports of Appendix II species). Crocodilians and spotted cats were initial concerns for CITES in the late 1970s (Wijnstekers, 2018).\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-fig-0001\", \"cobi14262-bib-0061\", \"cobi14262-bib-0101\", \"cobi14262-bib-0040\", \"cobi14262-bib-0223\", \"cobi14262-fig-0001\", \"cobi14262-bib-0211\"], \"section\": \"INTRODUCTION\", \"text\": \"Given our focus on elephants, rhinoceroses, pangolins, and lions, Figure\\u00a01 provides an overview of CITES\\u2010related trade\\u2010restrictive policy interventions and related indicative trends for these species from 1970 to 2020. Rhinoceroses and elephants drew attention as overexploited species for trade purposes early on (Martin, 1983; Somerville, 2016). More recently, pangolin species have similarly gained prominence (Heinrich et\\u00a0al., 2016), and there are growing concerns about possible trade impacts on African lions (Panthera leo) (Williams et\\u00a0al., 2017a). A surge in poaching and trafficking of these species in the late 2000s (Figure\\u00a01) (and the concomitant emergence of a new legal export trade of lion body parts from South Africa) prompted governments and nongovernmental organizations (NGOs) to take action, which included promoting and implementing further trade restrictions (\\u2019t Sas\\u2010Rolfes, 2017). These responses are ongoing, and wildlife trade (both illegal and legal), especially in the charismatic mammalian species, features as a controversial and fiercely debated issue on global conservation policy and research agendas. Although CITES provides an overall framework for regulating or restricting trade, governments have employed a range of additional restrictive or restriction\\u2010supportive policy measures throughout the trade chain, including law enforcement and efforts to reduce consumer demand through behavior change interventions.\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0208\", \"cobi14262-bib-0016\", \"cobi14262-bib-0216\"], \"section\": \"INTRODUCTION\", \"text\": \"With this in mind, we conducted a comprehensive and systematic review of scientific and gray literature to provide a clear and structured synthesis of the existing evidence on the impact and effectiveness of international wildlife trade restrictions for conservation in SADC countries from 1970 to 2020. The review purposefully excluded any developments during the COVID\\u201019 pandemic due to its unique and substantial influence on trade patterns, incomparable to the previous decades. Our results are based on a project funded by the U.S. Agency for International Development (USAID) with a broader focus (but limited to the specified iconic species), including measures aimed at indirectly influencing or controlling trade, such as resource rights regimes (\\u2019t Sas\\u2010Rolfes & Hiller, 2020). The review framework builds on earlier work that evaluated the conservation effectiveness of trade\\u2010related policy interventions at the global level (Cheng et\\u00a0al., 2017; UNEP, 2019) but concentrates more specifically on the impact of trade restrictions on the conservation of elephants, rhinoceroses, pangolins, and lions in SADC countries.\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0071\", \"cobi14262-bib-0027\", \"cobi14262-bib-0086\", \"cobi14262-bib-0100\"], \"section\": \"METHODS\", \"text\": \"We analyzed and synthesized the results of 46 studies that qualified as impact assessments of trade restrictions undertaken from 1970 to 2020 guided by the Preferred Reporting Items for Systematic Reviews and Meta\\u2010Analyses framework (PRISMA) (Moher et\\u00a0al., 2009). We selected the studies based on an analytical framework for evaluating wildlife trade restrictions on conservation outcomes and employed a rigorous review protocol, as described below and guided by previous relevant literature (Galvin et\\u00a0al., 2018; Partelow et\\u00a0al., 2017; Soliku & Schraml, 2018).\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-fig-0002\", \"cobi14262-bib-0212\", \"cobi14262-bib-0016\", \"cobi14262-bib-0216\"], \"section\": \"Analytical framework\", \"text\": \"We initially developed a basic analytical framework of influencing and outcome variables consistent with the review scope (Figure\\u00a02). The framework shows the influencing factors on the left of the diagram and the outcome variables on the right. The input factors were structured according to a simplified trade chain (\\u2019t Sas\\u2010Rolfes et\\u00a0al., 2019). We synthesized categories used in previous frameworks to account for relevant impact factors along these trade\\u2010chain dimensions (Cheng et\\u00a0al., 2017; UNEP, 2019).\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-tbl-0001\", \"cobi14262-supitem-0001\"], \"section\": \"Literature search and selection\", \"text\": \"Guided by the analytical framework, we conducted an extensive search on Web of Science (6 May 2020), Scopus (8 May 2020), and Google Scholar (19 May 2020). We used the Boolean search terms (Table\\u00a01), specifying geographical areas, animal species, and trade\\u2010restriction\\u2010related keywords. Our search further targeted specialist websites and databases during the specified time frame to account for relevant nonpeer\\u2010reviewed studies (i.e., gray literature, including reports of NGOs, government agencies, or other relevant institutions) (Appendix S1). Where appropriate, we applied a snowball approach during our screening process (i.e., using references of selected papers to find additional sources) and combined all search results into a single data set. Compared with peer\\u2010reviewed literature, it was impossible to conduct gray literature searches with the same rigor. Hence, our results might not represent all evidence\\u2010based data available at the point of the literature search.\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-fig-0003\", \"cobi14262-bib-0016\", \"cobi14262-bib-0008\"], \"section\": \"Literature search and selection\", \"text\": \"After implementing the search strategy and eliminating duplicates, all papers (originally 5667 without duplicates) were subjected to a multistep screening process, initially screening titles, then abstracts, and finally evaluating full publications (Figure\\u00a03). We excluded all articles unrelated to our study topic, outside the geographical location, ineligible publication types (e.g., editorials, commentaries, etc.), and papers not in English during the title\\u2010screening phase. During abstract screening, studies incompatible with the analytical framework were removed. Finally, we read the main texts and rejected all papers that did not qualify as evidence\\u2010based impact evaluations. We only included experimental and quasi\\u2010experimental studies that analyzed cause\\u2010and\\u2010effect relationships and considered confounding factors, along with qualitative studies that applied rigorous validity and reliability measures such as triangulation or intercoder reliability, in addition to systematic reviews and multiregression models testing the sensitivity of results to potential confounders. In other words, we excluded publications that did not examine the effects of at least one influencing factor on at least one outcome variable of the framework beyond monitoring approaches (Cheng et\\u00a0al., 2017) or exhibited no counterfactual thinking (Baylis et\\u00a0al., 2016). This screening process resulted in a total of 46 accepted studies.