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The following is the established format for referencing this article:
Bowd, R., N. Quinn, D. C. Kotze, D. G. Hay, and M. Mander. 2012. The identification of potential resilient estuary-based enterprises to encourage economic empowerment in South Africa: a toolkit approach. Ecology and Society 17(3): 15.
http://dx.doi.org/10.5751/ES-04840-170315
Research

The Identification of Potential Resilient Estuary-based Enterprises to Encourage Economic Empowerment in South Africa: a Toolkit Approach

1School of Environmental Sciences, University of KwaZulu-Natal, 2Department of Geography and Environmental Management, University of the West of England, 3Independent Consultant, 4Eco-Futures

ABSTRACT

It has been argued that ecosystem services can be used as the foundation to provide economic opportunities to empower the disadvantaged. The Ecosystem Services Framework (ESF) approach for poverty alleviation, which balances resource conservation and human resource use, has received much attention in the literature. However, few projects have successfully achieved both conservation and economic objectives. This is partly due to there being a hiatus between theory and practice, due to the absence of tools that help make the transition between conceptual frameworks and theory, to practical integration of ecosystem services into decision making. To address this hiatus, an existing conceptual framework for analyzing the robustness of social-ecological systems was translated into a practical toolkit to help understand the complexity of social-ecological systems (SES). The toolkit can be used by a diversity of stakeholders as a decision making aid for assessing ecosystem services supply and demand and associated enterprise opportunities. The toolkit is participatory and combines both a generic “top-down” scientific approach with a case-specific “bottom-up” approach. It promotes a shared understanding of the utilization of ecosystem services, which is the foundation of identifying resilient enterprises. The toolkit comprises four steps: (i) ecosystem services supply and demand assessment; (ii) roles identification; (iii) enterprise opportunity identification; and (vi) enterprise risk assessment, and was tested at two estuary study sites. Implementation of the toolkit requires the populating of preprogrammed Excel worksheets through the holding of workshops that are attended by stakeholders associated with the ecosystems. It was concluded that for an enterprise to be resilient, it must be resilient at an external SES level,which the toolkit addresses, and at an internal business functioning level, e.g., social dynamics among personnel, skills, and literacy levels. Although the toolkit does not address the internal resilience level of an enterprise, it proved helpful at indicating which enterprises show potential resilience given current SES conditions.
Key words: ecosystem services; participatory tools; risk assessment; social-ecological systems; stakeholder engagement

INTRODUCTION

In 2008 the South African Institute for Race Relations (SAIRR) recognized that the gap between the wealthy and the poor in South Africa was continuing to increase, and that this situation was not sustainable (Hunter et al. 2003, Meth and Dias 2004). Recent studies suggest South Africa’s inequality levels are among the highest in the world (Fosu 2011) and during the period 1993-2008, income has been increasingly concentrated in the top decile (Leibbrandt et al. 2010). Rural communities experience relatively greater poverty (Leibbrandt et al. 2010), and nowhere is this more the case than the Eastern Cape Province of South Africa, where concern has been expressed, not just in relation to standard poverty metrics (Dzivakwi and Jacobs 2010), but also to people’s vulnerability to poverty (Baiyegunhi and Fraser 2010).

It has been argued that ecosystem services can be employed as both a ‘common language’ for ecosystem-based management (Granek et al. 2009), and as the foundation to providing economic opportunities to empower the disadvantaged (MEA 2005). Although both the wealthy and the poor rely on the functioning of ecosystems (Batabyal and Yoo 1994, Scheffer et al. 2000, MEA 2005), the poor are often more directly reliant on these goods, services, and attributes than the affluent. As noted by Tallis et al. (2008:9459), “for the rural poor, at the local level, the status of ecosystem services can make a big difference in their daily lives.”

The potential application of the Ecosystem Services Framework (ESF) approach for poverty alleviation, which balances resource conservation and use according to how society values consumptive and nonconsumptive services provided by an ecosystem, has received much attention in the literature (Brown et al. 2008, Shackleton et al. 2008, Tallis et al. 2008). The ESF approach is currently the focus of a significant research endeavor known as ESPA (Ecosystem Services for Poverty Alleviation see www.espa.ac.uk/). Other initiatives, such as the Natural Capital Project (see www.naturalcapitalproject.org/home04.html) have also focused on the potential for aligning conservation and economics via the ESF (Turner and Daily 2008).

However, projects that have successfully achieved both conservation and economic objectives are relatively rare. For example, in an analysis of World Bank projects that had the dual aims of poverty alleviation and biodiversity conservation, Tallis et al. (2008) found that only 16% made significant progress on both objectives. Part of the reason for this has been the hiatus between theory and practice. As suggested by Turner and Daily (2008:25), despite this attention in the literature, “an operational decision support system” for implementing an ESF has been “slow to emerge.” Daily and Matson (2008:9456) put the challenge more strongly, “(r)adical transformations will be required to move from conceptual frameworks and theory to practical integration of ecosystem services into decision-making, in a way that is credible, replicable, scalable and sustainable.”

