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Where Do Ecosystem Services Come From? Assessing and Mapping Stakeholder Perceptions on Water Ecosystem Services in the Muga River Basin (Catalonia, Spain)

Department of Geography, Institute of Environment, IMA-UdG, University of Girona, 17071 Girona, Spain
ICRA, Catalan Institute for Water Research, 17003 Girona, Spain
Author to whom correspondence should be addressed.
Land 2020, 9(10), 385;
Received: 10 September 2020 / Revised: 6 October 2020 / Accepted: 9 October 2020 / Published: 12 October 2020


Reductions in water availability and increasing rainfall variability are generating a narrative of growing competition for water in the Mediterranean basin. In this article, we explore the distribution and importance of water resources in the Muga River Basin (Catalonia, Spain) based on key stakeholders’ perceptions. We performed a sociocultural evaluation of the main water ecosystem services in the region through stakeholder interviews and participatory mapping. The basin was generally perceived as a hotspot of ecosystem services, but we detected varying opinions and considerable differences in the perceptions of importance and spatial distribution of water ecosystem services. These discrepancies were linked to the varying levels of stakeholders’ dependence on water. Our findings are important for contributing to correct water planning and management in the river basin, which is a complex water social system marked by conflicts between different stakeholder groups vying for the same resource. This complex situation requires bottom-up strategies to create transparent, participatory decision-making models.

1. Introduction

Water ecosystems in the Mediterranean basin are increasingly under threat from anthropogenic pressures in a scenario marked by profound environmental changes that are placing even greater stress on these systems and diminishing their ability to provide an adequate flow of ecosystem services (ES). The Mediterranean basin is one the most vulnerable areas of the planet [1,2] and water resources one of the main causes of socio-environmental conflicts [3]. According to recent forecasts, the Mediterranean is facing a future marked by increasing water demands, declining rainfall, rising temperatures, and longer drought periods [2,4]. Water scarcity is therefore a matter of great concern and, like many environmental issues, it is closely linked to problems of a social, economic, and political nature [4].
Most economic activities, including tourism, are heavily dependent on water and have a significant impact on its use and consumption [5]. Demand peaks in the summer months, which is precisely when the Mediterranean’s water ecosystem services (WES) are at their most vulnerable. Although coastal wetlands are one of the world’s most degraded ecosystems [6], they are a major tourist attraction due to the wealth of opportunities they offer for recreational activities such as walking, bird watching, and fishing [7].
Although human activities have a direct and indirect influence on water resources, few studies have considered their combined effects [8]. Surface and groundwater flows are needed to produce food and energy [9] and to shape landscapes and ecosystems that provide both passive services (e.g., enjoying beautiful scenery) and active services (e.g., recreational activities) [10]. Ecosystems and society, however, are closely linked and are constantly interacting with each other [11]. However, how aware is society of these links? Sociocultural evaluations of ecosystem services serve to explore differing perceptions and value systems among stakeholders, identify priorities, needs, and objectives, and integrate these into joint decision-making processes [12]. There are not many studies that specifically focus on a sociocultural assessment on water and water ecosystem services (WES) (but see [13,14]). On the other hand, numerous studies analyze ES from a sociocultural perspective, integrating the supply and demand of ES, [15,16,17,18,19,20,21,22,23]. Most of these studies use different participatory techniques such as interviews [13,24], workshops [12,25,26] or participatory mapping processes online [22] for the analysis of different ES. These different participatory techniques allow the identification of hotspot areas of supply and demand and trade-offs and bundles between ecosystem services [12,22,25] and the study social preferences with respect to ES [13,17] as well as their visualization spatially according to the different stakeholder profiles [12], often with conflicting interests. Sociocultural evaluations also help determine different levels of stakeholder dependence on their surroundings and identify divergent interests in terms of landscape planning and management [27]. Nevertheless, inside this growing methodological framework, the combination of different participatory techniques to analyze ES is not very common yet [28], and participatory methodologies are they are mostly explored in cultural ES, rather than provisioning or regulating ES, where biophysical or economic evaluations are more common [12,24,29,30]. Moreover, sociocultural analysis finds little application in decision-making processes and the gap between scientific results and how to transform them into operational landscape planning policies in a real context is still big [30]. In order to contribute to these gaps in ES sociocultural valuations, the aim of our study was to apply a methodological approach that combines different socio-cultural techniques, interview and participatory mapping, to analyze WES, which on the one hand allows us to have an in-depth socio-qualitative analysis of ES and stakeholders’ value systems about WES and, on the other hand, explores the great potential of these methods for their practical applicability in decision-making processes from a participative and social learning point of view.
The main purpose of this research was to examine stakeholder preferences and the spatial distribution of WES in the Muga River basin and to determine how changes in the supply of these services might influence stakeholders either directly or indirectly. The article is structured into four sections, each with a different aim: (i) to identify the most important WES in the basin, (ii) to explore stakeholder preferences, perceptions (from a qualitative and spatial perspective), and social values in relation to these services, (iii) to identify and map WES hotspots in terms of supply, demand, and threats, and (iv) to analyze key stakeholder concerns in relation to water resources in the Muga river basin.

2. Study Area

This case study was performed in the Muga river basin, which is located in northeast Catalonia, Spain, just south of the French border (Figure 1).
The basin covers a surface area of 854 km2 and the river runs for 64 km. It is born in the Pre-Pyrenees (in the Puig de la Llibertat mountain) at an altitude of 1200 m and flows into the Gulf of Roses through the marina in Empúriabrava. With a mean annual flow of 2.5 m3/s [31], the river has a typically Mediterranean regime, although its flow is regulated by the Darnius-Boadella reservoir, which is the main source of water supply for the entire basin. Since the mid-20th century, the Muga river basin has experienced a progressive increase in intensive crop and livestock farming and urban and tourism development, particularly along the coast. The particularities of the basin, coupled with the changes in recent decades, have fueled tensions and conflicts over increasingly scarce water resources [32,33]. The basin is a socioecological system, where the landscape has been shaped by dynamic interactions between society and ecosystems and where heritage elements related to water have historically been and continue to be of enormous social and cultural importance.
Geographically speaking, the basin can be divided into three main areas: the headwaters (the high basin), which is an eminently mountainous area with extensive forestland; a central area (the middle basin), home to one of the most Catalonia’s productive agricultural plains and the city of Figueres; and a coastal area (the low basin), a renowned international tourist destination [34]. The coastal area contains the Aiguamolls de l’Empordà Natural Park (AENP), a natural reserve that has been a member of the Ramsar International Network of Protected Wetlands since 1993 [35]. These three unique areas converge to form a dynamic river basin with extraordinary environmental, social and economic diversity. Additional information on the study area is given in Table 1.
The growth of tourism from the mid-20th century onwards changed the traditional composition of the river basin, particularly along the coast, where the proliferation of hotels, campsites, holiday homes, and tourist facilities transformed the seafront into a powerful tourist attraction [36,37]. Tourism peaks in the summer months, placing considerable demands on local water resources and generating a veritable tourism-dependent water cycle (hydro-tourist cycle) that has a decisive influence on the hydrological and social water cycles. The tourism industry is heavily dependent on water and is also a major beneficiary of the ES it provides. The basin has also experienced a growth in intensive crop and livestock farming in recent decades, which has resulted in an increase in agricultural land and changes in crop types (from dryland to irrigated crops). Intensification of livestock farming, and pig farming in particular, has also placed greater demands on water supplies and contributed to the nitrate contamination of many of the main aquifers in the basin [38].

3. Materials and Methods

The methodology used to collect and analyze data in this study is summarized in Figure 2.