\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0012\", \"cobi14262-supitem-0001\", \"cobi14262-bib-0023\", \"cobi14262-bib-0078\", \"cobi14262-bib-0032\", \"cobi14262-bib-0045\", \"cobi14262-tbl-0002\", \"cobi14262-tbl-0003\", \"cobi14262-tbl-0004\"], \"section\": \"Data analyses\", \"text\": \"For data analyses and synthesis purposes based on qualitative thematic analysis (Braun & Clarke, 2006), we prepared a coding sheet and data extraction protocol (Appendix S2) and added relevant information to the data set in Microsoft Excel 2110 accordingly. We ascertained evidence\\u2010based research for each combination of influencing factors and outcome variables, resulting in clusters of studies for these combinations with reference to species and countries. We used open, manual coding to analyze this qualitative data inductively, inferring evidence for the impacts of influencing factors on outcome variables (Drury et\\u00a0al., 2011; Newing et\\u00a0al., 2011). We further synthesized the themes of findings and insights of the study clusters by grouping similar codes together to form themes (Gioia et\\u00a0al., 2013; Khan, 2014). The themes described particular levers or determinants wielding a specific effect on outcome variables. Based on these levers, we refined our synthesis through verbal discussions relating and contrasting the themed insights from the various studies, resulting in an organized overview of the existing research (Tables\\u00a02, 3, 4).\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0075\", \"cobi14262-bib-0092\"], \"section\": \"\", \"text\": \"Risk of uncontrolled meat poaching and human encroachment by rural communities due to loss in livelihood and human well\\u2010being in cases of longer\\u2010term restrictions (Mweetwa et\\u00a0al., 2018; Rosenblatt et\\u00a0al., 2014).\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0095\", \"cobi14262-bib-0030\", \"cobi14262-bib-0031\"], \"section\": \"\", \"text\": \"Elephant: Prohibition of elephant hunting in Botswana (introduced 2014): Poaching intensified significantly between 2014 and 2018 (Schlossberg et\\u00a0al., 2019).General: Hunting moratorium of 2014 in Botswana: Progressively antagonistic attitudes of towards wildlife of villagers of community\\u2010based natural resource management programs (CBNRM) and perceived rise of poaching levels (Gaodirelwe, Masunga, et\\u00a0al., 2020; Gaodirelwe, Motsholapheko, et\\u00a0al., 2020).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0009\"], \"section\": \"\", \"text\": \"Incentivizes hunters toward older trophies; reduced risk of hunting young, reproducing male lions; fewer trophies per annum overall (Begg et\\u00a0al., 2018).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0044\"], \"section\": \"\", \"text\": \"Stabilized elephant numbers in Luangwa Valley in Zambia (Jachmann & Billiouw, 1997).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0085\"], \"section\": \"\", \"text\": \"Lion: Reserves with the largest management budget: Highest lion populations (Packer et\\u00a0al., 2013).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0050\", \"cobi14262-bib-0051\"], \"section\": \"\", \"text\": \"Rhinoceros & Elephant: Small antipoaching field staff units in Zambia's Luangwa Valley (low manpower) and mild prison sentences for offenders: Unabated rhinoceros and elephant population declines due to illegal activity (1979\\u20131985); effective at capturing poachers, but ineffective at protecting the large elephant populations over the vast area (Leader\\u2010Williams, 1996; Leader\\u2010Williams et\\u00a0al., 1990).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0014\"], \"section\": \"\", \"text\": \"Elephant: Government effectiveness and human development: Impact on poaching levels measured as the Proportion of Illegally Killed Elephants (PIKE) at the country level (Burn et\\u00a0al., 2011).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0028\"], \"section\": \"\", \"text\": \"Elephant: Significant increases of law enforcement staff in Zimbabwe's Gonarezhou National Park between 2000 and 2010: Minimized illegal hunting, despite an expected increase in poaching due to the country's economic collapse (Gandiwa et\\u00a0al., 2013).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0062\"], \"section\": \"\", \"text\": \"Rhinoceros: Law enforcement efforts in the Lower Zambezi Valley in Zimbabwe: No apparent reduction in illegal activity with estimates that a 2% elephant population growth rate needs triple the field staff (Martin, 1993).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0068\"], \"section\": \"\", \"text\": \"Rhinoceros: Rapid response measures: identified as a suitable means to recover rhinoceros horns (Milledge, 2007).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0021\"], \"section\": \"\", \"text\": \"Rhinoceros: Generalized linear model factors (i) GDP per capita in Far East Asia, (ii) fine upon conviction, and (iii) antipoaching efforts most sensitive predictors of: Rhinoceros poaching levels in South Africa, emphasizing suitable law enforcement measures as vital to curb rhinoceros poaching under increasing wealth scenarios in the Far East (Di Minin et\\u00a0al., 2015).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0002\"], \"section\": \"\", \"text\": \"Rhinoceros: Focus on leadership and intelligence, with sufficient funding most influential for: low rhinoceros poaching levels in a Zimbabwean reserve, largely due to highly committed, loyal, and long\\u2010term staff workforce limiting the access of poachers to inside knowledge of security systems and flipping antipoaching activities from reactive to proactive (Ball et\\u00a0al., 2018).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0054\"], \"section\": \"\", \"text\": \"General: Increased capacity and capability of well\\u2010paid law enforcement village scouts with superior knowledge of the surrounding area in Zambia's Lupande Game Management Area: Dramatic increases in arrests and firearm confiscations; more protective attitude of villagers for wildlife (Lewis et\\u00a0al., 1990).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0098\"], \"section\": \"\", \"text\": \"General: First 10\\u00a0days of patrol periods of patrol teams: Most effective for encountering illegal activities and making arrests (Siamundaala et\\u00a0al., 2009).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0052\", \"cobi14262-bib-0070\"], \"section\": \"\", \"text\": \"Elephant/Rhinoceros: Strong law enforcement more effective than variable or fixed penalties according to an economic model on black rhinoceroses and elephants in Zambia's Luangwa Valley (1979\\u20131985) to deter organized crime gangs because potential penalties for poaching would need to be raised exponentially to counter the vast gains, including a shoot\\u2010to\\u2010kill policy to constitute an effective deterrent (Leader\\u2010Williams & Milner\\u2010Gulland, 1993; Milner\\u2010Gulland & Leader\\u2010Williams, 1992).