Protected areas are important refuges for biodiversity (Myers et al. 2000, Pimm et al. 2001) and are crucial for the conservation of species threatened by land use change and habitat loss (Chape et al. 2005, Gaston et al. 2008, Joppa et al. 2008, Palomo et al. 2013, 2014). In some cases, protected areas are becoming isolated in the landscape because of land use change and intensification (DeFries et al. 2005, Foley 2005, DeFries and Rosenzweig 2010), while other protected areas have been developed according to integrative approaches that address biodiversity conservation alongside human livelihood concerns (MA 2005, Bengtsson et al. 2003, Naughton-Treves et al. 2005, Kareiva and Marvier 2012, Zeller et al. 2017). Increasingly, more inclusive planning processes and coordination between conserved areas and surrounding communities are being called for (Reed 2008, Heller and Zavaleta 2009).
The successful integration of protected areas and surrounding landscapes depends on interactions between various stakeholders, including practitioners, policy makers, and resident communities (Kothari 2008, Lockwood et al. 2012). Protected areas are affected by and can have an effect on such stakeholders, either directly or indirectly, through their use of resources and land use decision making (Lockwood 2010). For effective stakeholder engagement, a strategic view of the social and institutional setting, which includes the issues stakeholders consider most salient and imperative to their well-being, is required (Mannetti et al. 2017). A failure to do so can lead to a lack of support from local communities and practitioners, making the aims of integrated conservation approaches futile. We present a case study of stakeholder identification and categorization regarding resident community inclusion in an expanded protected area around the Etosha National Park (ENP) in Namibia. By taking into account the perspectives and interests of those being integrated into the conservation landscape prior to protected area expansion, our approach attempts to reduce the risks of land use conflicts typically associated with people living adjacent to protected areas (Andrade and Rhodes 2012).
In southern Africa several participatory approaches to environmental management have emerged, focusing on the collective management of nature by conservation authorities and neighboring communities (Perrotton et al. 2017). Recognized as integrated conservation or community-based conservation, these inclusive approaches emerged as a result of the failures of top-down bureaucratic approaches to wildlife conservation (Fabricius et al. 2004). Initially, southern African community conservation initiatives led to a wide range of livelihood and conservation impacts, in some instances resulting in the large-scale expansion of wildlife-based land uses and a considerable growth in locally captured benefits from natural resources (Roe et al. 2009). There have been failures, however, relating mainly to human encroachment on ecosystems, particularly poaching and deforestation in protected areas, threatening not only the viability of wildlife populations (Watson et al. 2014), but also the livelihoods of resident communities (see Siamudaala et al. 2009, Namukonde and Kachali 2015). Failures are tied to the poor support for conservation initiatives by local residents and are attributable to a number of factors, mostly centered on the exclusion of communities in the protected area decision-making process (Roe et al. 2009), a lack of benefits flowing to people living with wildlife (Lindsey et al. 2014), increased incidences of human-wildlife conflict (Guerbois et al. 2012, Chitakira et al. 2015), as well as conflicting values and perspectives regarding ecosystem benefits (de Groot et al. 2010, Bennett et al. 2015).
We argue that where multiple users of the same resource, namely the natural environment, have divergent values or conflicting interests such as production, subsistence, or conservation, a need lies in first understanding their different perspectives. In a similar study, Rastogi et al. (2010) assessed the relationships, importance, and power of stakeholder groups to protected area management outside the Corbett National Park in India, highlighting the need to understand divergent opinions on the same issue to reduce conflict. Using prescribed attributes, Nastran (2014) determined stakeholder salience of individuals and groups involved in the implementation of the Kamniško-Savinjske Alps Regional Park in Slovenia and found that the salience of different stakeholder groups differ during the various project stages. Building on this approach to stakeholder analysis and protected area decision making, we identify and categorize stakeholders based on their perspectives and interests in being incorporated into a multifunctional conservation landscape, explicitly taking into account their self-perceived power and importance in the protected area decision-making process.