3.1. Identification of WES by an Expert Panel

We assembled a panel of experts from different scientific disciplines familiar with the study area to identify the main WES in the Muga river basin for use in a subsequent participatory mapping exercise with a selection of key stakeholders. The panel was held in July 2019. It lasted for approximately 4 h and brought together six experts from different backgrounds (ecosystem services, water ecosystems, climate change, and other fields of expertise). Drawing on the work of Palomo et al. [25], the experts were first tasked with selecting the eight most important WES in the basin using previously prepared panels featuring all the ecosystem services in the area, based on the Common International Classification Ecosystem Services, v5.1 [39].
Each expert was asked to fill out a form in which they had to rate the importance of each WES on a scale of 1 to 5 and identify the trends of each ecosystem service and the scale of its beneficiaries (local, regional, national or international). They then compared notes in an open debate. In the event of discrepancies, they were encouraged to continue their discussions until they reached a consensus. The WES identified and selected according to their importance were then mapped in a participatory exercise. The same mapping process was used with the selected stakeholders (Section 3.2).

3.2. Data Collection: Interview Design, Sampling, and Participatory Mapping

The data generated by the expert panel was used to build the stakeholder interview model under the premise that, “ecosystem services research should be ‘user-inspired’ and ‘user-useful’” [25,40]. A mixed model with open and closed questions was chosen to allow interviewees to express their opinions and explore in depth themes not initially covered. The interview was structured into five parts designed to explore: (i) familiarity with the study area, (ii) familiarity with the concept of ES, (iii) perceptions of WES importance, demand, vulnerability, and spatial position, (iv) perceived problems (existing and future) and concerns about water resources, and (v) socioeconomic profile (gender, age, place of residence, etc.). The interview model was built on the work of Iniesta-Arandia et al. [17] and was reviewed by researchers outside the project.
The stakeholders were selected by non-proportional quota sampling [41,42] to ensure that all major stakeholder groups were represented. The initial list of potential participants was expanded with the help of stakeholders already identified in previous studies in the same area [43,44]. The stakeholders were categorized into two groups: (i) those that were directly dependent on the water cycle (DD stakeholders), such as crop and livestock farmers, natural park service officers, and members of the on-site recreational tourism sector; and (ii) those that were indirectly dependent on the water cycle (ID stakeholders), such as members of the business tourism sector, environmental groups, and technical and political officers (Appendix A). One of the main reasons for this grouping was to analyze whether different levels of dependence influence perceptions and concerns about possible changes in WES provision [17]. Thirty-two stakeholders were contacted and 27 agreed to participate in the interview. The five people who declined were from the hydroelectric and tourist sectors. The interviews were held between June and November 2019. Each interview was audio-recorded and transcribed in full. The facilitators responsible for leading the discussions were key to the success of the mapping exercise, where the communication between the interviewee and the interviewer was fundamental to ensure that everyone’s opinions were taken into account and to avoid mechanisms that could affect the mapping results, as explained by Brown and Kyttä [45]. Following the methodological lead of Brown et al. [30] and Raymond et al. [41], we opted for a hard copy mapping system as we consider this to be an ideal tool for stimulating debate, encouraging participation, and facilitating the location of WES [20,24,46,47]. We used a 1:50,000 topographic map on which the experts and the stakeholders interviewed were asked to position the following for each WES: (i) service provision units (SPU), (ii) service benefiting areas (SBA), and (iii) degraded SP units (dSPU) [12,25]. They marked these points on separate maps using colored dots (green, blue, and orange, respectively), with a radius of 1 cm (equivalent to 500 m in reality) [12,20,25]. They were allowed to place as many dots (points) as needed. Once all the WES had been mapped (3 maps for each WES, with a maximum of 18 maps per stakeholder), a vertical photograph was taken of each map to facilitate subsequent digitization of points in Geographic Information System (GIS) layers.

3.3. Data and Content Analysis

To analyze stakeholder preferences and perceptions, their answers to the interview questions were coded by category and the overall responses analyzed by descriptive statistics. The transcripts of the conversations that took place during the mapping exercise were analyzed by discourse analysis. Such conversations can provide invaluable insights into reasons underlying decisions and spatial values. We therefore coded each of the units—SPU, SBA, and dSPU—and the reasons given for deciding on their location. The use of coding to understand the spatial distribution of WES hotspots and areas is based on the premise that elements that are mentioned most often are presumably those considered to be most important to society and should therefore be given priority in decision-making processes [29,48]. The transcripts were coded in Maxqda software v. 10 [49] and the data processed and analyzed in Jamovi (v. [50].

3.4. Spatial Data Analysis

The results of the participatory mapping exercise were digitized and analyzed using QGIS v.3.10 [51]. Vector data in the form of shapefiles were created using the points on the maps and the associated information on WES category, name, and unit (SPU, SBA, dSPU), and stakeholder profile. A total of 11,023 points, including those marked by the expert panel, were digitized and divided into 428 layers. In line with the definition of hotspot by Palomo et al. [25], point density was analyzed by calculating kernel density rasters (qgis:heatmapkerneldensityestimation) in PyQGIS. To this end, we used a mobile window (radius) of 5000 m (chosen as the optimal size after several trials) and a cell resolution (pixel size) of 500 m (the same size as the colored mapping dots) [52]. The different heatmaps were then combined and overlaid to obtain ecosystem service hotspots (SPH), service benefiting areas hotspots (SBAH), and degraded service provision hotspot (dSPH) maps [25]. Correlations between areas were analyzed according to stakeholder group categorization (DD and ID) using the raster library in R [53]. We also analyzed correlations between WES involving trade-offs and their SPH to assess trade-offs and synergies (bundles) between ES [54]. Differences between stakeholder groups were determined using the Wilcoxon test (non-parametric equivalent of t test) [55].

4. Results and Discussion

4.1. Identification of the Most Important WES

The WES identified by the experts were water for irrigation, water for livestock, drinking water (provisioning services), biodiversity, water regulation, and water purification (regulating services), and aesthetic values and opportunities for recreational activities (cultural services). To select which WES to map, these were ordered according to the importance with which they were rated by the experts [56]. The final WES identified as most important were six: water for irrigation and drinking water (provisioning), biodiversity and water regulation (regulating), and aesthetic values and opportunities for recreational activities (cultural). Water for livestock and water purification were ranked in last position by the experts and it was therefore decided not to map them. The experts considered that the WES were of medium to high importance and showed a downward trend. They stressed that changing trends in the context of ES were closely linked to management activities implemented in a given area over time. The scale of beneficiaries was identified as local–regional for provisioning and regulating WES and regional–international for cultural WES.
Most of the stakeholders worked in the study area (59%), were men (85%), and had a university education (70%); they were aged between 32 and 76 years (Table 2).
Before being asked to identify and map the different WES, the stakeholders were asked if they were familiar with the concept of ecosystem services. Eleven knew how to define it, twelve had never heard of it, and four had heard of it but did not know how to define it accurately. Following the approach of Iniesta-Arandia et al. [17] and Raymond et al. [41], we used the term benefits-contributions instead of ecosystem services for the rest of the interview to ensure clarity and minimize educational and cultural biases [17,41].
The content and discourse analysis of the interview transcripts produced 61 codes (Appendix B). All the interviewees considered that the Muga river basin benefited people a lot or quite a lot. When asked to give an example, the most common benefits mentioned were quality of life, availability of food and the ability to produce fresh vegetables and other products, rich biodiversity of flora and fauna, beautiful scenery, a wide range of opportunities for recreational activities, and a lack of air pollution. These results are of particular interest, as most studies of ES that have used open-ended questions to date have not detected answers related to regulating services [13,30,57,58]. In general, all the stakeholders, regardless of whether or not they lived in the Muga river basin, expressed a very strong sense of belonging and considered that basin had an almost bucolic air about it. Comments included:
“We like this landscape that has been embellished by the hand of man. It is our cultural landscape, it’s what makes the Alt Empordà beautiful; This area is like the Garden of Eden, it has everything, it offers all the resources we need, it’s wonderful. I’m in love with it”.
DD and ID stakeholders ranked the WES in a similar order of importance (Wilcoxon test, p > 0.05). Water for irrigation and drinking purposes were ranked first, followed by biodiversity and water regulation. Cultural WES were perceived as important as they were a tourist attraction but they were not considered essential for well-being. Accordingly they were largely ranked in position 5 or 6, in agreement with findings by Raymond et al. [41] (Figure 3).
The number of dots used (points on the map) did not vary significantly between DD (n = 5688) and ID stakeholders (n = 5575) (Wilcoxon test, p = 0.544). Regulating services had the most points (38.1% of total), followed by cultural (36.1%) and provisioning services (25.8%). WES perceived as important but that have few points on the map (e.g., provisioning services) can be considered to be particularly vulnerable, as they are dependent on just a few supply areas. The number of points used to map a WES is not always linked to its perceived importance. Drinking water, for example, is very important, but it was mostly concentrated at a single point, the Darnius-Boadella reservoir. The interviewees also perceived landscapes with aesthetic values as being very valuable in terms of biodiversity and habitats; they therefore typically used similar points to identify regulating and cultural services. The WES with the highest number of points was biodiversity, with 2349 points (20.9%), followed by aesthetic values, with 2056 points (18.3%) (Table 3). Stakeholders in the DD group used more points to map biodiversity, water regulation, and cultural WES, while those in the ID group used more points to map provisioning WES. DD stakeholders (e.g., crop and livestock farmers) used fewer points to map WES they interacted with daily in relation to their sociodemographic profile and familiarity with WES. Better knowledge of the basin, for example, resulted in more accurate mapping, with a greater focus on the position of provisioning units and better positional accuracy and completeness of each WES. The reliability of data obtained via ES mapping, however, remains to be determined in many cases [58].

