Abstract
To better account for how social–ecological legacies of social and ecological systems jointly shape the current composition, the quality and quantity of nature’s contribution to people (NCPs), we integrate the concept of NCP co-production into social–ecological system thinking. Our expanded framework highlights how NCP co-production is frequently entangled within its social–ecological context, such as legacies, current resources and social activities. Additionally, we underline the relevance of non-material and material dimensions of resources in NCP co-production. To illustrate the potential of this expanded framework, we explore its application to an agricultural system of the French Northern Alps. We conclude that this framework (1) facilitates the understanding of society–ecosystem interactions in a specific regional social–ecological context; (2) helps to better conceptualise the interdependencies between resources and social activities; (3) demonstrates how current rule sets to organise social–ecological legacies affect the entire NCP co-production chain. The framework’s further implementation requires more research to better understand the complex interlinkages between the social and the ecological subsystems that underpin socioeconomic activities.
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Introduction
Societies and surrounding ecosystems have co-evolved over a long period in their various interdependent material and non-material aspects. To support pathways to sustainability, there is a critical need to understand how this interplay of resources and social dynamics underpins current socioeconomic activities in their specific social–ecological context (Ostrom 2009; Meyfroidt et al. 2018; Mastrángelo et al. 2019). To explain these dynamic interrelationships, we use the multidimensional concept of “co-production” of “nature’s contributions to people” (NCP). Broadly defined, NCP encompass “all contributions, beneficial or harmful, that individuals, communities, societies, nations or humanity as a whole derive from nature” (Díaz et al. 2018). Expanding on the ecosystem service concept, the NCP concept explicitly acknowledges that flows from nature can have not only different qualities (material, non-material and regulating), but also offer different aspects of appreciation to people (MEA 2005; Díaz et al. 2018; Pascual et al. 2021 Mar 25). In addition, the NCP approach acknowledges that the material and non-material categories are fluid, thus, e.g. a material NCP such as milk can also have a non-material aspect such as the maintenance of identities (Díaz et al. 2015). The co-production concept as applied to NCP describes how people use different resources in diverse ways to generate with ecological systems outcomes that people consider as meaningful (Barnaud et al. 2018; Muhar et al. 2018). Palomo et al. (2016) and Jones et al. (2016) initiated the formalisation of NCP co-production (CP); they defined NCP co-production as the process by which societies and individuals organise and manage resources to mobilise material and non-material flows from nature to contributions to people’s good quality of life. The hyphen in ‘co-production’ stresses that these social activities for the production of NCP can vary to different extents (Palomo et al. 2016). For example, some NCP can benefit society without social intervention, such as some regulating NCP such as soil erosion reduction, regulation of hydrological flows and nutrient cycling. However material NCP (e.g. food production) require in most cases some minimum human intervention (Bruley et al. 2021a).
Research has yet to fully integrate NCP co-production in its social–ecological context. This means considering the diverse surrounding material and non-material resources and the associated social activities (Díaz et al. 2015). Research that has targeted the society–ecosystem interface has often analysed NCP co-production using a capital-based approach (Guerry et al. 2015; Jones et al. 2016). This approach distinguishes between social capital and manufactured capital, but neglects that non-material and material resources are mutually dependent (Chaigneau et al. 2019). For example, a material resource, such as a farm or other physical infrastructure, can also be the carrier of non-material aspects such as knowledge, habits or the feeling of belonging for different people (Winner 1980).The integration of social activities can facilitate understanding these multiple dimensions. As an example, co-production was used to evaluate the impact of varying degrees of human input (technology, infrastructure, etc.) in different Portuguese small-scale fisheries on one material NCP (Outeiro et al. 2017). In the French Alps, research suggests that material NCP require potentially more human intervention than non-material or regulating NCP (Bruley et al. 2021a). (Fedele et al. 2017) applied the concept of co-production along the different mechanisms of the ecosystem service cascade framework (Haines-Young and Potschin 2010). What unites these various approaches is the explicit or implicit acknowledgement of non-material aspects such as traditional knowledge (Outeiro et al. 2017), identities (Fischer and Eastwood 2016), shared values (Bruley et al. 2021a), value articulation (Ernstson 2013) or other cognitive dimensions (Palomo et al. 2016) to co-produce NCP. A systematic interpretation of co-production that accounts how societies apply these non-material and material dimensions in NCP co-production has yet to come (Bennett et al. 2015; Mastrángelo et al. 2019). We assert that the perspective of regional coupled social–ecological systems (SES) provides a means to contextualise and explain NCP co-production (Reyers et al. 2013).