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0060\"], \"section\": \"\", \"text\": \"Elephant: The probability of interception strikingly more effective than lowering black market ivory prices according to a bioeconomic model to: reduce the planned number of poaching expeditions (Lopes, 2015).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0097\"], \"section\": \"\", \"text\": \"Pangolin: Stark increase in the number of confiscated ground pangolins (Smutsia temminckii) in Zimbabwe (2010\\u20132015) combined with severe penalties: pangolins taken from the wild for the black market limited (Shepherd et\\u00a0al., 2017).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0067\"], \"section\": \"\", \"text\": \"General: Dramatic increase of poaching costs (willingness to implement shoot poachers on sight policies) according to an economic model of poaching constitutes: The only way to protect endangered species when nonpoaching wages are low and the economic benefits of poaching are high (Messer, 2010).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0047\"], \"section\": \"\", \"text\": \"General: Law enforcement/park ranger presence, dangerous wildlife and fines in Tanzania: Negligible probabilities of any harm (fines or injury) when hunting illegally; perceived higher number of hours a poacher needs to remain concealed to avoid detection (Knapp, 2012).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0072\"], \"section\": \"\", \"text\": \"Elephant: Based on DNA\\u2010matching technology poaching affects: the social structure of elephant populations (Mondol et\\u00a0al., 2014).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0038\", \"cobi14262-bib-0011\", \"cobi14262-bib-0074\", \"cobi14262-bib-0099\"], \"section\": \"\", \"text\": \"General: New technologies such as thermal imaging (Hart et\\u00a0al., 2015), remotely piloted aircraft systems fitted with cameras, AI\\u2010based applications (Bondi et\\u00a0al., 2018; Mulero\\u2010P\\u00e1zm\\u00e1ny et\\u00a0al., 2014), and GIS and remote sensing to monitor poaching activities (Sibanda et\\u00a0al., 2016) suggest: Advanced poaching detection rates under experimental conditions.\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0039\"], \"section\": \"\", \"text\": \"Elephant: Continued investment in law enforcement needs to be combined with interventions targeting ivory demand reduction, corruption, and poverty alleviation to: reduce elephant poaching (Hauenstein et\\u00a0al., 2019).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0018\"], \"section\": \"\", \"text\": \"Elephant: Levels of regional legal protection and other factors, in particular human access, the corruption perception index, and ecosystem type being affected: elephant poaching levels (CITES Secretariat, 2007).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0004\"], \"section\": \"\", \"text\": \"Rhinoceros: Insufficient or complicit law enforcement in South Africa attributed to explain: higher levels of patrol efforts around poaching hotspots before rhinoceros poaching incidents, that is, field rangers were at the right place, but at the wrong time, suggesting that even high presence in a poaching area does not deter organized rhinoceros poaching gangs (Barichievy et\\u00a0al., 2017).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0006\", \"cobi14262-bib-0026\"], \"section\": \"\", \"text\": \"General: Regular monitoring of animal populations to: identify poaching hotspots and worrying trends as a crucial element for law enforcement success (Bauer et\\u00a0al., 2015; Ferreira et\\u00a0al., 2017).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0017\"], \"section\": \"\", \"text\": \"Horns increasingly evading law and enforcement reaching illegal markets (from 2001) (Cheteni, 2014).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0025\", \"cobi14262-bib-0308\"], \"section\": \"\", \"text\": \"\\nRhinoceros: CITES Appendix 1 Listing followed by additional legal restrictions in South Africa: escalation of illegally killed rhinoceroses from 2007 despite substantial supporting law enforcement efforts (Emslie et\\u00a0al., 2016; Ferreira et\\u00a0al., 2018).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0015\"], \"section\": \"\", \"text\": \"\\nPangolin: Immediate onset of CITES imposed zero\\u2010quota policy in 2000: a spike in pangolin trade in Asia; a clear transfer of the preban trade volume to illicit markets (Challender et\\u00a0al., 2015).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0223\"], \"section\": \"\", \"text\": \"\\nLion: Anticipated restrictive (zero) export quota for lion products, imposed at CITES CoP17: surge in legal exports of lion skeletons from South Africa in 2016 and rising concerns of emerging black markets for lion products (Williams et\\u00a0al., 2017a).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0228\"], \"section\": \"\", \"text\": \"\\nElephant: restricted ivory supply due to CITES Appendix I listing (1989) compounded by Chinese ivory trafficking interception measures (2011\\u20132012): quick rise of illegal ivory prices accelerating elephant poaching rates (Zhou et\\u00a0al., 2018).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0102\", \"cobi14262-bib-0228\", \"cobi14262-bib-0102\", \"cobi14262-bib-0215\"], \"section\": \"\", \"text\": \"Short\\u2010term reduction of poaching pressure on many populations (Stiles, 2004; Zhou et\\u00a0al., 2018); however, persistent poaching increasing markedly from 1998 in countries with widespread corruption, civil unrest, or poor wildlife management, leading to further declining elephant numbers, particularly in West and Central Africa (Stiles 2004; Underwood et\\u00a0al., 2013).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0053\"], \"section\": \"\", \"text\": \"Elephant: CITES ivory ban: reversing overall decline of African elephant numbers between 1989 and 2007, except in countries with unregulated postban ivory markets (Lemieux & Clark, 2009).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0034\"], \"section\": \"\", \"text\": \"\\nRhinoceros: Social network analyses for trafficking network close to Kruger National Park: Crucial element to disrupt transnational trafficking networks effectively (Haas & Ferreira, 2015).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0043\"], \"section\": \"\", \"text\": \"\\nRhinoceros: Lack of coordinated intelligence activities and inadequate legislation for prosecution: organized crime dealers and kingpins favor efficiency over security, as the risks of being caught and prosecuted are minimal, and security plans for crime syndicate members and their families exist (H\\u00fcbschle, 2017).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0201\"], \"section\": \"\", \"text\": \"General: Antihunting regulations in Namibia and Mozambique: negative attitudes of most study participants due to wide\\u2010ranging negative effects on their well\\u2010being (food, assets, direct income [from illegal rhinoceros hunting]) (Strong & Silva, 2020).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0030\", \"cobi14262-bib-0309\"], \"section\": \"\", \"text\": \"General: hunting moratorium of 2014 in Botswana: negative effects on household well\\u2010being due to increased crop\\u2010raiding and predation, job losses, and decline in income (Gaodirelwe, Masunga, et\\u00a0al., 2020; Mbaiwa, 2018).