4.2. Social Perceptions and Spatial Distribution of WES

The WES hotspots mapped out were distributed differently through the basin according to category (provisioning, regulating, cultural) and unit (SPU, SBA, dSPU) (Figure 4). The provisioning WES hotspots mainly coincided with the Darnius-Boadella reservoir (around 190 points), which is the main source of irrigation and drinking water in the basin [32]. The Muga river also had two small dams that distribute water to irrigation channels in two key agricultural areas and to a number of towns and villages [59]. The agricultural plain was also considered a provisioning ES supply hotspot area (with around 230 points), as it contains numerous wells that extract water directly from the underground aquifers. Just eight of the 27 stakeholders considered that the forests and woods in the upper basin had a decisive role in guaranteeing the provision of water to the rest of the basin (around 43 points), contrasting with the views of the experts, who saw forests as having a crucial role in water storage and regulation. The stakeholders, however, did consider that forests in the upper basin (with around 70 points) and the main stem of the river, its tributaries, and the coastal wetlands (with around 530 points) were crucial for water regulation and for the presence and conservation of natural aquatic habitats. These results highlight the importance that stakeholders attach to the AENP in the lower basin and show that they recognized the important role that coastal wetlands play in biodiversity and in minimizing coastal erosion and the effects of heavy rainfall, river overflow, and sea storms [6]. The cultural hotspots identified were the AENP, the coastline, the high stretch of the river, the river mouth (about 325 points) and the Darnius-Boadella reservoir (around 163 points). These elements were mainly perceived as cultural hotspots because of their natural beauty and the opportunities for recreational activities.
There were no significant differences between DD and ID stakeholders in terms of the number of points used to map SPH, SBAH, or dSPH or in their spatial distribution. As shown in Figure 5, ID stakeholders used more points to identify degraded SPHs (with the exception of water regulation). By contrast, DD stakeholders used more points to map SBAH, which were mainly located on the coast, in urban areas, and in the agricultural plain.
As for WES categories (Figure 5), the stakeholders used more points to map regulating SPH (in particular biodiversity) and cultural SPH. In the case of SBAH, water for irrigation and human consumption, aesthetic values, and opportunities for recreational activities were mapped most. dSPH had the fewest points, but hotspots related to water regulation ES (rivers, forests in the high basin, and coastal wetlands) were considered to be the most degraded areas. All the stakeholders recognized the different anthropogenic pressures on the lower part of the Muga river and the AENP, which was considered both an SPH and a dSPH.
Our findings are consistent with those reported by Palomo et al. [25], who showed that provisioning ES tend to be located outside protected areas, while regulating and cultural ES tend to be located within these areas.
Urban dwellers and national and international tourists were all perceived as WES beneficiaries. Both DD and ID stakeholders, however, mapped regulating SPU and dSPU in the same area. Moreover, our density maps show that DD and ID stakeholders differed in their perceptions of the location of hotspots. For the DD stakeholders, these tended to be located more in natural spaces (rivers, wetlands, and forests), while for the ID stakeholders, they were spatially more spread out and particularly present along the coast.
The analysis of the participatory mapping audio-recordings revealed differences in perceptions according to type of WES category (provisioning, regulating, cultural) and unit (SPU, SBA, and dSPU). For example, in answer to the question, “Where, in your opinion, does irrigation water come from?” or “Which areas supply this benefit?”, the stakeholders typically answered: “Water clearly comes from the sky, is there any other possible answer to this question?”.
When asked to map the WES units, the stakeholders identified humanmade elements, such as the reservoir, wells, irrigation canals, and dams along the river as provisioning SPU and natural elements such as forests, mountains, and rivers as cultural SPU. In a study of the links between cultural ES and urban forest features, Baumeister et al. [52] showed that people considered humanmade elements to be an important part of cultural services. Our study shows that this was also the case for provisioning and regulating WES in the Muga river basin, which are in theory more closely linked to the ecological functioning of ecosystems than to cultural aspects. Most of the SBA elements were positioned in urban areas, in the agricultural plain, and along the coast (mainly campsites and tourist resorts). Most of the dSPU elements identified were natural features, such as the AENP, the coastline, the agricultural plain, the river and its tributaries, and the river mouth. Nonetheless, humanmade elements, such as irrigation channels, historical-cultural features (mills, factories, and fountains), the reservoir, and urban areas were also identified as dSPU (Figure 6). It is important to note that while the stakeholders coincided in their choice of dSPH, their reasons varied depending on their profile, highlighting the existence of different value systems that can generate conflicting views [13,17], as dependence on a given service would affect perceptions of possible impacts on activities.
The spatial correlation analysis allowed us to explore differences in value systems, visualize potential sources of conflict over the use of water resources, and better understand the power relations that shape decision-making processes [13,16,41] (Table 4).
Spatially, the WES supply areas were strongly correlated, indicating that they are sources of potential conflicts and trade-offs. SBAH and SPH, however, were not positioned in the same area, showing that stakeholders perceive that most WES are not “consumed” where they are generated. We also observed a greater overlap between SPH and SBAH among DD stakeholders, suggesting that they perceive lower WES mobilization than ID stakeholders. Similarly, they would appear to perceive themselves as having a close relationship with provisioning WES supply points, probably because changes in supply would affect their activities more than those of ID stakeholders.
Analysis of divergences and factors influencing preferences is crucial for identifying potential areas of conflict or tension and for understanding the reasons behind different choices [12,13,17,48]. Analysis of trade-offs between WES thus can help identify at-risk areas and potential conflicts between groups of stakeholders. The concept of “trade-off” indicates that the provision of one ES would reduce the provision of another. Therefore, when two ES involving trade-offs are strongly correlated, it means that they are being generated in the same place and may therefore lead to conflict. Trade-offs were identified by the question, “Do you think there is competition for water? And if so, what are the main problems?” [61]. Based on the answers to these questions, the relationships between WES were classified as trade-offs or bundles (Table 5).
We also tested the correlation between different SPH (Table 6).
Water for irrigation and drinking water (provisioning services) and water for irrigation and water regulation involved the most trade-offs between each other (r > 0.80). The correlation coefficients between provisioning services and biodiversity, followed by cultural WES, confirmed that these two categories do not coincide spatially. We also observed that relationships between WES could be negative (trade-offs) or positive (bundles) depending on the direction of the relationship [54]. For example, an increase in water for irrigation would reduce water regulation, but an increase in water regulation would not increase the availability of water for irrigation. A similar trend was observed for cultural WES, which coincided in terms of position and had clearly opposing trade-off directions. All the stakeholders were of the opinion that an increase in opportunities for recreational activities would result in a reduction in aesthetic values, while an increase in aesthetic values would result in increased opportunities for recreational activities (synergy). An increase in biodiversity was also perceived as positive as it would increase both aesthetic values and opportunities for recreational activities (e.g., bird watching in wetlands). By contrast, an increase in aesthetic values and opportunities for recreational activities would have a negative impact on biodiversity.
Our findings for trade-offs and bundles based on the correlation analysis and interview data shed light on possible sources of conflict or tension among stakeholders in the Muga river basin. Twenty of the 27 interviewees were of the opinion that there was competition for water. The main “concerns” expressed in response to the question “Are you worried about a decline in water resources and if so, why?” (Appendix B, q4.2) were related to climate change, in particular greater rainfall variability and more intense drought episodes. These concerns echo those raised in a recent study of tourist accommodation owners and managers in the Muga river basin who expressed concerns about the effects of climate change in the basin [62]. Nonetheless, most of them did not perceive serious risks to the future of tourism or their businesses, and some were even of the opinion that global warming could benefit them by lengthening the tourist season. We found numerous other studies that focus on a sociocultural evaluation of ES, although not specifically in WES, in other countries of the Mediterranean Basin, most of them on the Iberian peninsula [12,16,17,22]. The results of these researches underlined the need to increasingly apply this type of methodology, mostly in contexts such as the Mediterranean basin, where the relationship between WES and society is so delicate, especially referring to climate change, in one of the most affected areas that has already exceeded the 1.5 °C threshold [4].
The stakeholders interviewed in our study were very concerned about loss of biodiversity and habitat destruction and the increased demands on water due to human pressures, particularly from the urban and tourism sectors. The agricultural sector was perceived as the most problematic sector (mentioned by 20 of the 27 stakeholders); this perception is in line with the findings of the European MEDACC LIFE project [38], which estimated that 75% of all water in the Muga river basin was used for agricultural purposes. The tourism and urban sectors were mentioned as problematic by a similar number of stakeholders (17 and 16, respectively) (Appendix C). The above perceptions are supported by the results of the mapping exercise. Many stakeholders, however, claimed that conflicts due to competing demands for water arise in times of scarcity. In other words, they are closely linked to climate conditions and the availability of water at a given time. The discourse analysis of the opinions expressed by the stakeholders support the data presented thus far. The agricultural industry was identified as the main consumer of water in the basin:
“All the water from the reservoir goes to agriculture; the levels drop to dramatic levels two months a year and all the water is used for agriculture; there’s no water in the river the rest of the year, we’re outraged, they’re throwing it away”.
The farmers, by contrast, said:
“When there’s a drought, priority is given to urban and tourism uses, and we’re the ones who are most affected. We’re the only ones who change what we do to use water more efficiently, for example, by planting crops that are more suited to the effects of climate change (temperature, rain, wind, humidity”.
These were some of the burning issues that sparked debate among the various stakeholders, confirming the tensions that have historically marked the use of water in the Muga river basin [32]. Ten of the 27 stakeholders stated that competition was greatest between the agricultural sector and the tourism industry, particularly in the summer months, when water for irrigation is needed most and when the number of visitors to the area (local and international holidaymakers) is at its highest [32,36,37]. Some of the stakeholders from the agricultural sector went into quite some detail on this issue:
“More and more water is needed for general consumption and tourism; the entire coastline consumes a lot of water here in summer. The thing is, this area has always been agricultural; tourism came later and water that used to be for agriculture has been extracted from the aquifers and now there is less. The need for water has increased, but there is no control, nobody is looking at how many showers tourists are taking a day, for example. But everything we do is controlled. But in our case, a high proportion of the water we use goes back to the aquifer”.
The stakeholders also mentioned problems related to the salinization and nitrate contamination of groundwater and water from wells, which reduce the supply of water fit for human consumption and have a negative impact on natural habitats and biodiversity. These issues also spark conflicts between the agricultural sector and conservationists. On the contrary, the stakeholders were of the opinion that the agricultural sector had less influence on decisions regarding water use than the urban and tourism sectors. Thirteen of the 27 stakeholders considered that the agricultural sector had considerable power while 17 thought that was the case for the other two sectors. The majority of stakeholders thought that the conservationist sector had no decision-making power, with just 10 mentioning that they had moderate power. All the stakeholders agreed that the public administration sector had the greatest decision-making power and they mentioned a lack of communication and a prevailing top-down approach (Appendix C).