The SES approach considers social (e.g. institutions) and ecological (ecosystems) factors as deeply interlinked (Berkes et al. 2000; McGinnis and Ostrom 2014; Colding and Barthel 2019). They are composed of multiple subsystems with overlapping processes (such as farms, municipalities or pasture land) that interact across scales (Folke 2006; Ostrom 2009). From a spatial and organisational perspective, they are nested in or are linked to other political, socioeconomic, technological, cultural and biophysical structures (Folke 2006; Plieninger et al. 2015). The drawing of system boundaries can be challenging (Walker et al. 2002). Frequently, research designs them based on political or administrative units (Dearing et al. 2014; Hanspach et al. 2016), biophysical measures (Martín-López et al. 2017), institutional management divisions (Ostrom 2009), or broad concepts such as resilience (Alessa et al. 2009). Social–ecological system studies often do not appropriately address the definition of system boundaries (Colding and Barthel 2019).
SES are embedded in social–ecological legacies that continue to influence current types and forms of NCP co-production. These social and ecological memories are the result of numerous interactions between and within social and ecological processes for centuries to millennia (Cook et al. 2012). We consider social–ecological legacies as resources that contain social and ecological elements that co-evolved in time and space, resulting in integrated entities. These can be places like alpine pastures (Quétier et al. 2010; Egarter Vigl et al. 2016), cultural landscapes (Tengberg et al. 2012; Plieninger et al. 2015) or resources for management, such as local livestock breeds (Vilá and Arzamendia 2020 Oct 26) or agricultural knowledge (Berkes et al. 2000; Kim et al. 2017). Legacy effects of past society–ecosystem interactions such as modified ecosystems, altered ecosystem functions or social path dependencies have shaped and will continue to shape the type and modes of NCP co-production (Renard et al. 2015; Wu et al. 2020; Bruley et al. 2021b). Current resources may become legacies if their material or non-material forms and functions continue to influence future processes (Foster et al. 2003). For example, pasture fertility is a current material, ecological resource supporting fodder production, which will carry over to future soil nutrient status due to slow biogeochemical dynamics (Spiegelberger et al. 2006; Quétier et al. 2007). The same holds true for social resources such as cultural specificities or attachments to places that can transform into common value sets, institutional settings and routinised behaviour (Upton 2008). Non-material dimensions such as knowledge (Hernández-Morcillo et al. 2014) or collective identities (Pachoud 2019) depend on the type of social activities. They are frequently linked to visible social–ecological legacies such genetic diversity (Essl et al. 2015) and regional cultural landscapes (Oppermann et al. 2012; Plieninger et al. 2015). Policies related to agricultural land use have recognised these historically evolved co-production processes in more or less explicit ways. A notable example in Europe is the classification of farmland as High Nature Value (HNV) (Feranec et al. 2016) or regulations for protected areas that require sustained human intervention (Europarc 2018). The European food quality label “Protected Designation of Origin” (PDO) promotes distinct regional agricultural products and can be regarded as an attempt to preserve social–ecological legacies through economic mechanisms (Quiñones Ruiz et al. 2018). Still, the role of social–ecological legacies for NCP co-production remains underexplored in conceptual and empirical research (Herrero-Jáuregui et al. 2018; Mastrángelo et al. 2019). To fill this knowledge gap, we propose a conceptual framework that links NCP co-production to the SES approach. This allows us to effectively integrate social–ecological legacies and more robustly distinguish between social (infrastructure, knowledge, etc.) and ecological (biomass, livestock, etc.) resources (Anderies et al. 2004; McGinnis 2011).