In this paper we attempt to address this challenge by presenting an approach for applying an ESF to assist in the identification of opportunities for economic empowerment at two estuary study sites in the Eastern Cape Province, South Africa. In doing so, we also provide an example of how an ESF can be used toward the aim of poverty alleviation.

METHODS

Selection of study sites

Estuaries, in particular, are a useful context in which to develop and test ideas regarding ESFs. Day (1980:198) defines an estuary as a “partially enclosed coastal body of water which is either permanently or periodically open to the sea, and within which there is a mixture of seawater with freshwater derived from land drainage.” Estuaries are ecosystems comprised of a number of different habitats, such as mangroves, tidal flats, and reed beds, which can provide food, building material, and protection; are catalysts for residential, commercial, tourism, and recreational development; and can ameliorate floods and assimilate waste (Gunderson et al. 2006, Hay 2007, Barbier et al. 2011). Estuaries are therefore complex and dynamic social-ecological systems (SES; Anderies et al. 2004), where interactions occur between:
In South Africa (Turpie and Clark 2007), and globally (Barbier et al. 2011), estuaries are clearly valuable economic, environmental, and social assets that can provide economic empowerment, including job creation for disadvantaged people living at or near them (Turpie and Clark 2007). Many of the services provided by estuaries are taken for granted and consequently the derived benefits are undervalued. Estuaries are highly dynamic environments that are unpredictable and erratic in nature. Given their high productivity, they are often subject to very high levels of use, and given their location in the lowermost point in the catchment, are often subject to some of the greatest anthropogenic impacts.

Estuaries are also common property resources with poorly defined property rights. This complicates the allocation of opportunities and the benefits that arise from these opportunities. Securing tenure, a vital necessity for most economic developments to succeed, requires a level of sophistication that is currently in short supply in many rural parts of South Africa.

Two estuaries located in the Eastern Cape Province of South Africa were chosen to apply the toolkit: the Umngazi estuary, located near Port St. John (31°37'38.43"S, 29°32'58.44"E), and the Tyolomnqa estuary, located near East London (32°58'56.85"S, 27°56'52.70"E). Both sites currently provide a variety of ecosystem services but differ with respect to their component social systems. The Tyolomnqa estuary’s social system is large and complex, and comprises prominent local and provincial governmental bodies, nongovernmental agencies, and general service users, e.g., local and visiting fishermen. This system is in relatively close proximity to the urban center of East London, and the policing of resource use activities is high. In contrast, the Umngazi system is rural in nature and is less complex because there are fewer stakeholders. Although local and provincial governmental bodies operate in the area, their presence is not strong. The dominant stakeholders are the local community, a well-established hotel, and tourists.

Criteria for developing the ESF Toolkit

The overall aim of the ESF toolkit is to provide a structured mechanism for identifying potential estuary-based enterprises that take into consideration the dependence of human well-being on natural capital, and that consider resource conservation (Turner and Daily 2008). Turner and Daily (2008:26) identify three constraints in making an ESF approach operational. First there is what they describe as “information failure,” which is the lack of detailed information about the way in which people benefit from ecosystem services, and at a scale that is relevant to decision makers. The second is “institutional failure.” This arises as a result of the failure to consider local social-ecological contexts, including property rights and institutions, and the fact that those who benefit from ecosystem transformation are not the same as the recipients of ecosystem services. Finally “market failure” arises because of the public good nature of benefits and because many of the benefits cannot be quantified or measured in a single currency.

Turner and Daily’s (2008) critique has therefore informed the identification of a set of four criteria that would be instrumental in a successful ESF approach. The first criterion is that public participation should be an integral part. This relates strongly to information failure and institutional failure constraints. Second, it is evident that one of the fundamental attributes of an operational ESF should be a mechanism that allows the particular services to be discussed, understood, and valued in a common currency. In other words the ESF should provide a platform for discussion by contributing detailed information on ecosystem services. Third the toolkit must have the ability to gauge a system’s resilience because the purpose of this study is to have a framework that identifies potential resilient estuary-based enterprises. Finally, the toolkit must contribute to obtaining a thorough understanding of the complex social-ecological context. This too would help address the institutional failure and the market failure constraints.