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0220\"], \"section\": \"\", \"text\": \"General: Zambian hunting moratorium (2013\\u20132014): adverse livelihood and well\\u2010being effects in already poverty\\u2010stricken areas due to lost meat and (seasonal) income possibilities through sport hunting (White & Belant, 2015).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0205\"], \"section\": \"\", \"text\": \"General: Restrictive hunting legislation in Botswana: unwillingness of the Basarwa to submit to external controls over wildlife use and hunting, as wildlife is part of Basarwa's diet due its association with their heritage (Taylor, 2007).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0043\"], \"section\": \"\", \"text\": \"pros for local people: (financial) security, indirect benefits like basic roads, water wells, and so forth from rhinoceros poachers and kingpins, whereas the state and private/public partnerships have failed in achieving tangible benefits and a sense of security; (ii) cons especially for women: impaired social fabric of village life and cause for fear of losing relatives through law enforcement (H\\u00fcbschle, 2017).\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0218\", \"cobi14262-bib-0227\"], \"section\": \"\", \"text\": \"Poor community members (i) dislike poachers due to perceived threat to the community's social security and (ii) struggle with enforcement officials due to perceived antipoor enforcement of conservation\\u2010prone, restrictive policies for protected area, despite a generally positive attitude toward the protected area (Vundla, 2019).Rhinoceros: Militarization of antipoaching in Mozambique's Limpopo National Park: villagers fear further violent antipoaching tactics of park officials and rhinoceros poachers, such as burning houses of villagers rightly or wrongly associated with poaching; villagers suspect reenvisioned resettlement strategy to achieve conservation outcomes (Witter & Satterfield, 2019).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0102\"], \"section\": \"\", \"text\": \"Effective anti\\u2010ivory campaigns in conjunction with the ivory trade ban in 1989 are associated with stigmatizing buying or possessing ivory in America, Europe, and Japan, reportedly reducing demand in these countries, resulting in smaller postban ivory markets throughout Africa, except for Nigeria (Stiles, 2004).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0048\"], \"section\": \"\", \"text\": \"Thailand limiting domestic ivory trade exclusively to products coming from registered captive Asian Elephants (Elephas maximus) in 2015 while banning the import, export, and trade in African Elephants (Loxodonta africana) resulted in a significant reduction of legal ivory trade in Bangkok, inferred from a downward trend in the number of shops selling ivory and the number of traded ivory products (Krishnasamy et\\u00a0al., 2016).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0228\"], \"section\": \"\", \"text\": \"Powerful campaigns of the Chinese government using Radio, Film, and Television showed effects in reducing extravagant consumption and developing negative attitudes toward buying ivory products of the younger generation, while the campaigns are thought to have contributed to a drop in the price of illegal ivory (Zhou et\\u00a0al., 2018).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0066\"], \"section\": \"\", \"text\": \"\\u2010 A pre\\u2010 and postban survey in Chinese cities related to China's shutdown of all licensed ivory carving factories and retailers at the end of December 2017 indicated both a significantly grown proportion of ivory rejectors and a decline in ivory purchases, despite a persistent residuum of \\u201cDiehard Buyers\\u201d indicating that demand might not be completely preventable (Meijer et\\u00a0al., 2018).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0021\"], \"section\": \"\", \"text\": \"\\u2010 A generalized linear model of rhinoceros poaching in South Africa suggests that in addition to increasing antipoaching efforts and monetary fines upon conviction, governance improvements in Vietnam would be crucial to maintaining rhinoceros populations by helping to reduce poaching (Di Minin et\\u00a0al., 2015).\\n\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-fig-0004\", \"cobi14262-supitem-0001\"], \"section\": \"RESULTS\", \"text\": \"The literature search and systematic review yielded 46 wildlife trade\\u2010related impact studies relevant to the SADC region, focusing on the highlighted species. We found a strong focus on impact studies investigating supply\\u2010side and transaction\\u2010chain wildlife trade measures as input variables and the effects of monitoring and enforcing these measures as output variables (Figure\\u00a04) (references to corresponding studies with emergent thematic clusters in Appendices S3\\u2013S7).\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-fig-0004\", \"cobi14262-fig-0004\"], \"section\": \"RESULTS\", \"text\": \"The following main research areas emerged (Figure\\u00a04): law enforcement measures impacting human behavior (especially illegal hunting) or human attitudes toward wildlife crimes, particularly among rural communities (n\\u00a0=\\u00a020); the effects of law enforcement on wildlife conservation outcomes at the species or population level (n\\u00a0=\\u00a06); and the impact of international trade restrictions (in the form of CITES Appendix I listings) on wildlife conservation outcomes (n\\u00a0=\\u00a06). Furthermore, some research was conducted on the impact of legal supply restriction measures (including laws, policies, and regulations for spatial or species\\u2010related constraints, such as quotas) on wildlife conservation (n\\u00a0=\\u00a07) and rural livelihoods (n\\u00a0=\\u00a03) and of demand\\u2010side measures on conservation\\u2010related behavior or attitudes (n\\u00a0=\\u00a05) (Figure\\u00a04).\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-fig-0004\", \"cobi14262-fig-0004\"], \"section\": \"RESULTS\", \"text\": \"The effects of the identification and disruption of actor networks and demand\\u2010side measures were underresearched (Figure\\u00a04). Furthermore, none of the identified studies evaluated the impact of demand\\u2010side legal measures to reduce the purchase, consumption, and possession of wild animals or wildlife products domestically (i.e., in SADC range states). However, few studies assessed the effectiveness of demand\\u2010related restrictions in the target consumer countries, mainly in Southeast Asia. Further apparent gaps included a lack of research on the socioeconomic impacts of wildlife trade restrictions on rural livelihoods and national economies (Figure\\u00a04).\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-tbl-0002\", \"cobi14262-tbl-0003\", \"cobi14262-tbl-0004\"], \"section\": \"RESULTS\", \"text\": \"The following subsections summarize the themes emerging from our qualitative analysis of the identified impact studies (detailed thematic analysis in Tables\\u00a02, 3, 4). For the areas with the most obvious research gaps highlighted above, we briefly discuss the existing insights and evidence in the final 2 subsections (i.e., impact studies on rural livelihoods, well\\u2010being, and national economies and insights into demand reduction for wildlife products of SADC origin).