The rest of the paper is organised as follows: first, we present an expanded SES framework to fully account for the role of social–ecological legacies and social activities in the NCP co-production. In particular, we discuss the challenges regarding the delineation of system boundaries within these frameworks between the organisational (social, ecological), temporal (legacies, current resources) and spatial (biophysical, economic) dimensions. In the subsequent section, we apply this framework to a regional SES. In Europe, agricultural mountain production systems rely on social–ecological legacies to ensure the maintenance of regional rural economies. The integration of social–ecological legacies and interlinked social activities can explain varying transformation strategies of the same products (Madelrieux et al. 2018) or entirely different agricultural production systems in adjacent regions with similar physical endowments (Bruley et al. 2021b). It allows us to show how different trajectories are based on the previous experiences of a system and how they are linked to different appreciations and values of NCP co-production. Specifically, we illustrate the applicability of our framework for a regional mountain SES and its cheese production.
An expanded SES Framework for NCP co-production in agricultural systems
We present a framework to embed NCP co-production in its social–ecological context. We defined the social–ecological context as social–ecological legacies, current resources and social activities. We separated the social from the ecological subsystem (Fig. 1, boxes) following previous epistemological and analytical considerations on NCP co-production (Díaz et al. 2015; Palomo et al. 2016; Bruley et al. 2021a) and the current IPBES framework (Díaz et al. 2015). We decided on this delineation because social activities are widely considered as dominant drivers of change in SES (Folke 2006; Kofinas and Chapin 2009; Spangenberg et al. 2014). Further, the two systems exhibit their own processes that can (1) act independently (Anderies et al. 2004; Colding and Barthel 2019), (2) have different rates of change, (Ostrom 2000; Foster et al. 2003; Walker et al. 2006) and (3) imply different understandings of scale (Winkler et al. 2021 Mar 16). We link these two subsystems with four subsequent steps (Fig. 1, black arrows) that describe social activities.
We used an economic delineation of the boundaries based on material NCP, which are frequently agricultural or forestry products. This permits the identification of social activities and their actors. It allows for the possible modifications of social activities for future adaptation. More broadly, agricultural activities frequently present an “umbrella” for other non-monetarised NCP (such as pest control, pollination) (Lescourret et al. 2015). However, economic boundaries are more diffuse than biophysical boundaries and not spatially explicit. Our top-down approach is in contrast to other (bottom-up) NCP studies based on biophysical boundaries that subsequently identify NCP in a given spatial area (Reyers et al. 2013). Economic boundaries are non-spatial, and actors involved in different NCP may share the same resources (Eakin et al. 2017). In the context of an Alpine region, for example, tourism shares the same pastureland as the agricultural system, but each of these socioeconomic activities represents different, yet linked, types of NCP co-production. To accentuate social activities interacting with their surrounding ecosystem, we limit this framework to the regional scale. To consider demand (see Fig. 1, white box), we integrate monetary flows (such as subsidies, tourist spending, etc.) that can influence the resource use in NCP co-production (Carrasco et al. 2017). For example, increased profits may lead to increased technology use (e.g. investments in new time saving machinery that leads to increases in farm size). Non-monetary, exogenous factors such as climate change (e.g. droughts), water pollution, higher-scale governance decisions or the externalised production of energy intensive products highlight the porosity of these human boundary constructs (Martín-López et al. 2017). Lastly, we assume there are unidentified flows (Fig. 1, grey arrows) between the social and the ecological system that cannot be analysed with our conceptual framework.