5. Conclusions

WES provide a diverse range of benefits that are crucial to our well-being. While some of these services, namely provisioning and cultural services, are clearly recognized by stakeholders, our results support previous findings that the benefits of regulating services are less evident [63], particularly to stakeholders who are less dependent on water. Our study shows the importance of understanding how perceptions and decision-making processes related to water resource management in a scenario of conflict marked by increasing demand for water and increasingly scarce water resources are influenced by sociocultural values. In a context of ever-greater complexity, one of the strengths of sociocultural evaluation and participatory techniques is that they can identify ES hotspots that are potential sources of conflict for sectors with incompatible or divergent interests.
Our findings also highlight the importance of recording and analyzing opinions expressed during participatory mapping as this provides essential information for subsequent data evaluation and interpretation. This approach enabled us to explore in detail the involvement of stakeholders in water resource management, their level of decision-making power, their knowledge and vision of the basin, and their views of bottom-up strategies [12,47].
At the end of the interview, the stakeholders were asked about their opinions on the methodology used. Most of them thought that mapping was a very useful tool for visualizing the location and distribution of problems, for obtaining information, for improving the management of natural resources, and, in particular, for creating a shared awareness of the region. Highlighting, however, the power game that exists between certain groups, six of the 27 stakeholders stated that the methodology should be accompanied by scientific validation and representativeness, stating that:
“If only the most influential actors put points where they want, lying about reality and their behaviors, and influencing the weakest, they’ll end up making their own interests prevail, like always”.
This statement reflects the difficult interaction between multiple stakeholders and the lack of transparency in how environmental problems are managed at the public administration level. We believe that more studies of how WES are understood and perceived by stakeholders are needed to gain a better understanding of the multifunctional nature of river basins and to generate new knowledge that will contribute to greater social acceptance of conservation measures and restoration of aquatic ecosystems [63].
Our findings also highlight an interesting paradox: WES are not humanmade, but many of their SPU are (e.g., the reservoir, wells, irrigation channels, water purification plants) and in many cases they can eclipse the role of ecosystems and our dependence on them. They also highlight a lack of awareness of the close link between water availability and ecosystems, and the difficulty of answering questions such as, “Where does the water in the reservoir (well/tap) come from?”
Our study shows that the generated maps can be used not only as a diagnostic tool, but also as an operational tool to help the administrative actors in decision-making processes by integrating and involving the views of stakeholders from the beginning. This could be one of the new directions of research for the future, trying to combine these sociocultural techniques and participative map processes with the operational tools and instruments for landscape planning, with the aim to build and construct a shared knowledge between public administration and stakeholders in the very initial part of decision-making processes, in order to orient political choices and landscape management towards specific needs and holistic long-term visions.
In conclusion, it is essential to integrate frequently divergent outlooks, experiences, and priorities to create tools that will ensure a holistic, cross-disciplinary vision of water systems such as a river basin. The ultimate goal is to avoid egocentric attitudes and water and territorial management models not based on the needs and perceptions of different sectors, as this will ultimately help achieve a shared consensus and build social resilience for addressing the changes that lie ahead. In line with the findings of other authors [58,64], this study shows the need to apply wisdom of the crowd approaches to water and WES management, using collective intelligence and social learning to identify problems and conflicts and to find inclusive solutions that account for the complexity of interests, opinions, and values in order to foster a better relationship between humans and nature.