Community-based conservation in Namibia is largely considered a success by local communities, development NGOs, and the government (Brown and Bird 2011). This is attributable to policy reforms that led to the devolution of rights over resources at a local level (Jones 2010), which in turn resulted in an increase in conservancies, i.e., large areas designated for the protection and conservation of natural resources, and a recovery of wildlife populations (Weaver and Petersen 2008). Biophysical and socioeconomic conditions have led to there being minimal opportunity costs of alternative land uses (Roe et al. 2009), while institutional structures allow for cooperation between the private sector and communal conservancies (Mannetti et al. 2017).
The protected area landscape is thus effectively expanding because of the proliferation of communal and freehold conservancies (Weaver and Skyer 2003, Weaver and Peterson 2008, NACSO 2014, 2015). Overall, the protected area network expanded by 28,983 km² (9%) between 2010 and 2013 (MET 2014), directly affecting roughly 195,000 people, or 13.9% of the population (NACSO 2016). Together with national parks and private game reserves, these conservancies ensure that, to some degree, roughly 40% of the country is dedicated to wildlife conservation (MET 2010). This expanded protected area network includes different land use types and policy sectors, thereby generating multiple interdependencies between various stakeholders. Stakeholders include the state, groups and entities from international donors and NGOs, to private and communal farmers, communities, traditional authorities, and hunting and tourism enterprises.
Because it is not possible to include all stakeholders in the expansion of the protected area network surrounding ENP, we applied stakeholder analysis to our study (see Table 1 for an explanation of key terms used). Stakeholder analysis is a technique used to generate knowledge about participants and to better understand their interests and behaviors, ultimately assessing stakeholder value in decision making (Varvasovszky and Brugha 2000). Although rooted in political economics, the stakeholder analysis approach has increasingly been used to identify stakeholders that influence the decision-making process surrounding natural resources (Reed et al. 2009). Generally, stakeholder analysis is used to generate information on the relevant participants in an attempt to understand their actions, perceptions, agendas, and influence on decision-making processes (Brugha and Varvasovszky 2000). It also helps identify opportunities and threats to projects, finding compatibility between objectives and stakeholder aspirations (Chevalier and Buckles 1999) and to better understand the diverse range of potentially conflicting stakeholder viewpoints (Friedman and Miles 2004, 2006, Prell et al. 2007).
According to Freeman (1984), stakeholders are those who are affected by the choices and actions taken by decision makers and who have the power to influence those choices. Mitchell et al. (1997) suggest that individuals, groups, communities, organizations, societies, and the natural environment are all entities that qualify as being actual or potential stakeholders. The existence and nature of the stakes, i.e., shares or interest in a situation, is what generates disparity, because whatever is believed to constitute a stake is that which will inevitably dictate what counts (Mitchell et al. 1997). Therefore, defining who or what stakeholders are is linked to defining what makes a legitimate stake. Much of the literature makes implicit assumptions about the legitimacy of stakeholders (Friedman and Miles 2002) presuming that stakeholders are self-evident and self-construed. This makes it challenging to know which stakeholders should be involved in identifying relevant issues (Dougill et al. 2006) and to subsequently categorize stakeholders to better understand their interests and relationships.
It is necessary to identify who holds a stake and the nature of the stake held. In our study, the scenario under analysis is the incorporation of adjacent land users into the integrated protected area network around ENP. The country’s long-term vision is to develop a system of integrated land and natural resource management, essentially transforming the current protected area patchwork into a protected area network, involving state-owned protected areas, game parks, private nature reserves, tourism concessions, freehold and communal conservancies (Brown et al. 2005). Our research places stakeholder involvement in the context of natural resource management and protected area decision making. The aims of this paper are (a) the identification of primary stakeholders related to an expanded protected area network, (b) the categorization of primary stakeholders according to their perceived interests in an integrated landscape, their degree of support for the concept, and their power to influence it, and (c) a calculation of stakeholder importance in protected area decision making.