Social–ecological legacies and current resources
Disentangling social–ecological legacies (landscape, livestock breeds, farm infrastructure, etc.) into social and ecological components is complex and often not straightforward (Remme et al. 2014; Jones et al. 2016). Based on Remme et al. (2014), we assign social–ecological legacies to the ecological or the social subsystem by identifying those for which ecological processes play a significant role. This allocation also acknowledges that current ecological processes cannot be substituted by technological or social innovations (Edens and Hein 2013). We incorporated this consideration into our framework. For example, we consider farm infrastructure as a social–ecological legacy in the social subsystem, which contains ecological resources (timber) previously mobilised by human intervention. Biomass is an ecological resource and if not extracted will become a social–ecological legacy (potentially leading to an increase in soil carbon) in the ecological subsystem. We easily identify these boundaries for common material resources (milk, biomass, etc.) utilised for later NCP co-production processes. In contrast, these distinctions are less evident for ongoing livestock husbandry. We regard mobilised resources of livestock husbandry (e.g. wool, milk, meat) as leaving the ecological subsystem, while grazing livestock (and its manure) remain in the ecological subsystem. When livestock is sold (and serves than as an NCP for various aspects of appreciation), we consider it as leaving the ecological subsystem. However, the non-material dimension, such as genetic diversity, remains in the subsystem. The knowledge and values to maintain this breed is a social–ecological legacy in the social subsystem and exhibits its own processes. While the notion of social–ecological legacy strongly emphasises the intimate interlinkages between the social and the ecological system, we opted for didactic purposes for an analytical (and accordingly graphical) presentation of two separate spheres. In doing so, we also align with Riechers et al.’s (2020) reasoning that most resource types (e.g. infrastructure, genetic diversity) are best measured in social, respective ecological indicators.
Legacies and current resources can influence each other and are linked. For example, current practices such as irrigation and fertilisation along with the legacies of former land use and social values affect the amount of the current resource of biomass (Quétier et al. 2007). In addition, society can agree on maintaining extensive, labour intensive management practices based on previous experience coupled with current resources. For example, Alpine agricultural systems maintain traditional haymaking for winter livestock feed, but they have considerably reduced manual labour by increasing mechanisation. Aspects of appreciation from NCP co-production can thus feedback into the social subsystem and influence how and which social–ecological legacies and current resources are used. In Table 1, we present an illustrative overview about possible variables for the analysis for co-production of a regional agricultural NCP (more information on indicators is provided in SM1).
Activities along the NCP co-production chain
Social activities make use of social–ecological legacies and current resources along the different steps of co-production. They define and affect the types of co-production (Spangenberg et al. 2014; Plieninger et al. 2015). Following the ecosystem service cascade framework (Potschin-Young et al. 2018) and its refinement for accounting explicitly for human agency in the delivery of benefits from ecosystems to people (Fedele et al. 2017; Bruley et al. 2021a), we structured NCP co-production as a four-step process (illustrated by the four arrows in Fig. 1). This disaggregation enables the more precise identification of the various actors (e.g. individual or collective) and eventually assessing their role along the entire NCP co-production process.
We define a pre-conditioning step zero of co-production (CP0; organising) that describes how different actors, either collectively or individually, agree on a rule set over the types and modes of co-production (Bergeret and Lavorel in press). CP0 may stem from former NCP co-production, and then be considered as a mix of social–ecological legacies (such as already established rule sets that predominate a landscape) and represent actors’ network and dynamics. This step is biophysically and spatially separate from the local ecological subsystem, but social–ecological legacies affect and frame this rule set. In democratic structures, this organisation of resources requires collective agreement on common values and knowledge (Ostrom 2000). It depends on the social–ecological context, and tereby the social–ecological legacies, current resources and the involved actors. The crooked arrow indicates these rule sets are the consolidated result of often long negotiations among local stakeholders and government or regulatory authorities. Empirical research analyses formalised relationships to capture the non-material collective values of a given social subsystem (Ostrom 1990). However, we suggest that these formalised collective values can only present a compromise between the different actors and do not capture the totality of collective values.
Co-production at step one (CP1) is the stage of biophysical ecosystem management, such as fertilisation of agricultural fields. For example, actors apply different management practices based on the agreed rule set, their current resources (available labour, technology and/or knowledge about management practices, etc.) and their personal considerations on the management of the cultural landscape as shaped by social–ecological legacies. Thus, the combination of CP0 and individual perceptions of the involved actor underpin the management of the social–ecological legacy landscape.