Author Contributions

Conceptualization, E.G.; Data curation, E.G.; Writing—original draft, E.G., J.V.-S., J.P.-R. and A.R.P.; Writing—review and editing, E.G., J.V.-S., J.P.-R. and A.R.P. All authors have read and agreed to the published version of the manuscript.


This research was funded by the financial support of the Spanish Ministry of Economy and Competitiveness through the project “Incentives and barriers to water conservation in the tourism sector. Analysis and proposals for efficient water management” (CSO2016-75740-P).


We thank all respondents of our study for their attention and time.

Conflicts of Interest

The authors declare no conflict of interest.

Appendix A

Table A1. Stakeholder categorization.
Table A1. Stakeholder categorization.
Stakeholder Groups
DD (Directly dependent on WES)Crop/livestock farmers (agriculture)
Natural protected areas
On-site recreational tourism sector
Recreational leisure tourism sector
ID (Indirectly dependent on WES)
Tourism business sector
Environmental groups and associations
Public bodies (political level)
Public bodies (technical level)

Appendix B

Table A2. Coding of interview responses and categories derived from the content analysis (Code structure– categories–code frequency).
Table A2. Coding of interview responses and categories derived from the content analysis (Code structure– categories–code frequency).
Q1.5 If you had to describe this territory to a person who lived outside the Muga river basin, how would you describe it in a minute?
q1.5\Place of transit and communication6
q1.5\Landscape diversity/multifunctionality16
q1.5\It gives you many options0
q1.5\Physical description
q1.5\Physical description\land uses (crops, urban areas, different landscapes)8
q1.5\Physical description\coast—plain—mountain11
q1.5\Physical description\weather3
Q2.2 Do you think that this territory, defined by the Muga river basin, and its different manifestations of water, provides some kind of benefit or positive effect for your well-being and the well-being of society? If so, can you give some examples?
q2.2\Benefits limitation3
q2.2\Quality of life7
q2.2\Economic benefits-services10
q2.2\Cultural ES
q2.2\Cultural ES\hunting1
q2.2\Cultural ES\natural protected areas4
q2.2\Cultural ESs\Recreational activities-tourism8
q2.2\Cultural ES\peace and quiet2
q2.2\Cultural ES\beautiful landscapes-sense of attachment to the place6
q2.2\Regulating ES
q2.2\Regulating ES \biodiversity-Habitats8
q2.2\Regulating ES \good weather - climate regulation5
q2.2\Regulating ES \clean air5
q2.2\Provisioning ES
q2.2\Provisioning ES\wood2
q2.2\Provisioning ES\livestock farming2
q2.2\Provisioning ES\water5
q2.2\Provisioning ES\food and fresh vegetables11
Q4.2 What are the most serious water-related problems in the Muga river basin for you? Could you indicate the main ones?
q4.2\Do not know1
q4.2\Territory and landscape management1
q4.2\Human pressures6
q4.2\Human pressures \lifestyle changes2
q4.2\Human pressures \Urban-tourism growth5
q4.2\Human pressures \agriculture6
q4.2\Climate change
q4.2\Climate change\biodiversity-habitat loss6
q4.2\Climate change\fires2
q4.2\Climate change\temperature4
q4.2\Climate change\drought6
q4.2\Climate change\Rainfall regime changes-decreasing water supplies17
Q4.6 Do you think there is competition for the use of water resources? If so, do you think that this competition is or could be an incentive or a barrier when implementing water-saving measures? Please justify your answers.
q4.6\Water management proposal3
q4.6\No competition5
q4.6\Yes-no competition (depends on time of year or water available)4
q4.6\Competition\urban sector2
q4.6\Competition\tourism sector1
q4.6\Competition\agricultural sector7
q4.6\Competition\agricultural sector\agricultural sector- environmental groups4
q4.6\Competition\agricultural sector\agricultural sector-public sector1
q4.6\Competition\agricultural sector\agricultural sector-urban sector3
q4.6\Competition\agricultural sector\agricultural sector-tourism sector6
q4.6\Competition\public sector- environmental groups1
q4.6\Competition\tourism sector-urban sector-environmental groups3
q4.6\Competition\participatory processes2
q4.6\Competition\Public sector8
Q4.8 Do you think that working with ecosystem services for the well-being of people and society can help efficient water management in the river basin? Please justify your answer.
q4.8\ I don’t believe in this method3
q4.8\I don’t know how0
q4.8\To construct a better vision of the territory-better management of natural resources9
q4.8\Communication and dissemination of the study2
q4.8\To visualize problems on a map4
q4.8\To study representativeness and validity6
q4.8\To get information3
q4.8\Hydraulic works2
q4.8\To create a shared awareness-vision among people11

Appendix C

Table A3. Comparison between level of water use and consumption by stakeholder sectors (A) and their level of influence on decision-making (B) according to stakeholder perceptions.
Table A3. Comparison between level of water use and consumption by stakeholder sectors (A) and their level of influence on decision-making (B) according to stakeholder perceptions.
(A) Level of Water Use and Consumption(B) Level of Influence on Decision-Making
SectorLevelsCounts% of TotalCounts% of Total
Low 518.5
None 13.7
None 13.7
ConservationistHigh 311.1
Forest sectorHigh13.713.7
Public sectorHigh 2592.6
Medium 27.4