The study was conducted along the southern and southwestern border of ENP (22,270 km²) in the Kunene region of Namibia (Fig. 1a). The region has a semiarid to arid climate with less than 50 mm to approximately 350 mm of average annual rainfall (Mendelsohn et al. 2003). The mountainous topography leaves large areas of the landscape inaccessible, and combined with the aridity, this significantly hinders agriculture (Mendelsohn 2006). The region’s economy is dominated by tourism and hunting enterprises, sedentary livestock production at low stocking rates, and seminomadic pastoralism (Mendelsohn 2006). The area supports a variety of arid savanna and desert-adapted mammalian species, including African elephant (Loxodonta africana) and black rhinoceros (Diceros bicornis; Schwabe et al. 2015). Predators include lion (Panthera leo), leopard (P. pardus), cheetah (Acinonyx jubatus), spotted hyena (Crocuta crocuta), and brown hyena (Hyaena brunnea; Lindsey et al. 2013, Trinkel et al. 2017).
The ENP is surrounded by several land users, including private and communal livestock farmers, game reserve owners/managers, communal conservancy members, and “resettlement” farmers. On resettlement farms, communities reside on land procured by the state in an attempt to equitably distribute social, economic, and ecological benefits of land and natural resources to previously disadvantaged citizens. Here, land has been parceled into smaller units and distributed by traditional leaders to subsistence livestock farmers. To the west of ENP, two conservancies cover more than 5000 km² and are home to approximately 5000 agro-pastoralists with access to benefits from wildlife (NACSO 2016). To the south of ENP, private land is variably dedicated to livestock production, wildlife production, and combination livestock and wildlife farms (Jokisch 2009). Private game reserve and livestock farmers own the properties on which they operate, while communal livestock farmers have limited rights to either communal conservancies or resettlement farms.
Apart from a boundary fence, ENP is also surrounded by a veterinary cordon fence, a control method for establishing disease-free zones in beef exporting countries (Scoones et al. 2010). It separates the conservancies in the west and private land in the south from ENP (Berry 1997). The fence is therefore a double fence, consisting of a high game-proof fence separated by a 10-m passage from a stock-proof fence on the side of the farms and communities (Fig. 1b).
A pilot study was conducted in February 2013 to identify relevant stakeholders in the study area and to design the interview schedule. During April to June 2013, primary data were collected using participant observation, key informant structured interviews, and semistructured interviews with representatives from each stakeholder group (Chambers 1997). Stakeholder interviews (n = 82, varying from 60–90 minutes in duration) were then conducted with landowners and managers, conservancy members, resettlement farmers, conservation professionals, and other experts in the area, and on individual farms along the southern border of ENP. Apart from two landowners who declined the interview, all private landowners/managers were interviewed. In the communal conservancies and resettlement farm, a representative sample of 12 households was interviewed in each community. See Appendix 1 for the study sample of individuals interviewed and the sample selection techniques used. Formal, closed-ended questions were used to guide the interview and maintain structure, while open-ended questions allowed interviewees to speak freely and discuss issues they deemed relevant to the study, encouraging the emergence of unexpected themes and issues (Creswell 2009). Our research observed the international ethics guidelines of informed prior consent, avoiding harm and providing benefit wherever possible.
Interview protocols were translated, transcribed, and analyzed, with codes and categories being derived according to the research questions. Using QSR-NVivo (version 10), codes were assigned to words, phrases, and sentences (Hutchison et al. 2010) that referred to stakeholders’ perceived interests and how important stakeholders considered themselves to be in relation to the proposed protected area landscape (see Appendix 2 for a description of stakeholder identification and categorization). Stakeholders were further distinguished as primary or secondary, based on their stakes in the implementation of an expanded protected area system around ENP (Clarkson 1995; Table 1). The factors describing stakeholders’ attributes were position (stakeholder level of support for, or opposition to, an expanded protected area network), interest (perceived disadvantages and advantages of being part of an integrated landscape, and power (the resources a stakeholder is able to mobilize in order to express their position).