An ESF Toolkit for economic empowerment must be participative

In recent years stakeholder engagement has moved from being a marginal concern to a driving force (Lynam et al. 2007). Furthermore a dichotomy has been recognized between the commonly used “top-down” generic scientific tools that are frequently developed without input from the local stakeholders, and the case-specific customized “bottom-up” tools that are generally driven by local needs (Fall and Fall 2001, Sturtevant et al. 2007). Gunderson et al. (2006) identify five factors for constructive communication to take place: (1) the development and maintenance of open communication channels (Berkes et al. 1998, Folke et al. 2005); (2) identification of the roles of the different stakeholders through scientific activities or social communication (Fazey et al. 2005); (3) the designation of a meeting place at which discussions can take place between the different stakeholders; (4) the establishment of trust between the stakeholders; and (5) the establishment of leadership because this is required to integrate social and ecological understanding, and to delegate responsibility to ensure that progress is made. Participation characterized by constructive communication must therefore be a central criterion.

An ESF Toolkit for economic empowerment must provide detailed information on ecosystem services

An early challenge in the ecosystem services debate was defining and categorizing the nature and scope of these services. For example, Hein et al. (2006) present a generically applicable framework based on earlier contributions (Pearce and Turner 1990, Costanza and Folke 1997, de Groot et al. 2002, MEA 2003). This framework defines three types of services, i.e., production, regulation, and cultural. Production services refer to goods and services produced in an ecosystem, e.g., food, fuel timber; regulation services result from the capacity of ecosystems to regulate a variety of biological processes, e.g., erosion, storm protection; and cultural services relate to the benefits people obtain from ecosystems through recreation, cognitive development, relaxation, and spiritual reflection. It differs from the Millennium Ecosystem Assessment (MEA 2003), in that it does not differentiate supporting services. Supporting services represent the ecological processes that underlie the functioning of an ecosystem, and Hein et al. (2006) are of the opinion that the inclusion of supporting services could result in the “double counting” of services, and thus affect the valuation because they will feature in one of the other three types of services. The Resilience Alliance (2010) modified the Hein et al. (2006) framework by adding “regeneration services” to the regulation services. This was done to emphasize the importance of services, such as soil fertility maintenance (Resilience Alliance 2010).

In South Africa much work on describing and classifying estuary ecosystem services has been conducted. Turpie and Clark (2007) document estuary associated goods, services, and attributes and define goods as harvested resources, such as fish, services as processes that contribute to economic production or save costs, such as water purification, and attributes as relating to the structure and organization of biodiversity, such as beauty, rarity, or diversity, that generate less tangible benefits, such as spiritual, educational, cultural, and recreational values.

Based on these contributions a comprehensive list of estuary ecosystem services was developed. The term ‘services’ has been used to encompass goods, services, and attributes, as per Hein et al. (2006), Resilience Alliance (2010), and Bowd et al. (2012). Each of these services is related to the presence of suitable estuary habitat(s) and consequently it was important to identify the full range of estuary habitats. From conducting a brief literature review on the ecological functioning of South African estuaries, it became apparent that 10 habitat types could be identified (Branch and Grindley 1979, Allanson 1981, Baird 1999, Colloty et al. 2002), each of which was associated with one or more services (Table 1).

An ESF Toolkit for economic empowerment must consider resilience

Because all ecosystem services are subject to the influences of natural and anthropogenic processes that are highly variable, supplies of services are seldom uniform. Although some services may seem to be constant over time, others can exhibit wide variations, even over short time scales. Thus every enterprise that is founded on ecosystem services must anticipate changes over time and space as a consequence of both natural and human influences. Some of these influences may be controlled by society, e.g., pollution, however others, e.g., large floods, cannot. The viability of ecosystem-based enterprises will equally be influenced by fluctuations in the demand for services (see Baumgärtner et al. 2011 for an interesting discussion on the relationship between consumer preferences and resilience of ecological-economic systems). These demands may be very variable over time and in space, and furthermore, not all demands are compatible. Neither can they necessarily be accommodated at the same time, and in the same place. This lack of control of interaction places resilience at the forefront of conceptualizing, designing, establishing, and operating estuary-based enterprises. We define resilient estuary-based enterprises as those that are able to continue profitably under conditions of varying supply of, and demand for, the services upon which they are dependent. Necessarily this needs to be contextualized within the broader debate around resilience, adaptability, and transformability in social-ecological systems (Walker et al. 2004, Folke et al. 2010).

Since the 1970s a variety of definitions and interpretations of resilience have appeared (Pimm 1991, Grimm and Wissel 1997, Neubert and Caswell 1997, Walker et al. 2004). Ecological resilience is generally defined as the amount of disturbance that a system can absorb without a change in its state, usually defined by its structure and composition (Carpenter et al. 2001, Walker et al. 2006, Holling 2010). A resilient estuarine system is a system that can continue to provide the necessary services, which are utilized by the different stakeholders, even after times of stress, e.g., ecological conditions allow fish stocks to recover after extensive fishing during the previous season.