  1. European Environment Agency. National Climate Change Vulnerability and Risk Assessments in Europe, 2018; EEA Report No 1/2018; Publications Office of the European Union: Luxembourg, 2018; ISBN 978-92-9213-940-7. [Google Scholar]
  2. Masson-Delmotte, V.; Zhai, P.; Pörtner, H.-O.; Roberts, D.; Skea, J.; Shukla, P.R.; Pirani, A.; Moufouma-Okia, W.; Péan, C.; Pidcock, R.; et al. Global Warming of 1.5 °C An IPCC Special Report; IPCC: Geneva, Switzerland, 2018; Volume 265, ISBN 9789291691517. [Google Scholar]
  3. Ohlsson, L. Water conflicts and social resource scarcity. Phys. Chem. Earth Part B Hydrol. Ocean. Atmos. 2000, 25, 213–220. [Google Scholar] [CrossRef]
  4. Cramer, W.; Guiot, J.; Fader, M.; Garrabou, J.; Gattuso, J.P.; Iglesias, A.; Lange, M.A.; Lionello, P.; Llasat, M.C.; Paz, S.; et al. Climate change and interconnected risks to sustainable development in the Mediterranean. Nat. Clim. Chang. 2018, 8, 972–980. [Google Scholar] [CrossRef][Green Version]
  5. World Tourism Organization (UNWTO). UNWTO Regional Seminar on Climate Change, Biodiversity and Sustainable Tourism Development; World Tourism Organization (UNWTO): Madrid, Spain, 2018; ISBN 9789284420148. [Google Scholar]
  6. Zhao, Q.; Bai, J.; Huang, L.; Gu, B.; Lu, Q.; Gao, Z. A review of methodologies and success indicators for coastal wetland restoration. Ecol. Indic. 2016, 60, 442–452. [Google Scholar] [CrossRef]
  7. Pueyo-Ros, J.; Ribas, A.; Fraguell, R.M. Uses and Preferences of Visitors to Coastal Wetlands in Tourism Destinations (Costa Brava, Spain). Wetlands 2018, 38, 1183–1197. [Google Scholar] [CrossRef]
  8. Gössling, S. Global environmental consequences of tourism. Glob. Environ. Chang. 2002, 12, 283–302. [Google Scholar] [CrossRef]
  9. Gössling, S.; Peeters, P.; Hall, C.M.; Ceron, J.P.; Dubois, G.; Lehmann, L.V.; Scott, D. Tourism and water use: Supply, demand, and security. An international review. Tour. Manag. 2012, 33, 1–15. [Google Scholar] [CrossRef]
  10. Vollmer, D.; Shaad, K.; Souter, N.J.; Farrell, T.; Dudgeon, D.; Sullivan, C.A.; Fauconnier, I.; MacDonald, G.M.; McCartney, M.P.; Power, A.G.; et al. Integrating the social, hydrological and ecological dimensions of freshwater health: The Freshwater Health Index. Sci. Total Environ. 2018, 627, 304–313. [Google Scholar] [CrossRef]
  11. Millennium Ecosystem Assessment. Living Beyond Our Means: Natural Assets and Human Well-being. Annu. Rep. 2004, 24. [Google Scholar] [CrossRef][Green Version]
  12. García-Nieto, A.P.; Quintas-Soriano, C.; García-Llorente, M.; Palomo, I.; Montes, C.; Martín-López, B. Collaborative mapping of ecosystem services: The role of stakeholders’ profiles. Ecosyst. Serv. 2015, 13, 141–152. [Google Scholar] [CrossRef]
  13. Castro, A.J.; Vaughn, C.C.; Julian, J.P.; García-Llorente, M. Social Demand for Ecosystem Services and Implications for Watershed Management. J. Am. Water Resour. Assoc. 2016, 52, 209–221. [Google Scholar] [CrossRef]
  14. Castro, A.J.; Julian, J.P.; Vaughn, C.C.; Martin-Mikle, C.J.; Quintas-Soriano, C. Ecosystem Services across US Watersheds: A Meta-Analysis of Studies 2000–2014. Ecosyst. Serv. Glob. Ecol. 2018. [Google Scholar] [CrossRef]
  15. Martín-López, B.; Iniesta-Arandia, I.; García-Llorente, M.; Palomo, I.; Casado-Arzuaga, I.; Del Amo, D.G.; Gómez-Baggethun, E.; Oteros-Rozas, E.; Palacios-Agundez, I.; Willaarts, B.; et al. Uncovering ecosystem service bundles through social preferences. PLoS ONE 2012, 7. [Google Scholar] [CrossRef][Green Version]
  16. García-Nieto, A.P.; García-Llorente, M.; Iniesta-Arandia, I.; Martín-López, B. Mapping forest ecosystem services: From providing units to beneficiaries. Ecosyst. Serv. 2013, 4, 126–138. [Google Scholar] [CrossRef]
  17. Iniesta-Arandia, I.; García-Llorente, M.; Aguilera, P.A.; Montes, C.; Martín-López, B. Socio-cultural valuation of ecosystem services: Uncovering the links between values, drivers of change, and human well-being. Ecol. Econ. 2014, 108, 36–48. [Google Scholar] [CrossRef]
  18. Villamor, G.B.; Palomo, I.; Santiago, C.A.L.; Oteros-Rozas, E.; Hill, J. Assessing stakeholders’ perceptions and values towards social-ecological systems using participatory methods. Ecol. Process. 2014, 3. [Google Scholar] [CrossRef][Green Version]
  19. Garcia-Martin, M.; Fagerholm, N.; Bieling, C.; Gounaridis, D.; Kizos, T.; Printsmann, A.; Müller, M.; Lieskovský, J.; Plieninger, T. Participatory mapping of landscape values in a Pan-European perspective. Landsc. Ecol. 2017, 32, 2133–2150. [Google Scholar] [CrossRef]
  20. Pérez-Ramírez, I.; García-Llorente, M.; Benito, A.; Castro, A.J. Exploring sense of place across cultivated lands through public participatory mapping. Landsc. Ecol. 2019, 9. [Google Scholar] [CrossRef]
  21. Fagerholm, N.; Eilola, S.; Kisanga, D.; Arki, V.; Käyhkö, N. Place-based landscape services and potential of participatory spatial planning in multifunctional rural landscapes in Southern highlands, Tanzania. Landsc. Ecol. 2019, 34, 1769–1787. [Google Scholar] [CrossRef][Green Version]
  22. García-Díez, V.; García-Llorente, M.; González, J.A. Participatory mapping of cultural ecosystem services in madrid: Insights for landscape planning. Land 2020, 9, 244. [Google Scholar] [CrossRef]
  23. Xu, H.; Zhao, G.; Fagerholm, N.; Primdahl, J.; Plieninger, T. Participatory mapping of cultural ecosystem services for landscape corridor planning: A case study of the Silk Roads corridor in Zhangye, China. J. Environ. Manage. 2020, 264, 110458. [Google Scholar] [CrossRef]
  24. Plieninger, T.; Dijks, S.; Oteros-Rozas, E.; Bieling, C. Assessing, mapping, and quantifying cultural ecosystem services at community level. Land Use Policy 2013, 33, 118–129. [Google Scholar] [CrossRef][Green Version]
  25. Palomo, I.; Martín-López, B.; Potschin, M.; Haines-Young, R.; Montes, C. National Parks, buffer zones and surrounding lands: Mapping ecosystem service flows. Ecosyst. Serv. 2013, 4, 104–116. [Google Scholar] [CrossRef]
  26. García-Nieto, A.P.; Huland, E.; Quintas-Soriano, C.; Iniesta-Arandia, I.; García-Llorente, M.; Palomo, I.; Martín-López, B. Evaluating social learning in participatory mapping of ecosystem services. Ecosyst. People 2019, 15, 257–268. [Google Scholar] [CrossRef]
  27. Steinbacher, M.; Bardgett, R.D.; Tappeiner, U.; Turner, C.; Schermer, M.; Lamarque, P.; Lavorel, S.; Szukics, U. Stakeholder perceptions of grassland ecosystem services in relation to knowledge on soil fertility and biodiversity. Reg. Environ. Chang. 2011, 11, 791–804. [Google Scholar] [CrossRef]
  28. Brown, G.; Strickland-Munro, J.; Kobryn, H.; Moore, S.A. Mixed methods participatory GIS: An evaluation of the validity of qualitative and quantitative mapping methods. Appl. Geogr. 2017, 79, 153–166. [Google Scholar] [CrossRef]
  29. Brown, G.; Weber, D. Measuring change in place values using public participation GIS (PPGIS). Appl. Geogr. 2012, 34, 316–324. [Google Scholar] [CrossRef]
  30. Brown, G.; Montag, J.M.; Lyon, K. Public Participation GIS: A Method for Identifying Ecosystem Services. Soc. Nat. Resour. 2012, 25, 633–651. [Google Scholar] [CrossRef]
  31. IDESCAT. Sistemas Fluviales. AportaciónPor Temporadas. Metodología. Available online: (accessed on 10 May 2020).
  32. Saurí i Pujol, D.; Ventura Pujolar, M.; Ribas i Palom, A. Gestión del agua y conflictividad social en la cuenca del río Muga (Alt Empordá). Geographicalia 2000, 59–76. [Google Scholar] [CrossRef]
  33. Tàbara, D.; Saurí, D.; Ribas, A.; Bayés, C.; Pavón, D.; Ventura, M. The old and the new Exploring social learning and participation processes under the WFD. The case of the Muga river basin, Catalonia. In Proceedings of the V Congreso Ibérico de Gestión y Planificación del Agua, Tortosa, Spain, 8–12 December 2004. [Google Scholar]