These attributes were assessed using unipolar scales anchored at the ends, i.e., stakeholders were rated based on the presence or absence of an attribute, namely position, interest, or power, with the midpoint indicating indifference/neutrality, general interest, and neither the resources or the ability to mobilize them, respectively. See Appendix 3 for a description of the 10-point scale. Stakeholder attributes were based on answers to questions asked during the interview (Appendix 4) and were assessed according to the descriptions and categorizations described in Table 2. According to experts with prior experience of the study system and its resident communities, the three attributes are representative and efficient in determining a stakeholder’s importance in the decision-making process involving an expanded protected area network. The analytical categorization was based on that of Mitchell et al. (1997) who prescribe using urgency, legitimacy, and power to assess “who and what really counts” in stakeholder theory. Here, urgency or a stakeholder’s attention-getting capacity, is substituted with the interest attribute because all groups studied were considered to have equal or similar urgency on account of their proximity to ENP. The interest attribute gives an indication of the stakeholder’s willingness to participate in the expanded protected area concept and thus influence future decisions. Legitimacy denotes socially acceptable or normative appropriateness of stakeholder demands, i.e., expected structures of behaviors (Neville et al. 2011). Because assessing desirability and appropriateness of stakeholder viewpoints was not the aim of the study, and we only intend to ascertain the pragmatic or cognitive validity of stakeholder support or opposition of the concept, the legitimacy attribute was replaced by that of position.
Twelve main stakeholder groups were identified based on differences in land use practices and their roles in the system under study (Table 3). Stakeholders were classified as “primary” (n = 56) or “secondary” (n = 26) based on their proximity to ENP (whether they were located adjacent to the park or not), land tenure (private or communal), and how important they were to the decision-making process guiding integrated landscape management, i.e., their stake in the protected area expansion.
Stakeholder positions on being incorporated into the conservation landscape vary from negative (oppose) to strongly positive (support). When the results of stakeholder position were assessed, opposition to being incorporated into the protected area landscape was found in the resettlement farmer, livestock farmer, and communal conservancy member primary stakeholder groups (score = 4; Fig. 2a). However, when results were classified in relation to land use, i.e., commercial or subsistence livestock farming, consumptive wildlife use, tourism, and hunting, and not according to stakeholder roles in the system, we found opposition in the livestock production group (Fig. 2b). Livestock farmers directly adjacent to the park were in opposition to the concept of being part of the integrated conservation landscape. Although they did not score 1 (strongly negative and in opposition of the idea) and are categorized as negative (2 or 3), their opposition was offset by the more slightly negative or indifferent scores (4 or 5) of the majority of their group (n=5).
Based on stakeholder responses to questions relating to the perceived advantages and disadvantages to being incorporated into the protected area landscape, interest scores varied across and within stakeholder groups. The median scores of each stakeholder group are depicted in Figure 3 where stakeholders are categorized on a 1–10 scale ranging from “no or minimal” to “primary” interest in being part of an integrated conservation landscape. Based on answers to open-ended questions, stakeholders were also grouped according to their stated interest in becoming part of the protected area landscape. Livestock farmers stated consumptive benefits such as “better quality grazing,” “improved soil maintenance,” and “rich underground water reserves.” The tourism facilities mentioned nonconsumptive benefits such as “increased wildlife sightings,” “proximity to a renowned protected area,” and “existence value.” Those tourism facilities that provided game and trophy hunting experiences or the private landowners that practiced combination farming, i.e. livestock and game production, cited both consumptive and nonconsumptive benefits related to being part of the conservation landscape.