\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-tbl-0002\", \"cobi14262-tbl-0002\"], \"section\": \"Impacts of international trade restrictions and related measures on reducing threats to species\", \"text\": \"International trade restrictions tend to be guided by CITES listings and include measures such as restrictions on cross\\u2010border trade for primarily commercial purposes, permitting requirements, and quotas. Our qualitative analysis generated 4 themes in relation to international trade regulations. All themes relate to the effectiveness of CITES trade bans (i.e., Appendix I listings) (Table\\u00a02, T\\u2010C1\\u2013T\\u2010C4). (Theme codes in parentheses here in \\u201cResults\\u201d refer to summarized conservation\\u2010related research findings in Table\\u00a02.) The themes highlighted the ambiguity and uncertainty of the effectiveness of such measures for wildlife conservation. The results of the few existing impact evaluations varied considerably in their assessment of the ecological, human behavioral, and economic effects at the macro level. This substantially compromised our ability to infer direct links relating to the impact of international\\u2010level regulations.\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-tbl-0001\", \"cobi14262-bib-0019\", \"cobi14262-bib-0013\"], \"section\": \"Impacts of international trade restrictions and related measures on reducing threats to species\", \"text\": \"Impact studies on rhinoceros and pangolin species as well as on lions confirmed concerns that some international trade bans may simply drive markets underground instead of exerting a discernible positive influence on species populations (theme code T\\u2010C1 [Table\\u00a01]) (Conrad, 2012). Furthermore, evidence\\u2010based research on African elephants suggested that unregulated markets, widespread corruption, civil unrest, or poor wildlife management increase the likelihood of rendering trade bans ineffective (T\\u2010C2). These findings need to be considered in the light that some countries might rather need to address an elephant overpopulation challenge. An early economic model based on data from Zambia reflected that optimal elephant stock was consistently lower than the estimates of elephant populations for both trade\\u2010 and no\\u2010trade scenarios, suggesting that such countries might need to reduce those levels actively (through culling) or passively (through underinvestment in protection) (Bulte & van Kooten, 1999).\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0055\", \"cobi14262-bib-0073\", \"cobi14262-bib-0206\", \"cobi14262-bib-0041\", \"cobi14262-bib-0046\"], \"section\": \"Impacts of international trade restrictions and related measures on reducing threats to species\", \"text\": \"We found examples of short\\u2010term trade bans benefitting conservation in conjunction with further conditions (T\\u2010C3). However, we noted a persistent debate over the role of post\\u2010ban efforts to enable subsequent use and trade, based on cases lauded as trade\\u2010ban successes, notably crocodilians (Crocodilia) and the vicu\\u0148a (Vicugna vicugna), for which CITES coupled strict trade restrictions with efforts to support nations in establishing sustainable use programs (Lichtenstein, 2010; Moyle, 2013; Thorbjarnarson, 1999). One theoretical model suggested a trade ban was likely to positively affect elephant populations if it achieved the following: a widespread moral demand\\u2010reducing effect; improved interception of smuggled products; limited increases of ivory stockpiles from official production; and no reduction in law enforcement efforts (Heltberg, 2001). Another theoretical model indicated that a successful trade ban would need to deal effectively with the so\\u2010called free\\u2010rider problem, whereby nations placing a high existence value on elephants without actively investing in their survival are classified as free riders (Khanna & Harford, 1996). The authors argue that an international transfer payment mechanism would support conservation strategies in the producer countries.\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0042\", \"cobi14262-bib-0034\", \"cobi14262-bib-0077\", \"cobi14262-bib-0069\", \"cobi14262-bib-0043\", \"cobi14262-bib-0077\"], \"section\": \"Impacts of international trade restrictions and related measures on reducing threats to species\", \"text\": \"Intelligence\\u2010led, proactive interruption and inhibition of illegal hunting activities were regularly emphasized as measures to render international trade restrictions effective (H\\u00fcbschle, 2016). However, corresponding evidence\\u2010based impact studies were few. The only emerging theme from the qualitative analysis was a lack of collaborative approaches across jurisdictions (T\\u2010C4). As a result, very few large\\u2010scale seizures prompted successful investigations or arrests and almost no convictions. Research suggested that failure to disrupt criminal networks more effectively may result from missing federated criminal evidence data and trust as a basis for legal prosecuting provisions between different jurisdictions (Haas & Ferreira, 2015; Nanima, 2019); a lack of complements, such as scanners, X\\u2010ray devices, sniffer dogs, and so forth (Milliken, 2014); a lack of coordinated intelligence activities; and inadequate legislation to prosecute individuals (H\\u00fcbschle, 2017; Nanima, 2019).\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-tbl-0002\"], \"section\": \"Impacts of domestic trade restrictions on reducing threats to species\", \"text\": \"Studies investigating the impact of domestic laws, policies, and regulations to restrict wildlife harvesting and supply on wildlife conservation outcomes elicited 3 synthesized themes (Table\\u00a02, S\\u2010C1\\u2013S\\u2010C3). Wildlife hunting bans, moratoria, and quotas constituted the typical domestic restriction measures in the identified impact studies. Studies of hunting prohibitions on lions and elephants suggested that these measures only benefited strained animal populations in the short term (S\\u2010C1). The associated loss of livelihood and human well\\u2010being for rural communities during the hunting suspension led to uncontrolled meat poaching and human encroachment and an even greater risk for wild animal populations in the longer term. A second theme indicated detrimental consequences for social animal structures, such as elephants, when hunting quotas across national borders were uncoordinated (S\\u2010C2). Another theme suggested that restrictions were more effective at modulating human behavior in favor of wildlife conservation when framed as permissions rather than prohibitions (S\\u2010C3).