  34. United Nations Environment Programme and World Tourism Organization Background Report Tourism in the Green Economy; World Tourism Organization (UNWTO) and the United Nations Environment Programme (UNEP): Madrid, Spain, 2012; ISBN 9789284414512.
  35. Ramsar SISR. Servicio de Información Sobre Sitios Ramsar Aiguamolls de l’Empordà. Available online: (accessed on 20 June 2020).
  36. Torres-Bagur, M.; Ribas, A.; Vila-Subirós, J. Incentives and barriers to water-saving measures in hotels in the Mediterranean: A case study of the Muga river basin (Girona, Spain). Sustainability 2019, 11, 3583. [Google Scholar] [CrossRef][Green Version]
  37. Gabarda Mallorquí, A.; Ribas Palom, A.; Daunis-i-Estadella, J. Desarrollo turístico y gestión eficiente del agua. Una oportunidad para el turismo sostenible en la Costa Brava (Girona). Rev. Investig. Turísticas 2015, 9. [Google Scholar] [CrossRef][Green Version]
  38. Pascual, D.; Zabalza Martínez, J.; Funes, I.; Vicente-Serrano, S.M.; Pla, E.; Aranda, X.; Savé, R.; Biel, C. Impacts of Climate and Global Change on the Environmental, Hydrological and Agricultura Systems in the LIFE MEDACC Case Study Basins. Available online: (accessed on 24 June 2020).
  39. Haines-Young, R.; Potschin, M. Common International Classification of Ecosystem Services (CICES) V5.1 and Guidance on the Application of the Revised Structure. Available online: (accessed on 11 October 2020).
  40. Cowling, R.M.; Egoh, B.; Knight, A.T.; O’Farrell, P.J.; Reyers, B.; Rouget, M.; Roux, D.J.; Welz, A.; Wilhelm-Rechman, A. An operational model for mainstreaming ecosystem services for implementation. Proc. Natl. Acad. Sci. USA 2008, 105, 9483–9488. [Google Scholar] [CrossRef] [PubMed][Green Version]
  41. Raymond, C.M.; Bryan, B.A.; MacDonald, D.H.; Cast, A.; Strathearn, S.; Grandgirard, A.; Kalivas, T. Mapping community values for natural capital and ecosystem services. Ecol. Econ. 2009, 68, 1301–1315. [Google Scholar] [CrossRef]
  42. Tashakkori, A.; Teddlie, C. Handbook of Mixed Methods in Social & Behavioral Research; Thousand Oaks: Thousand Oaks, CA, USA, 2003. [Google Scholar]
  43. Ventura Pujolar, M. Conflictes Socioterriorials i Participació Pública en la Gestió de L’aigua de la Conca del riu Muga (Alt Empordà); Universitat de Girona: Girona, Spain, 2005. [Google Scholar]
  44. Ricart Casadevall, S. Vers una gestió territorial del regadiu. Model i aplicació a tres casos d’estudi de l’Europa meridional; Universitat de Girona: Girona, Spain, 2014. [Google Scholar]
  45. Brown, G.; Kyttä, M. Key issues and research priorities for public participation GIS (PPGIS): A synthesis based on empirical research. Appl. Geogr. 2014, 46, 122–136. [Google Scholar] [CrossRef]
  46. Pocewicz, A.; Nielsen-Pincus, M.; Brown, G.; Schnitzer, R. An Evaluation of Internet Versus Paper-based Methods for Public Participation Geographic Information Systems (PPGIS). Trans. GIS 2012, 16, 39–53. [Google Scholar] [CrossRef]
  47. Fagerholm, N.; Käyhkö, N.; Ndumbaro, F.; Khamis, M. Community stakeholders’ knowledge in landscape assessments—Mapping indicators for landscape services. Ecol. Indic. 2012, 18, 421–433. [Google Scholar] [CrossRef]
  48. Garcia, X.; Benages-Albert, M.; Pavón, D.; Ribas, A.; Garcia-Aymerich, J.; Vall-Casas, P. Public participation GIS for assessing landscape values and improvement preferences in urban stream corridors. Appl. Geogr. 2017, 87, 184–196. [Google Scholar] [CrossRef]
  49. Software, V. MAXQDA 2020 [computer software]. Berlin, Germany: VERBI Software. Available online: (accessed on 15 July 2020).
  50. The Jamovi Project. jamovi (Version 1.2) [Computer Software]. 2020. Available online: (accessed on 15 July 2020).
  51. QQGIS Development Team. QGIS Geographic Information System. Open Source Geospatial Foundation Project. 2020. Available online: (accessed on 15 July 2020).
  52. Baumeister, C.F.; Gerstenberg, T.; Plieninger, T.; Schraml, U. Exploring cultural ecosystem service hotspots: Linking multiple urban forest features with public participation mapping data. Urban For. Urban Green. 2020, 48, 126561. [Google Scholar] [CrossRef]
  53. R Core Team 2020. R: A Language and Environment for Statistical Computing. Vienna, Austria. Available online: (accessed on 15 July 2020).
  54. Milcu, A.I.; Hanspach, J.; Abson, D.; Fischer, J. Cultural ecosystem services: A literature review and prospects for future research. Ecol. Soc. 2013, 18. [Google Scholar] [CrossRef][Green Version]
  55. Bauer, D.F. Constructing confidence sets using rank statistics. J. Am. Stat. Assoc. 1972, 67, 687–690. [Google Scholar] [CrossRef]
  56. Zilio, M.I.; Alfonso, M.B.; Ferrelli, F.; Perillo, G.M.E.; Piccolo, M.C. Ecosystem services provision, tourism and climate variability in shallow lakes: The case of La Salada, Buenos Aires, Argentina. Tour. Manag. 2017, 62, 208–217. [Google Scholar] [CrossRef]
  57. Pueyo-Ros, J.; Ribas, A.; Fraguell, R.M. A cultural approach to wetlands restoration to assess its public acceptance. Restor. Ecol. 2019, 27, 626–637. [Google Scholar] [CrossRef]
  58. Brown, G.; Fagerholm, N. Empirical PPGIS/PGIS mapping of ecosystem services: A review and evaluation. Ecosyst. Serv. 2015, 13, 119–133. [Google Scholar] [CrossRef]
  59. Pavon, D. La gran obra hidràulica a les conques de la Muga i del Fluvià: Dels projectes a les realitzacions (1850-1980); Tesis doctoral, Universitat de Girona: Girona, Spain, 2007. [Google Scholar]
  60. Palomo, I.; Felipe-Lucia, M.R.; Bennett, E.M.; Martín-López, B.; Pascual, U. Disentangling the Pathways and Effects of Ecosystem Service Co-Production, 1st ed.; Elsevier Ltd.: Amsterdam, The Netherlands, 2016; Volume 54, ISBN 9780081009789. [Google Scholar]
  61. Kandziora, M.; Burkhard, B.; Müller, F. Interactions of ecosystem properties, ecosystem integrity and ecosystem service indicators: A theoretical matrix exercise. Ecol. Indic. 2013, 28, 54–78. [Google Scholar] [CrossRef]
  62. Torres-Bagur, M.; Ribas Palom, A.; Vila-Subirós, J. Perceptions of climate change and water availability in the Mediterranean tourist sector: A case study of the Muga River basin (Girona, Spain). Int. J. Clim. Chang. Strateg. Manag. 2019, 11, 552–569. [Google Scholar] [CrossRef]
  63. Grizzetti, B.; Lanzanova, D.; Liquete, C.; Reynaud, A.; Cardoso, A.C. Assessing water ecosystem services for water resource management. Environ. Sci. Policy 2016, 61, 194–203. [Google Scholar] [CrossRef]
  64. Surowiecki, J. The Wisdom of Crowds; Anchor: New York, NY, USA, 2005. [Google Scholar]
Figure 1. Territorial framework of the Muga river basin.
Figure 1. Territorial framework of the Muga river basin.
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Figure 2. Methodological workflow.
Figure 2. Methodological workflow.
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Figure 3. Perceived importance of water ecosystem services among stakeholders.
Figure 3. Perceived importance of water ecosystem services among stakeholders.
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Figure 4. Intensity raster maps of water ecosystem service categories, Provisioning (A), Regulating (B), and Cultural (C) (left) and SPH hotspots (D), SBAH hotspots (E), and dSPH hotspots (F) (right) as perceived by stakeholders. SPH indicates service provision hotspots, SBAH, service benefiting areas hotspots, and dSPH, degraded service provision hotspots.
Figure 4. Intensity raster maps of water ecosystem service categories, Provisioning (A), Regulating (B), and Cultural (C) (left) and SPH hotspots (D), SBAH hotspots (E), and dSPH hotspots (F) (right) as perceived by stakeholders. SPH indicates service provision hotspots, SBAH, service benefiting areas hotspots, and dSPH, degraded service provision hotspots.