The communal conservancy stakeholder group stated that being part of the larger conservation area will benefit them tangibly, i.e., provisioning ecosystem services such as fuel wood and forage for livestock, and intangibly, i.e., cultural and regulating ecosystem services, including hunting and tourism as well as flood and drought control. Unlike the other stakeholder groups, communal conservancy members are legally bound to maintain and monitor natural resources on their land and many mentioned this obligation during interviews or informal conversations. Their interests span consumptive and nonconsumptive benefits being derived from the park, and also a concern, as determined by policy, for the ecological health of the ENP and its surroundings. Also stated by several participants in various stakeholder groups were certain “collateral benefits” of flanking the park, including availability of roads, clinics, and schools in the area.
The most commonly cited disadvantage, both within stakeholder groups and amongst all respondents, related to the ENP fence. The physical fence was viewed as ineffective in preventing human-wildlife conflict because a lack of maintenance, fire and structural damage caused by animals seeking forage and/or water has left some sections permeable. Several respondents mentioned disadvantages and threats to the ENP in the event of an expanded protected area. These mostly included concerns surrounding increased poaching incidents, human encroachment, land conversion, invasive species, e.g., common impala (Aepyceros melampus), and illegal livestock grazing and fuel wood collection in the park because of the permeability of the fence.
The majority of the power rests with private land owners directly adjacent to the ENP, because under freehold title they are entitled to use their land as they deem fit. Land managers, i.e., those in charge of properties but who do not own or have any financial shares in the establishment, and private landowners not directly bordering the park, the government, and park management, all fall in to the medium range of power. As secondary stakeholders, investors and insurance companies, unions and NGOs had low power scores. Communal conservancy members and resettlement farmers, although primary stakeholders, had low power scores because they do not own the land they are managing and have neither the resources nor, in most cases, the ability to mobilize them to decisively determine outcomes regarding protected area expansion.
The median values of each stakeholder group’s attribute estimates are presented in Table 4. Key stakeholder groups in the protected area landscape were identified as those with the highest scores; ENP management (S = 15.2), tourism facilities (S = 13.3), and the state (S = 13.3). Also of importance were livestock farmers (S = 12.1), experts (S = 11.8), and NGOs (S = 11.8). The majority of stakeholder groups scored high on the x and y axes where position and interest intercept, but because of their lower power scores their placement on the z axis shortened their distance from the starting point, lowering their salience. Primary stakeholders such as communal conservancy members, who expressed interest and support for the concept of an integrated landscape, had lower salience estimates than other primary stakeholders also directly neighboring the park (Fig. 4). The group with the highest salience, ENP management (S = 15.2), directs the processes of the park and any future expansion. The state had the second highest score (S = 13.3). Both the state and ENP management are responsible for protected area planning and implementation and in effect, they should be responsible for conducting a stakeholder analysis, instead of being a subject thereof. Tourism facilities are thus viewed as having the highest salience, effectively (S = 13.3).
Group specific cumulative values for interest revealed that ENP management and scientific/research experts were the most supportive of the expanded protected area concept (Appendix 5). As a group, livestock farmers, and ENP management, perceived themselves as having primary interests in the conservation landscape; whereas livestock farmers and the state, cumulatively, had the highest power scores. Livestock farmers mostly (63%) scored as moderately supportive, indifferent, and slightly opposing the concept, while half of the group had a general to high interest therein and the rest scored as having a high to primary interest.
The planning and implementation of protected areas involves different policy sectors and affects different land use categories. According to Grimble and Wellard (1997), the explicit consideration of trade-offs between different policy objectives and conflicts between stakeholder interests facilitates effective project design and improves the likelihood of success thereof, aiding in the assessment of outcomes and avoiding the unexpected. The collective governance of natural systems involves multiple uses and users of resources. Thus by analyzing the interests and impacts of intervention of different stakeholders, stakeholder analysis can help ensure that potential costs and benefits are equitably considered and reach the intended parties.