An estuary can be impacted upon by both natural events and human actions, which include human interventions that occur in response to natural events, e.g., implementation of bank stabilization measures. For an estuary to be considered resilient it must retain its state. Because an estuary supplies a wide range of services to a variety of stakeholder groups, it is unlikely that at any one time, there will be consensus among the different stakeholders that an estuary has retained its state, and is thus resilient.

There were a number of reasons why the concept of resilience was seen as being key to the approach. First, resilience has been applied widely to SESs and is increasingly being used to help understand, manage, and govern complex SESs (Walker et al. 2002, Anderies et al. 2004, Folke et al. 2004, Ostrom 2007). For example, it has been applied to political ecology and resource management (Berkes et al. 1998, Berkes 1999), as well as to a variety of specific ecosystems that include: rangelands (Anderies 2002, Janssen et al. 2004); lakes and wetlands (Gunderson 2001, Olsson et al. 2004); coral reefs (Hughes et al. 2005); a protected area (Newton 2011); and an evolving urban system (Bures and Kanapaux 2011).

Second, resilience theory suggests that the major entities of an SES, and the level at which they interact, are identified through approaches that involve constructive communication between experts and stakeholders who understand the SES at different scales and perspectives (Walker et al. 2002, Westley et al. 2002). Third, resilience theory emphasizes the need to consider human adaptability (Gunderson and Holling 2002, Walker et al. 2006). Human adaptability is the capacity of humans to manage for resilience; indeed collective capacity to manage resilience ultimately determines the future state of the SES (Walker et al. 2004). Human adaptability is therefore key in assessing the resilience of an enterprise and the SES on which an enterprise is dependent. Transformability has been defined as the “capacity to create a fundamentally new system when ecological, economic, or social (including political) conditions make the existing system untenable” (Walker et al. 2004). This includes “introducing new components and new ways of making a living” that define the nature of the SES (Walker et al. 2004), so the concept is particularly relevant in defining resilient estuary-based enterprises.

An ESF Toolkit for economic empowerment must accommodate complex social-ecological contexts

Folke et al. (2010) argue that social-ecological resilience is concerned with the interdependence of people and nature, and furthermore that an ability to effect social change is necessary for SES resilience. The implication of this is that not only do we need to understand the present nature of the SES, but also how this SES might adapt or transform in the future. We show how an existing framework can be used to establish these relationships and use them in a process of social learning. Anderies et al. (2004) present a framework for analyzing the robustness of SESs from an institutional perspective. This framework provides a mechanism for disaggregating the entities of a SES and promotes the identification of the relationships between the different entities. The SES is separated into the following four entities (1) the resource, (2) the resource users, (3) public infrastructure, and (4) public infrastructure providers, and considers two types of disturbance, external and internal (Fig. 1). Table 2 provides examples of each of these entities, together with the typical management challenges that characterize them, whereas Table 3 explores the links between each entity and their associated problems. Tables 2 and 3 are taken directly from Anderies et al. (2004). Although the Anderies et al. (2004) approach is based on robustness and not resilience, we do not need to distinguish between the two because we consider robustness and resilience to have the same attributes for the purposes of this study.

Developing the ESF Toolkit: structure

The toolkit comprises four steps that are supported using a preprogrammed Excel worksheet, linked with the four entities of the Anderies et al. (2004) framework (Fig. 1). The Excel worksheet and toolkit manual have been published by the South African Water Research Commission (Bowd et al. 2012).

Step 1: ecosystem services supply and demand assessment

This step requires that the estuary habitats present are confirmed and their functionality assessed. The functionality, and thus health, of an estuary’s habitats is directly related to its ability to supply ecosystem services. To identify the estuary habitats, the boundaries of the SES first need to be identified, e.g., areas accessible on foot from the estuary mouth. The functionality of each of the habitats is then calculated, by assessing its condition (0 – 3, three being the best condition), size (area given in ha), and prominence of the ecosystem within the landscape (0 – 3, three being the most prominent). Although condition and size are the key determinants of service levels, the landscape context is less important and thus only weighted at 10% of the other two scores in the functionality calculation.

Next, the level of supply of the ecosystem services associated with each of the different habitats is scored (0 – 3, three being high, 0 being no supply). The scores are given as if the habitats are pristine. The service supply score is then multiplied by the functionality score, to give a relative service supply level for each service. It is recommended that the issue of seasonal variations in the supply of services is raised before scoring commences. It may be assumed that those services that have a high overall supply level are the services that enterprises should be based around.

Whereas the previous is concerned with the supply of services, the next focuses on the potential demand for services. Service demand at the local, downstream, provincial, and national and international levels are estimated. Estimated figures of users are shown as orders of magnitude (e.g. 0, 100, 1000). Following this the users of the services are listed, followed by the dependence of each of the different services being scored between 0 (no impact on welfare) and 3 (critical for welfare).