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Figure 5. Distribution (number of points) of SPH, SBAH, and dSPH by water ecosystem category (left), unit (center), and stakeholder profile (right). DD, directly dependent; ID, indirectly dependent; dSPH, degraded service provision hotspot; SBAH, service benefiting areas hotspot; SPH, service provision hotspot.
Figure 5. Distribution (number of points) of SPH, SBAH, and dSPH by water ecosystem category (left), unit (center), and stakeholder profile (right). DD, directly dependent; ID, indirectly dependent; dSPH, degraded service provision hotspot; SBAH, service benefiting areas hotspot; SPH, service provision hotspot.
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Figure 6. Gradient of elements mentioned as predominantly natural or humanmade and frequency of mentions as service provision hotspots SPH, service benefiting areas hotspots SBAH, or degraded service provision hotspots dSPH (adapted from Palomo et al. [60].
Figure 6. Gradient of elements mentioned as predominantly natural or humanmade and frequency of mentions as service provision hotspots SPH, service benefiting areas hotspots SBAH, or degraded service provision hotspots dSPH (adapted from Palomo et al. [60].
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Table 1. Characteristics of the Muga river basin.
Table 1. Characteristics of the Muga river basin.
River Length65 km (from La Garrotxa d’Empordà Mountains to Castellò d’Empúries Beach)
Extension758 km2
Landscape typologyMountain (holm oak, cork oak, and pine trees and bushes)
Agricultural plain (irrigated crops: corn, sorghum, sunflowers, rice; fruit trees: apple, nectarine, peach; vineyards, olive trees and rain-fed cereals)
Coastline (coastal dunes and wetlands, tourist and residential buildings, tourist facilities and campsites)
Protected areasAlbera Natural Park, Alta Garrotxa Natural Park, Salines-Bassegoda Natural Park, and Aiguamolls de l’Empordà Natural Park (Ramsar wetlands site)
Population140,000 inhabitants
Land uses71% forest, 24% crops (estimated 75% of all water consumption in basin), 10% urban (estimated 20% of all water consumption in basin) (Pascual et al., 2016)
Sources of socio-environmental conflicts and tensionsWater contamination due to high nitrate levels in agricultural soil (pig farming); excessive groundwater extraction; morphological changes to river; invasive species; morphological changes to coastline.
Table 2. Sociodemographic characteristics of stakeholders (n = 27).
Table 2. Sociodemographic characteristics of stakeholders (n = 27).
Age (years) 4723.5
Educational levelPrimary school311.1
Secondary school13.7
Vocational training27.4
No studies13.7
No answer13.7
Place of residenceInside study area1659.3
Outside study area1140.7
Stakeholder groupDirectly dependent (DD) on water ecosystem services1451.9
Indirectly dependent (ID) on water ecosystem services1348.1
Table 3. Number of points mapped for each water ecosystem service category and unit by stakeholders directly and indirectly dependent on these services (directly dependent (DD) and indirectly dependent (ID) stakeholders).
Table 3. Number of points mapped for each water ecosystem service category and unit by stakeholders directly and indirectly dependent on these services (directly dependent (DD) and indirectly dependent (ID) stakeholders).
Number of Points Mapped
CategoryWater Ecosystem ServicesGroup
Provisioning 13721535
Water for irrigation603637
Drinking water769838
Regulating 22642027
Water regulation1019983
Cultural 20522013
Aesthetic values10231033
Recreational uses1029980
Table 4. Spatial correlations between water ecosystem service SPH, SBAH, and dSPH according to perceptions of directly dependent (DD) and indirectly dependent (ID) stakeholders.
Table 4. Spatial correlations between water ecosystem service SPH, SBAH, and dSPH according to perceptions of directly dependent (DD) and indirectly dependent (ID) stakeholders.
SPH-DD 0.9440.8080.6470.8920.801
SPH-ND 0.7420.6310.8320.794
SBAH-DD 0.9190.9240.835
SBAH-ND 0.8160.857
dSPH-DD 0.883
Abbreviations: DD, directly dependent; ID, indirectly dependent; dSPH, degraded service provision hotspot; SBAH, service benefiting areas hotspot; SPH, service provision hotspot.
Table 5. Direct interactions between water ecosystem services (WES) in the Muga river basin as perceived by stakeholders.
Table 5. Direct interactions between water ecosystem services (WES) in the Muga river basin as perceived by stakeholders.
IrrigationDrinking WaterBiodiversityWater RegulationAesthetic ValuesRecreational Uses
Water for Irrigation Land 09 00385 i001 Land 09 00385 i001 Land 09 00385 i001 Land 09 00385 i002 Land 09 00385 i002
Drinking water Land 09 00385 i001 Land 09 00385 i001 Land 09 00385 i002 Land 09 00385 i001 Land 09 00385 i002
Biodiversity Land 09 00385 i002 Land 09 00385 i002 Land 09 00385 i002 Land 09 00385 i003 Land 09 00385 i003
Water regulation Land 09 00385 i003 Land 09 00385 i003 Land 09 00385 i003 Land 09 00385 i001 Land 09 00385 i001
Aesthetic values Land 09 00385 i002 Land 09 00385 i002 Land 09 00385 i002 Land 09 00385 i002 Land 09 00385 i001
Recreational uses Land 09 00385 i002 Land 09 00385 i001 Land 09 00385 i001 Land 09 00385 i001 Land 09 00385 i001
Land 09 00385 i001An increase in (Y) has a reducing effect on (X). Strong probability for exclusion and competition perceived by stakeholders (trade-offs) → Negative relationships
Land 09 00385 i003An increase in (Y) has a supporting effect on (X). Strong probability for mutual support perceived by stakeholders (bundles) → Positive relationships
Land 09 00385 i002An increase in (Y) has no relevant direct effect on (X) → No significant direct interactions perceived by stakeholders
Table 6. Spatial correlation between provisioning water ecosystem service hotspots (SPH) generating trade-offs. Yellow color represents trade-offs; green color represents synergies (bundles); grey color represents partial spatial match.
Table 6. Spatial correlation between provisioning water ecosystem service hotspots (SPH) generating trade-offs. Yellow color represents trade-offs; green color represents synergies (bundles); grey color represents partial spatial match.
SPH_ IrrigationSPH_ Drinking WaterSPH_ BiodiversitySPH_ Water RegulationSPH_ Aesthetic ValuesSPH_ Recreational Uses
SPH_Irrigation 0.84491330.65561890.81135720.63829320.6106935
SPH_Drinking water 0.51011860.78115660.65452070.6117226
SPH_Biodiversity 0.88891950.90659110.9027135
SPH_Water regulation 0.89277450.8598754
SPH_Aesthetic values 0.9833962
SPH_Recreational uses
Spatial match and trade-offs → Negative relationships
Spatial match and synergies (bundles) → Positive relationships
Partial spatial match

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MDPI and ACS Style

Garau, E.; Vila-Subiros, J.; Pueyo-Ros, J.; Ribas Palom, A. Where Do Ecosystem Services Come From? Assessing and Mapping Stakeholder Perceptions on Water Ecosystem Services in the Muga River Basin (Catalonia, Spain). Land 2020, 9, 385.

AMA Style

Garau E, Vila-Subiros J, Pueyo-Ros J, Ribas Palom A. Where Do Ecosystem Services Come From? Assessing and Mapping Stakeholder Perceptions on Water Ecosystem Services in the Muga River Basin (Catalonia, Spain). Land. 2020; 9(10):385.

Chicago/Turabian Style

Garau, Enrica, Josep Vila-Subiros, Josep Pueyo-Ros, and Anna Ribas Palom. 2020. "Where Do Ecosystem Services Come From? Assessing and Mapping Stakeholder Perceptions on Water Ecosystem Services in the Muga River Basin (Catalonia, Spain)" Land 9, no. 10: 385.

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