Stakeholder analysis was used to identify and categorize stakeholder groups surrounding the ENP and those potentially involved in the extension of the current protected area system. Based on their proximity to the national park, private landowners, communal conservancy members, and resettlement farmers together with ENP management, were identified as primary stakeholders. Local residents and local level protected area staff who are imperative to the preservation of cultural and natural landscapes (Furze et al. 1996, Borrini-Feyerabend et al. 2004) have also been highlighted as important in the joint process of conservation and development by studies in the field of participatory planning (Hannah et al. 1998, Wells and McShane 2004, Treves et al. 2009). The selection of stakeholders based only on proximity, however, obscures the variable viewpoints held by resident communities (Reed et al. 2009).
Once identified, matrices are commonly used to categorize stakeholders by grouping them according to their relative interest and influence. Reed et al. (2009) applied interest-influence matrices in describing the principle ways in which stakeholders involved in the UK Rural Economy and Land Use Programme related to various aspects of the project. They found that although such matrices provided quantitative information about the relative interest and influence of different stakeholders, the information remains subjective, containing many hidden assumptions that fail to capture the position of stakeholders regarding the matter at stake, and as such have limited replicability. They conclude that “by capturing qualitative information about why different stakeholders have a particular interest (and specifically what this interest is), and why certain stakeholders have more influence than others (and in what contexts), the information gathered is likely to be more useful and replicable” (Reed et al. 2009:1946). Our study therefore categorized stakeholders according to attributes of position, interest and power.
When opposition to the concept of being incorporated into the conservation landscape was assessed based on land use, i.e., commercial or subsistence livestock farming, consumptive or nonconsumptive wildlife use, combined livestock farming and wildlife use, opposition was linked to dependence on livestock farming. In addition to assessing position on being incorporated into the conservation landscape, we assessed stakeholders’ perceived advantages and disadvantages of being part of the protected area matrix, i.e., interests. The combination of interest and position provided a clearer picture of supportive stakeholders and the reasons for their support.
Supportive stakeholders can be viewed as collaborators (Varvasovszky and Brugha 2000), particularly when their viewpoints have been incorporated in the initial planning phases and they have a sense of ownership over the project. Strong supporters for an integrated conservation landscape include those particularly focused on nonconsumptive activities. Those only moderately supportive of the concept included tourism facilities that practiced combined game and livestock production because of the risk of predation on livestock. These moderately supportive, so-called “fence-sitters” could be important in generating support for the protected area network if the areas surrounding the ENP are to be incorporated (see Rastogi et al. 2014).
Stakeholder groups that are categorized as neutral and slightly negative still need to be considered because they are directly affected by any decisions regarding the conservation landscape. Opposition to the expanded protected area concept is stronger among livestock farmers, on private and communal land, than among other land use types (consumptive and nonconsumptive tourism and combination farming). Other studies involving protected areas and their surrounding farmlands also identified farmers as main opponents (Stoll-Kleemann 2001a, b, Arnberger and Schoissengeier 2012, Nastran 2015). Because farmers and protected areas depend on similar natural benefits provided by landscapes, e.g., provisioning and regulating ecosystem services such as clean water, pastures, and soil maintenance, they are often in conflict with each other for these benefits. This emphasizes the importance of considering ecosystem services used by stakeholders in the conservation landscape decision-making process (de Groot et al. 2010, Darvill and Lindo 2016).
Regarding perceived interests of being part of the protected area network, diverse opinions were expressed within the same stakeholder groups. In the groups that depended on a combination of wildlife use and livestock farming, mentioned advantages of being adjacent to the park included consumptive and nonconsumptive benefits being derived from an increase in wildlife populations, namely the potential increase in hunting quotas and an increase in tourism, respectively. Within these groups, increased human-wildlife conflict was also considered a disadvantage, because the predation on livestock and the destruction of crops threaten livelihoods. This indicates diversity in opinion on the same issue, because of different perceptions surrounding the benefits of living adjacent to a protected area. Stakeholder dynamics within and between groups can thus not be overlooked.