As the toolkit is presented in a preprogrammed Excel worksheet, the following information is automatically calculated for each service: total supply score, total number of beneficiaries, average dependency, total demand summary, and combined total score. These data are then consolidated for use in Step 2.

Step 2: future estuary roles identification

The endpoint of the previous step is a ranking, in order of priority, of services that currently have high supply and low demand at a local, downstream, provincial, and national and international level. Using the knowledge and common understanding of the status quo gained though implementing Step 1, the desired roles for the estuary and possible conflicting uses, at local, downstream, provincial, and national and international levels, are then determined through discussion. Where supply is low, either intrinsically or because of poor ecological condition, but demand is high should be identified because this could indicate potential management actions that in themselves could represent enterprises, e.g., restoration.

Step 3: enterprise opportunity identification

The worksheet associated with this step provides space to document discussions around current and desired roles of the estuary, and possible conflicting uses. The worksheet provides different types of service use and possible estuary management categories to assist with identifying possible enterprise opportunities.

Step 4: enterprise risk assessment

This step is supported by two worksheets and is conducted for each enterprise. This step consists of a variety of questions that demonstrate the nature of possible relationships that may operate among the four entities of a SES (as identified by Anderies et al. 2004). Also included in this matrix are the external biophysical, social, and economic forces that may generate perturbations in a SES. The questions are based on those compiled by R. Bowd, N. W. Quinn, D. C. Kotze, D. G. Hay, and M. Mander (unpublished manuscript) who used the Anderies et al. (2004) framework to develop an analytical framework for understanding complex SES when conducting Environmental Impact Assessments in South Africa (Table 4).

The first worksheet requires that the severity and likelihood of each risk is scored (0-3, three being very severe). A risk with a high severity of impact and a high likelihood of occurrence is considered to pose a major risk to enterprise resilience. The severity and likelihood scores are then summed to provide a semiquantitative value for each risk.

The second worksheet automatically ranks the risks according to the magnitude of risks identified previously. Once ranked, the priority risks are then assessed and mitigating actions identified and noted. If severe risks cannot be mitigated, then the proposed enterprise has a strong possibility of failure.

TESTING THE TOOLKIT

As recommended by Pickett et al. (1999), Scheffer et al. (2000), Anderies et al. (2006), and Sturtevant et al. (2007), a multidisciplinary team was involved in developing and testing the approach, including ecological, economic, and social scientists. Criteria 2 and 4 encourage the involvement of a diverse team. The opinions from the different disciplines helped gain a comprehensive and common understanding of the different ecosystem services, and different aspects of the SES.

Criterion 1 highlights the importance of a participative approach, and as such the toolkit is primarily based on stakeholder engagement. Leemans (2000) identified stakeholder groups at a number of different levels. For the implementing and testing phase we adopted the following:
Walker (1992) believed that the greater the diversity of stakeholders involved in a process, the greater the chance of understanding the resilience of a system. This mix of stakeholder groups comprises the social component of the SES, and thus contributes to addressing criteria 3 and 4.

The toolkit was applied at Umngazi over two 2-day workshops, and at Tyolomnqa over one 2-day workshop. A full suite of stakeholders were identified through discussions with key stakeholders in the relevant areas, i.e., government departments, established enterprise owners, and review of estuary-related reports commissioned by the South African Water Research Commission. The identified stakeholders were personally invited to the workshop by phone, post, or email. At both study sites a wide variety of stakeholders attended and actively participated in the workshops (Table 5).

At each study site the first step was to define the boundaries of the SES. This helped gain a collective understanding of the SES among the different stakeholders (and helped address criterion 4). This was done by the stakeholders visiting the estuarine system and then continuing on to discuss the success and failure of past and present estuary-based enterprises, possible reasons for this success or failure, the supply and demand of the estuary services, and potential enterprise opportunities. Site visits facilitated a greater understanding of the system being considered, and promoted a shared understanding of the different ecosystem services provided by the estuary (Deconchat et al. 2007). The site visit and discussions contributed to addressing criterion 2.

Following the site visits, workshops for the stakeholders were held where the project team methodically introduced and applied the toolkit. Although the toolkit provided structured questions, discussions around the different questions and between the different stakeholders were encouraged to gain a greater understanding of the SES, and especially to enable different stakeholders to understand each other’s perspective. This helped address criteria 1, 2, and 4.

In an effort to promote inclusivity at the workshops, when one stakeholder group dominated a response the facilitator would directly ask the other stakeholder groups whether or not they agreed with the dominant stakeholder group’s viewpoint. This promoted discussion, ensured all participated, and helped gain a shared understanding of a situation. At both sites the provincial level planning authorities were generally more dominant and enthusiastic in comparison to other stakeholders. At Umngazi the provincial level authorities showed a keen interest in the indigenous knowledge communicated by the local community, and frequently asked for the community to expand on information when they did not initially grasp what was being said.