\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-fig-0002\", \"cobi14262-tbl-0002\"], \"section\": \"Impacts of domestic monitoring and enforcement on reducing threats to species\", \"text\": \"Most evidence\\u2010based research on dedicated trade\\u2010restriction measures examined the impact of efforts to monitor and enforce trade\\u2010restrictive laws, policies, and regulations on conservation\\u2010related outcomes (Figure\\u00a02). Studies on measures such as patrol efforts, sentencing strategies, or intelligence elicited 5 corresponding themes (Table\\u00a02, S\\u2010C4\\u2013S\\u2010C8).\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0059\", \"cobi14262-bib-0068\"], \"section\": \"Impacts of domestic monitoring and enforcement on reducing threats to species\", \"text\": \"Numerous studies suggested that sufficient high\\u2010quality and proactive law enforcement efforts are beneficial for wildlife conservation, both directly (on species or population level) and indirectly (on human behavior level) (S\\u2010C4). In other words, impact studies showed positive effects of law enforcement measures to combat wildlife crime or achieve species conservation when these efforts were well\\u2010resourced both quantitatively, in terms of human and financial capacities, and qualitatively, in terms of the capabilities of field rangers and leadership, even in cases when illegal hunting and fishing soared in countries experiencing economic hardship, such as in Zimbabwe after its economic collapse (Lindsey et\\u00a0al., 2011). Approaching monitoring and enforcement in a proactive rather than a reactive way (i.e., a shift from patrolling efforts to intelligence\\u2010based approaches) was also found to positively influence conservation outcomes. Conversely, this theme included findings that poaching remained a constant and severe problem in cases of insufficient or incapable resources (S\\u2010C4). The effectiveness of law enforcement efforts was sometimes measured in terms of discovering illegal activities ex post when the lives of targeted animals had already been lost, such as in Milledge (2007) who reported a 42% rhinoceros horn recovery rate through measures ranging from rapid response in protected areas to investigations and confiscations in urban centers in 9 African countries.\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0080\", \"cobi14262-fig-0002\", \"cobi14262-bib-0089\"], \"section\": \"Impacts of domestic monitoring and enforcement on reducing threats to species\", \"text\": \"The research also showed that effective law enforcement hinges more on detection risk than on harm or loss (S\\u2010C5). In other words, although measures to increase detection risk, such as patrol efforts, showed positive impacts on conservation outcomes, the potential harm or loss in case of detection (through prison sentences, fines, or other forms of financial loss) did not constitute a comparable deterrent, unless such penalties were raised to extreme levels, such as a shoot\\u2010on\\u2010sight policy for poachers. Furthermore, large\\u2010scale prosecutions for wildlife crimes tended to be rare globally (Nowell, 2012). A third theme emerged, suggesting that new technologies show promise to enhance detection risk for illegal hunters (S\\u2010C6). However, evidence\\u2010based studies investigating the impact of these technological developments on conservation outcomes were rare (Figure\\u00a02). Most relevant studies were confined to field tests of various tech solutions under experimental conditions (Pimm et\\u00a0al., 2015).\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0043\"], \"section\": \"Impacts of domestic monitoring and enforcement on reducing threats to species\", \"text\": \"Several authors argued that measures to change human behavior and attitudes for wildlife conservation purposes must couple law enforcement measures with other efforts to mitigate negative consequences for socioeconomic development (S\\u2010C7). The identified impact studies suggested that such measures might need to address consumer demand, corruption, and poverty and be supplemented by regular monitoring of animal populations. The final theme linked the effectiveness of law enforcement to nonmarket\\u2010related social constructs of a society's relationship with an animal species (S\\u2010C8). Evidence\\u2010based investigations highlighted the significance of social legitimacy factors in supporting or undermining domestic law enforcement efforts (H\\u00fcbschle, 2017).\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-tbl-0003\", \"cobi14262-fig-0002\"], \"section\": \"Impact of trade restrictions on socioeconomic development (rural livelihoods and national economies)\", \"text\": \"The synthesized themes relating to this topic are summarized in Table\\u00a03 (with theme codes appearing below in parentheses). We found evidence\\u2010based impact studies of restrictive measures along the trade chain on socioeconomic development outcome variables were sparse in comparison with conservation\\u2010related outcomes (Figure\\u00a02). Consequently, the qualitative thematic analysis of findings was limited to a small number of studies, even though such impacts could plausibly be significant and lead to adverse secondary conservation outcomes.\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0076\", \"cobi14262-bib-0225\"], \"section\": \"Impact of trade restrictions on socioeconomic development (rural livelihoods and national economies)\", \"text\": \"Our analyses elicited the potential of trade bans to significantly harm wildlife economies as the only theme for the socioeconomic impact of international trade restrictions (T\\u2010SE1). Any effects of measures restricting trade activities on rural livelihoods were researched on a domestic level. Domestically, hunting restrictions overwhelmingly demonstrated adverse impacts on rural livelihoods and well\\u2010being (S\\u2010SE1). Imposed costs included lost food sources, assets, jobs, or other forms of income, thereby aggravating already poverty\\u2010stricken areas. This theme was supported by other research emphasizing the complementary benefits of both tourism and hunting for rural communities in Namibia because the benefits occurred at different times, appeared in different places, and reached different sections of local communities (Naidoo et\\u00a0al., 2016). Similarly, a survey on the effects of the US suspension on imports of captive lion trophies from South Africa highlighted alleged job losses in rural areas, thereby indicating the impact of trade restrictive measures on livelihood outcomes (Williams & \\u2019t Sas\\u2010Rolfes, 2019).\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0063\"], \"section\": \"Impact of trade restrictions on socioeconomic development (rural livelihoods and national economies)\", \"text\": \"In addition to material hardship, researchers identified how law enforcement measures can result in other detriments for rural communities, such as a loss of the social fabric in a village (S\\u2010SE2). The studies in this theme highlighted how rural communities experience both benefits and costs through illegal hunting, especially when the state failed to deliver basic public services in poverty\\u2010stricken areas (S\\u2010SE2). However, this research also highlighted the ambiguous relationships of rural communities with poachers and law enforcement officers. Although poachers can be seen to threaten secure village life, there was also evidence of adverse treatment of villagers by law enforcement staff and associated fear of violent antipoaching tactics, despite the fact that entire villages are not necessarily involved in or complicit with illegal hunting of high\\u2010value species. In their most extreme form, conservation\\u2010related enforcement measures were reportedly used as a means for renewed dispossession and displacement of rural communities (Mass\\u00e9 & Lunstrum, 2016).