Individual estimates of stakeholder attributes may also change over time, depending on the social-ecological or political situation (Neville et al. 2011, Van Assche et al. 2011). In the current study, the land tenure systems in place affects power dynamics. Under freehold title, private farmers have absolute land rights over their properties, while communal conservancy members and resettlement farmers, under customary tenure, are authorized by traditional leaders with the land and resources belonging to the state. This affects their decision-making ability in the landscape, particularly the mobilization of resources to support or oppose any changes (Mitchell et al. 1997). Other stakeholder analyses have incorporated stakeholder attributes of legitimacy: whether stakeholders have legitimate demands, and urgency, whether stakeholder’s claims call for immediate attention (Neville et al. 2011, Nastran 2014). In the southern African context, the combination of interest, position, and power, as applied here, is sufficient in that it considers the diverse socio-political and ecological variables present in the landscape.
Even those opposed to the expanded protected area, such as livestock farmers, and those with less power to effect change, such as conservancy members and resettlement farmers, need to be included in the decision-making process, and their concerns about being incorporated into the conservation landscape taken into account (Suŝkevičs et al. 2013, Nastran 2015). Under mobilization, such opposing and less powerful groups may be able to sway opinions and it is therefore important to identify their concerns and seek ways to address them, solving conflicts proactively. A larger, diverse and connected landscape is more resilient than a smaller, fragmented one (Cumming 2011). This is critical in arid southern Africa, where diversified resource dependence and a broader livelihood base provide greater safety nets for more people (Shackleton and Shackleton 2004, O'Farrell et al. 2010). The support and collaboration of (all) key stakeholders is therefore essential for a successful protected area system, supporting a variety of land uses and resource users.
Land use type affects stakeholder position concerning being incorporated into the protected area system, with livestock farmers mostly opposing the concept. All primary stakeholders cite interest therein, however, with power greatly affecting stakeholder salience because land tenure prescribes the roles and activities of stakeholders on the various properties surrounding the ENP. The interpretation of stakeholder analysis varies across disciplines, with stakeholder participation and empowerment presenting a central theme. In most cases, stakeholders are categorized according to their power, legitimacy, and urgency, with the assumption that these attributes indicate the amount and type of attention stakeholders need. We argue that this only provides a static view of the situation and highlight the need to understand the dynamic nature of stakeholder attributes instead. Furthermore, only a limited amount of empirical research adopts the perspective of the stakeholders to understand stakeholder attributes and how these potentially influence decision making. In this paper, we combine the identification and categorization of stakeholders with stakeholder perspectives on position, interest, and power in the expansion of the protected area network, and thus their influence in the outcome. The paper extends existing research by assessing the dynamic nature of stakeholder salience in protected area decision making and understanding the differences within and between stakeholder groups. Ultimately, recognizing stakeholder perspectives can enable practitioners and policy makers to better understand and manage stakeholder inclusion in landscape management.
Thank you to all the study participants for sharing their valuable time, observations, and perspectives and the anonymous reviewers for their helpful and constructive comments. The research was conducted with funding provided by the International Foundation for Science (grant number S/5299-1), the Namibia Environmental Investment Fund, and the Harry Crossley Foundation (MET Research Permit 1828/2013-16). We acknowledge support from the International Offices of Stellenbosch University (namely R. Kotze) and Humboldt-Universität zu Berlin (namely U. Hans) and the German Academic Exchange Service (DAAD) for supporting this study under the umbrella project “Quality Network Biodiversity in Sub-Sahara Africa” (project number: 20010181 PI: Prof. Zeller) and to the Zwillenberg-Tietz Stiftung and the project “Land use contrasts and edge effects - a comparative approach.” KJE acknowledges the South African National Research Foundation, NRF (grant number 103841). LMM and KJE recognize the Southern African Program on Ecosystem Change and Society (SAPECS) for their invaluable input.
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