Step 1 of the toolkit, which took place at the beginning of the workshops and forced the stakeholders to work together to collectively ascribe scores, significantly contributed to the positive interactions that were observed between the stakeholders for the duration of the workshop. These good relations were most valued when populating the risk assessment and potentially sensitive issues needed to be discussed, e.g., the local community at Umngazi had to explain that there was a lack of service delivery from local government.

Although some discussions were very technical and difficult for all to understand, e.g., at Umngazi the community members struggled with understanding data presented by a university student researching estuarine benthic organisms, this lack of understanding did not cause resentment, but was in fact a source of amusement for all when scientific information was explained, which helped connect the stakeholders. At Umngazi this positive response to knowledge sharing was confirmed when after the workshop the community told the facilitator that the toolkit had “opened their eyes to the importance of the estuary, how it worked, and the opportunities it held.”

Through implementing Step 1 at the Umngazi estuary, a total of 12 possible estuary-based enterprises were identified. Through implementing the subsequent steps, four were identified as priority enterprises (Table 5). The village-based tourist accommodation, as part of a destination package, was selected for the risk assessment because the consensus of the stakeholders was that this enterprise would benefit a greater proportion of the community compared with the canoe and horse trails. In addition, the success of the accommodation enterprise predominantly rested with the community and the management of the well-established and successful hotel, thus its success was semicontrolled by the stakeholders. Although an estuary rehabilitation program (labor intensive alien plant removal), which the provincial level planning authorities were initially favoring, has the potential to result in a larger cash injection into the community in the short-term, similar programs have been established in the area and, because of inconsistent implementation, the community was wary of these types of enterprises. Although a number of risks were identified for the accommodation, possible actions to reduce these risks were provided (Table 5).

Through implementing Step 1 at the Tyolomnqa estuary, a total of eight possible estuary-based enterprises were identified. In working through the remaining steps there was consensus between the stakeholders that a wilderness camp would be used in Step 4 (Table 5). A wilderness camp at Tyolomnqa had previously failed, and the attendees were keen to know the reason for its failure, and if any mitigation measures could be implemented to improve its chances of survival if it was resuscitated.

It was concluded that the identified risks were of a magnitude that could not be mitigated or easily controlled without a combination of improved regulatory capacity and the sourcing of alternative nonmunicipal funds. Because the potential for implementing these two mitigation measures could not be accurately assessed with only those in attendance, the wilderness camp was not pursued further.

When the risk assessment concludes that an enterprise does not show potential resilience, the risk assessment can be repeated to assess an alternative enterprise. However, in this instance the identified risks at Tyolomnqa, which includes a lack of regulating capacity, poor water quality standards, habitat destruction, limited access, and poor security, are likely to affect the supply of the services on which any estuary enterprise is based. The risk assessment highlighted to the provincial planning authority representatives at the workshop, that to give an estuary-based enterprise the greatest chance of survival, some or all of the identified risks should be addressed before any new enterprise is pursued.

The provincial planning authority at Tyolomnqa could see value in the approach and in reflecting on a potential wider application. They were of the opinion that the toolkit could be:
At both sites the use of numerical values as relative measures in the toolkit helped to objectively select which enterprises should be selected for the risk assessment, because the scores were ascribed with consensus from the stakeholders in attendance. Having a broad scope of enterprises that need to be scored helped prevent the stakeholders getting fixated on one particular enterprise. In addition, numerical illustration steered discussions toward obtaining relevant qualitative data, thus time was not lost on irrelevant discussions.

In summary, the workshops identified that there are significant opportunities for the establishment of estuary-based enterprises that could act as catalysts for economic empowerment. However, currently the public service infrastructure providers, primarily local government, are either unwilling or unable to provide the necessary support required to improve the likelihood of an estuary-based enterprise being resilient. It is here where the major risks lie.

The purpose of the toolkit is to help identify potential resilient enterprises. Although all four steps within the toolkit contribute to identifying potential resilient enterprises, it is Step 4 (risk assessment) where the resilience of an enterprise is gauged. Thus the implementation of the risk assessment contributed toward addressing criterion 3.

DISCUSSION

In this section we consider application of the toolkit in view of the four criteria in Turner and Daily’s (2008) critique.

An ESF Toolkit for economic empowerment must be participative

The first constraint identified by Turner and Daily (2008) was that of information failure. The toolkit addresses this constraint because it is participant-focused and promotes direct communication between the different stakeholders, some of whom are decision makers. The toolkit combines both a generic top-down scientific approach, because the preprogrammed worksheet and risk assessment are founded on theory and scientific knowledge, with a case-specific bottom-up approach, which is obtained through a diversity of stakeholders actively engaging in discussion and reaching consensus on the scoring of the supply and demand of ecosystems services at a site-specific level. A facilitator is required to collate, interpret, and concisely present the information from the workshops, but this nevertheless represents a process aimed at bringing indigenous knowledge and science together to foster social-ecological system resilience (Bohensky and Maru 2011).