\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-fig-0002\", \"cobi14262-tbl-0004\", \"cobi14262-bib-0210\"], \"section\": \"Consumer demand reduction\", \"text\": \"Our review did not elicit evidence\\u2010based research studies assessing direct links between demand\\u2010side measures to restrict trade\\u2010related activities and their effect on wildlife conservation or socioeconomic development in SADC range states (Figure\\u00a02; Table\\u00a04). Reductions in consumer demand were often presented as a proxy outcome variable to infer themes for reduced threats to species by means of legal measures to restrict activities along the trade chain. However, consumer demand reduction as an outcome variable was challenging to ascertain, partly because illegal purchases and consumption are clandestine and partly because demand is multidimensional and difficult to measure by a single attribute. Both sale volumes (quantities of goods sold per unit of time) and product prices would be relevant, especially the latter. Due to the ambiguity of the net effects of declining volumes accompanied by increasing prices, depending on the price elasticity of demand (\\u2019t Sas\\u2010Rolfes, 2012), the only certain measure of declining demand would have been a confirmed simultaneous decline in both consumer sales volumes and prices.\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0015\", \"cobi14262-bib-0029\", \"cobi14262-bib-0210\"], \"section\": \"Consumer demand reduction\", \"text\": \"Coupling law enforcement with consumer\\u2010targeted government campaigns emerged as the one theme to enhance the potential of reducing demand in consumer countries (with a focus on ivory) (D\\u2010D1). The relevant studies emphasized the potency of combining trade bans with enforcement measures and consumer campaigns to stigmatize the purchase or possession of ivory to effectively reduce demand. However, some researchers suggested that media campaigns and changing fashion alone provide a plausible alternative explanation for reversing the decline in Africa's elephant population (Challender et\\u00a0al., 2015). Overall, the full impact of regulatory interventions in China in late 2011 remained somewhat unclear (Gao & Clark, 2014), as did Vietnam's penal code revisions. The evidence for successful demand reduction of other relevant species products was less compelling. Although the domestic trade restrictions in Asian rhinoceros horn consumer countries in the early 1990s are believed to have been effective, the subsequent obvious surge in East Asian consumer prices in the early 21st century suggested that the effects were, in part, only temporary (\\u2019t Sas\\u2010Rolfes, 2012).\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0020\", \"cobi14262-bib-0081\", \"cobi14262-bib-0082\", \"cobi14262-bib-0217\", \"cobi14262-bib-0216\"], \"section\": \"Consumer demand reduction\", \"text\": \"To support regulation, NGOs made attempts at voluntary consumer demand reduction. These attempts applied a range of techniques, from public awareness campaigns and celebrity endorsements to more targeted social marketing techniques. Independent assessments of these attempts pointed to various and significant shortcomings (Dang Vu et\\u00a0al., 2020; Olmedo et\\u00a0al., 2020, 2018; Ver\\u00edssimo & Wan, 2019), and their ultimate impact to date remains uncertain. There have been relatively few demand reduction interventions grounded in appropriately structured consumer research guided by behavioral science and even fewer robust impact evaluations of such interventions (UNEP, 2019).\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0212\", \"cobi14262-bib-0003\", \"cobi14262-bib-0226\"], \"section\": \"DISCUSSION\", \"text\": \"The role of trade in relation to other factors driving wildlife species decline remains a somewhat uncertain and contested issue. The relatively low number (46) of studies that constituted acceptable evidence\\u2010based evaluations related to this question was striking. Although wildlife trade has recently gained further significant prominence as both a perceived threat and a catalyst for conservation activism (\\u2019t Sas\\u2010Rolfes et\\u00a0al., 2019), many assessments of species decline pointed to habitat loss and fragmentation as the most salient long\\u2010term drivers. At the time of the 1989 CITES ivory trade ban, economists contemplated whether it would serve as a long\\u2010term solution for African elephant conservation and concluded that it would not (Barbier et\\u00a0al., 1990). Around the same time, Wilson (1989) highlighted the main factor driving 20th\\u2010century biodiversity loss as anthropogenic habitat destruction, fueled by the rapid growth of the global human population and associated economic activity.\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0202\"], \"section\": \"DISCUSSION\", \"text\": \"In a subsequent analysis, Swanson (1994) argued that trade restrictions are most appropriate for genuine open\\u2010access resources (e.g., marine species) because they provide a deterrent effect to slow down the rate of harvesting. However, for terrestrial species that occupy land with other potential uses and require the active investment of resources to manage and protect them, the associated opportunity costs with trade restrictions can undermine the long\\u2010term economic case for conserving such species. If illegal consumer markets for their harvested products persist, they become increasingly costly to protect from commercial poaching. They may eventually be viewed as economic liabilities rather than assets, especially in the case of species that pose potential threats to the lives and livelihoods of local people. In such instances, reestablishing controlled and sustainably supplied legal trading regimes may be a better long\\u2010term option to ensure species persistence.\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0203\", \"cobi14262-bib-0064\", \"cobi14262-bib-0207\"], \"section\": \"DISCUSSION\", \"text\": \"Following a broader dialogue with inputs from both ecologists and economists, Swanson (1995) noted deep ideological differences over whether biodiversity conservation is best achieved through shielding nature from human development or through human development, which may also influence the perceptions of both relative threats to wildlife and the most appropriate measures to address these. Such differing emphases were reflected in recent global assessments of species threats. For example, one claimed that overexploitation is the most prevalent threat currently facing species (Maxwell et\\u00a0al., 2016), whereas another identified habitat loss as the more salient factor (Tilman et\\u00a0al., 2017). Nevertheless, it is notable that of the 11 categories of the IUCN Red List's current threat classification system, only 2\\u2014biological resource use and spread of invasive and problem species, pathogens, and genes\\u2014are (indirectly) associated with wildlife trade.