This extent of dialogue clearly results in better decisions being made. For example, at the Umngazi study site, the results of implementing the ESF Framework indicated that an estuary rehabilitation program would have created greater economic advantages compared with the community-based accommodation. However the community was strongly against this type of enterprise because similar initiatives had failed in the past. It is likely that without the participation of the community and the testing of the toolkit, decision makers would have pursued the estuary rehabilitation program. Based on the negative reactions of the community, it is likely that this enterprise would not have been supported.

Through applying the toolkit a number of participatory lessons were learned. These lessons have been tabulated and have been grouped into (i) facilitator; (ii) stakeholder; and (iii) workshop procedure lessons (Table 6). Bohensky and Maru (2011) have recently reviewed the challenges and achievements in bringing indigenous knowledge and science together and a number of key lessons presented in Table 2 of Bohensky and Maru (2011) could also assist the facilitator with implementing the toolkit in the future.

An ESF Toolkit for economic empowerment must provide detailed information on ecosystem services

The toolkit provides a systematic process for obtaining both qualitative and semiquantitative information, and a shared understanding of the way in which stakeholders benefit from ecosystem services. At Umngazi this mutual understanding is likely to help improve the resilience of the community-based accommodation enterprise because the stakeholders understood why this particular enterprise had been chosen and what services were required for it to be successful. It is likely that with the depth of understanding gained through implementing the toolkit, those in decision making positions, e.g., government officials, will help to ensure the protection of the ecosystems on which the community-based accommodation is reliant, e.g., basic infrastructure to service the accommodation, electricity, water, access road.

The second constraint identified by Turner and Daily (2008) was that of institutional failure. Before the workshop at the Tyolomnqa estuary, the provincial planning authority was of the opinion that there were likely to be many estuary-based enterprise opportunities because of the estuary being utilized for a wide range of activities and by a relatively high number of people. However, the risk assessment highlighted a wide range of constraints of which the provincial planning authority was previously unaware. This emphasizes the value of the toolkit in promoting discussion based on structured consideration of ecosystem services.

The third constraint identified by Turner and Daily (2008) was that of market failure. Although there is neither a universal currency to value the services provided by the estuary, nor quantification of services in currency terms, the use of relative scoring allowed services to be given nominal values to facilitate comparisons to be made.

An ESF Toolkit for economic empowerment must consider resilience

The collated data on the supply and demand of the ecosystem services highlighted to all stakeholders at both study sites that the estuary is a common pool that is utilized by many. Because the toolkit promotes a shared understanding of the resource and of resource users, enterprises that do not affect or have limited impact on the availability of the services used by other resource users, and vice versa, were identifiable. This knowledge is the foundation for identifying resilient enterprises.

The toolkit has demonstrated that it can be used to help identify potential estuary-based enterprises that can function under current ecosystem service supply and demand conditions. However supply and demand are constantly changing and for an enterprise to have the greatest chance of being resilient, it must be adaptable. The adaptability of an enterprise, i.e., ability of the enterprise to be managed for resilience, is difficult to gauge without an enterprise first being established. The adaptability of an enterprise is human driven and this highlights a gap in the toolkit. For an enterprise to be resilient, it must be resilient at an external SES level, which the toolkit addresses, and at an internal business functioning level, which includes social dynamics among personnel, skills, and literacy levels. Furthermore, as noted by Coulthard (2012), fundamental questions still remain around the equity of adaptation, i.e., how the gains and losses of adaptation in a resilient system are distributed within a society, and that improved resilience does not necessarily result in improved well-being of people.

Although the toolkit does not address the internal resilience of an enterprise, it does indicate which enterprises show potential resilience, given current SES conditions. Establishing whether or not an enterprise is resilient in terms of external SES conditions must always be done before an enterprise is established, for without external resilience, an internally resilient enterprise will still not succeed. If the internal operation of an enterprise is not resilient, for example if the market demands beach holidays and the holiday package is not being adapted to offer beach visits because of a lack of market knowledge, it is possible to educate personnel to provide this service. However, it is much more challenging to alter external level factors that impact on the supply and demand of ecosystem services, such as providing and maintaining access roads to the beach.

Although the toolkit was aimed at accommodating resilience, it does establish a level of common understanding that would enable a vulnerability assessment to be conducted. For example one could envisage leading from this application of the toolkit into a subsequent vulnerability assessment along the lines proposed by Ravera et al. (2011). Similarly, Cabell and Oelofse (2012) propose 13 behavior-based indicators that can be used to assess resilience and capacity for adaptation and transformation. Although developed with agroecosystems in mind the approach has obvious extensions to other SESs.

An ESF Toolkit for economic empowerment must accommodate complex social-ecological contexts

The greater the diversity of stakeholders attending and participating at a workshop, the greater the understanding of a complex SES. At both study sites there were a reasonable variety of stakeholders present. Although some stakeholders were more dominant than others, with good facilitation all participants contributed, and this resulted in a greater level of trust, respect, and knowledge sharing between stakeholders.

Although the degree to which a stakeholder understood the viewpoint of another stakeholder was not formally evaluated, by the end of the workshop the facilitator was confident that stakeholders had a good understanding of both the ecosystem services utilized by other stakeholder groups, and the complexities of the SES. Other than directly asking each stakeholder what they have learned, there is no other practical method for evaluating what information was absorbed by the different stakeholders. Although possible, this questioning would have added additional time to an already lengthy participatory process. Despite this shortcoming, there is little doubt that the process could be categorized as a good example of social learning. Keen et al. (2005:4) define social learning as the “collective action and reflection that occurs among different individuals and groups as the work to improve the management of human and environmental interrelations.” McCarthy et al. (2011) have outlined a heuristic for describing the epistemological context for social learning within complex SES, and doubtless use of this in future applications of the toolkit would improve the quality of the social learning process.

In summary the participatory approach of the toolkit helped the stakeholders to gain a good understanding of the different perspectives of the other stakeholders, and importantly, the complex interdependencies of the SES. This is an important first step in enhancing resilience, adaptability, and transformability. More specifically this mutual understanding would improve the resilience of an enterprise, because it is likely that if the operating of an enterprise negatively impacts upon service delivery for another stakeholder, with greater shared understanding there may be more chance for compromise whereby both stakeholders continue to benefit from services supplied by the estuary. Moore and Westley (2011) have highlighted the importance of networks in relationship building and brokering, and knowledge and resource brokering and how this is fundamental to social innovation. They see this as key in improving human capacity to address challenging problems and improve resilience. In the context of the estuary project, it was clear that we were seeing the incipient formation of a network that if nurtured, could generate the ‘institutional entrepreneurs’ referred to by Moore and Westley (2011).

Improvement to and further development of the toolkit

The data extracted when implementing the toolkit is primarily derived from discussions among the different stakeholders attending the workshop. A shortcoming of the toolkit is that in its present form it does not explicitly encourage the sourcing of existing ecological, demographic, social, or market data. The integration of this data into the ESF Framework would considerably strengthen the toolkits scientific founding. Such data could include censuses, market analyses, (such as B. Reyers and E. Ginsburg, unpublished manuscript), and published biodiversity assessments (such as the National Biodiversity Assessment Database which shows the habitat areas and ecological health statuses of all South African estuaries, http://rava.qsens.net/themes/coastal_template/national-biodiversity-assessment-2011-estuary-component/2011_NSBApartial01.xlsx/view).

Because our findings are based primarily on estuarine SESs, and because ecosystems greatly differ in terms of species composition, service provision, and resilience thresholds (Scheffer et al. 2000), it is not possible to directly transfer this framework to other ecosystems, e.g., wetlands, grasslands, forests. However, given the fact that only Step 1 of the toolkit directly deals with ecosystem services and is tailored specifically to estuaries, the toolkit is likely to be readily adapted for other ecosystem types. The integration of relevant ecological data for other ecosystems is also recommended.

CONCLUSION

In summary this paper documents how the theory of the Anderies et al. (2004) framework has been translated into a practical toolkit that can be used by a diversity of stakeholders as a decision making aid for assessing ecosystem services supply and demand, and associated enterprise opportunities. Thus, the toolkit addresses the hiatus previously referred to by providing an operational decision support system for the practical integration of ecosystem services into decision making processes. In doing so the approach initiates a process of social learning, considered critical in enhancing resilience, adaptability, and transformability in complex SESs.

Of course it is impossible to accurately predict if a proposed enterprise will be resilient or not, but the toolkit does however, provide a structured mechanism for identifying enterprises that have the potential to be resilient. At present the toolkit does not include steps to monitor the impacts of the enterprise on the receiving SES once established, or to assess the internal business functioning level of a particular enterprise. Additional work is required in these areas.

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ACKNOWLEDGMENTS

Dr. Steve Mitchell of the South African Water Research Commission and Mr. Andrew Mather of eThekwini Municipality for their valuable input into the development of this toolkit. The participants of the Umngazi and Tyolomnqa workshops for sharing their knowledge. Funding for this project came from the South African Water Research Commission: Estuaries and Economic Empowerment project.

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Address of Correspondent:
Rebecca Bowd
PO Box 11
Hilton, KwaZulu-Natal
South Africa 3245
rebecca@greendoorgroup.co.za
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