\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0024\", \"cobi14262-bib-0025\", \"cobi14262-bib-0079\", \"cobi14262-bib-0087\", \"cobi14262-bib-0033\", \"cobi14262-bib-0007\"], \"section\": \"DISCUSSION\", \"text\": \"The IUCN Red List assessments identified illegal harvesting for international trade as the central threat to the 2 rhinoceros species (Emslie, 2020; Emslie et\\u00a0al., 2016) and a growing threat to pangolins, which are also harvested for domestic consumption and trade and threatened by habitat loss (Nixon et\\u00a0al., 2019; Pietersen et\\u00a0al., 2019). However, the African elephant assessment emphasized that although illegal hunting for ivory and meat remains a key factor in specific areas, the most important perceived threat is habitat loss and fragmentation, aggravated by increasing human\\u2013elephant conflict (Gobush et\\u00a0al., 2021). The lion assessment listed indiscriminate killing and prey depletion, accompanied by habitat loss and fragmentation, as key factors, with a minor role of poorly managed trophy hunting in some instances (Bauer et\\u00a0al., 2016). It noted only a small role for domestic trade and some concern over a potential future international trade in lion body parts.\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0035\", \"cobi14262-bib-0090\"], \"section\": \"DISCUSSION\", \"text\": \"Our review results indicated that CITES listings, when viewed as a stand\\u2010alone measure, offered limited protection to these species, constrained by varying perceptions of social legitimacy among market actors and with potentially even detrimental conservation and socioeconomic outcomes. Announcements of unconditional or wide\\u2010ranging trade restrictions, such as export or import bans, might even abruptly increase species threats by signaling scarcity in the marketplace, resulting in higher prices and increased incentives for illegal activity, which may persist (Hall et\\u00a0al., 2008; Rivalan et\\u00a0al., 2007). Our results suggested that, to be effective, CITES listings must be supported by a fully aligned range of appropriate measures in range, transit, and consumer countries. The CITES trade restrictions for rhinoceros, elephant, pangolin, and lion alike supported this insight that stand\\u2010alone Appendix I listings tend to be ineffective in the longer term.\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0213\"], \"section\": \"DISCUSSION\", \"text\": \"The 1977 CITES Appendix I rhinoceros listings failed to prevent the further poaching and decline of Africa's black rhinoceros. At the continental level, populations only started to recover after 4 key Asian consumer countries agreed to take measures to outlaw their domestic markets in 1993, following direct diplomatic pressure from the United States. Even so, under complete ban conditions, rhinoceros poaching resurged significantly from 2007 onward, not only slowing and threatening the recovery of black rhinoceros populations but also starting to reverse the previously impressive southern white rhinoceros (Ceratotherium simum simum) recovery. Uninterrupted since the 1960s, the latter recovery took place with the support of some legal trade measures for live animals and hunting trophies (\\u2019t Sas\\u2010Rolfes et\\u00a0al., 2022). Importantly, the Appendix I listings also failed to prevent the loss of 2 subspecies, the northern white rhinoceros (Ceratotherium simum cottoni) and the northwestern black rhinoceros (Diceros bicornis longipes) (neither of which occurred in the SADC region).\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0044\", \"cobi14262-bib-0214\", \"cobi14262-bib-0049\", \"cobi14262-bib-0022\", \"cobi14262-bib-0094\"], \"section\": \"DISCUSSION\", \"text\": \"Despite a reasonable body of research on the topic, the role of CITES in protecting African elephants continues to be disputed. Although it is widely agreed that the 1989 Appendix I listing suppressed key consumer markets and slowed the rate of poaching at the time, it is also clear that the subsequent benefits of the ivory ban under the CITES regime have been unevenly distributed and that local law enforcement efforts remain critical (Jachmann & Billiouw, 1997). Certain countries with adequately protected and sizable populations carry a disproportionately high burden in the form of management and opportunity costs. Attempts to address this imbalance by way of split listing (i.e., downlisting populations of well\\u2010performing countries to Appendix II and then allowing one\\u2010off ivory sales) have created confusion and tension. Critics blamed these on resurgent consumer demand in the early 21st century (\\u2019t Sas\\u2010Rolfes et\\u00a0al., 2014). As a result, no further sales are currently contemplated, and ivory trade policy continues to be fiercely debated. However, recent analyses confirmed the importance of other domestic factors (e.g., poverty and corruption) in influencing elephant conservation performance (Kuiper et\\u00a0al., 2023). Furthermore, a comprehensive study of historical ivory prices (Do et\\u00a0al., 2021) suggested that elephant poaching is relatively inelastic. This implies that the overall effect of the CITES ban itself is relatively neutral, neither encouraging nor discouraging poaching significantly. This result appears to be supported by another recent study that showed fairly persistent poaching levels, especially in the southern African region (Schlossberg et\\u00a0al., 2020).\"}, {\"pmc\": \"PMC11780195\", \"pmid\": \"38578131\", \"reference_ids\": [\"cobi14262-bib-0058\", \"cobi14262-bib-0065\"], \"section\": \"DISCUSSION\", \"text\": \"The socioeconomic impacts of CITES listings at national and, especially, local community levels were inadequately researched, and the opportunity costs imposed on the countries with good conservation track records that oppose them are potentially substantial. This is a cause for concern, especially given the current lack of long\\u2010term vision for elephant ivory and rhinoceros horn trade. Both will continue to accumulate in collected stockpiles as long as populations of elephants and rhinoceroses continue to survive and naturally produce these harvestable and storable products. Furthermore, with evidence of persistent residual demand in consumer countries despite domestic trade bans, all indications were that these species will require the continued allocation of significant resources to protect them from poaching. Given the budgetary constraints facing many SADC governments, likely aggravated by the economic impacts of the COVID\\u201019 pandemic, it is unclear whether these resources will be available at adequate levels. Consistent reports of severe shortfalls in conservation funding suggest that there will be an ongoing, if not increasing, dependence on external donor support, which may be insufficient and insecure (Lindsey et\\u00a0al., 2018; McCarthy et\\u00a0al.
Metadata
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