Co-production at step 2 (CP2) is where activities of extraction of current resources (e.g. biomass) from the social–ecological legacies (livestock breed, landscape) occur, such as milking or haymaking. Mobilisation does not necessarily depend on the current biophysical management at CP1, but on social–ecological legacies such as the amount of pastureland, infrastructure or knowledge. Picking berries in a forest does not require targeted management for the production of these fruits, but this activity necessitates access in physical (e.g. a path) and more intangible (e.g. knowledge about the edibility or location) terms. However, current resources can modify the type and quality of current ecological resources (e.g. fertilisation increases biomass yields). CP2 usually requires some social resources, such as permanent infrastructure, e.g. a form of physical access to mobilise ecological outputs (Bruley et al. 2021a).
Co-production at step 3 (CP3) relates to the translation to a final NCP benefit, e.g. the sale or transformation of milk and other aspects of appreciation (happiness to be in nature, place of belonging, etc.) that co-producing actors consider as relevant. It requires multiple, frequently subtle cognitive factors e.g. feeling of attachment (Fedele et al. 2017). These appreciations feedback into the social subsystem as current resources.
NCP co-production is dynamic and not linear. The entire process is based on and will produce future social–ecological legacies. Each of the following steps is an outcome of the previous steps. Here, we chose the chronological numbering to align with previous conceptualisations of NCP co-production (Bergeret and Lavorel in press; Bruley et al. 2021a) and reasoning on society–ecosystem interactions (Haines-Young and Potschin 2010; Fedele et al. 2017). Nevertheless, we emphasise the interdependent, frequently concurrent (accumulating) circular processes of NCP co-production.
The Maurienne Beaufort cheese production system
Beaufort cheese production takes place in three adjacent valleys (Beaufortain, Tarentaise and Maurienne) of the Northern French Alps. Since 1968, the EU label “Protected designation of origin” (PDO) entails binding product specifications. This commonly agreed rule set guarantees the characteristics of the final product and the maintenance of associated management and production techniques (INAO 2015; Lynch and Harvois 2016). In the following, we exclusively discuss the Beaufort production system in the Maurienne valley; however, the rule set applies to the whole production area. The Maurienne valley with its three cooperatives representing about 80 producers (900 t of cheese/yr) has been an integral part of the Beaufort PDO since its inception in 1968. All 14 cooperatives in the three valleys are associated to a consortium. The consortium offers and regulates legal and technical assistance and control of the product specifications. The Maurienne valley shaped by the Arc River spans almost 120 km and is the longest Alpine valley in France. Its 40,000 inhabitants live in predominantly rural settings with only 3 of the 56 municipalities exceeding 2000 inhabitants (SPM 2020). The climate ranges from a humid pre-Alpine climate in the west to a continental alpine climate in the east. Representing one-third of the whole area, grasslands are a characteristic feature of landscape (Fig. 2). Today, the local economy largely reflects the general picture of European mountainous areas with a large part of the work force (25%) linked to the service sector, 19% to the industrial sector and 2% to the primary sector (EC 2009; SPM 2020).
To apply our framework to the Maurienne Beaufort production system, we conducted 20 semi-structured interviews with actors associated with the system. We first identified 100 actors directly economically affiliated with Beaufort production and selected interviewees based on Internet searches and subsequent purposive snowballing (Bryman 2016). Seventeen of them were active in the Maurienne Beaufort production system during the research period, among which 4 actors in managing positions of the three cooperatives, 1 of the consortium and 12 Beaufort producers. In addition, we included three actors as “time witnesses” who were actively involved in the establishment of the Beaufort production system from the 1960s onwards. The interviews were conducted between February and September 2019 (see SM2). The interviews focused on the role and background of respective actors and their views on and relations to the Beaufort production system (interview guide is provided in SM3).
Using qualitative manual coding with NVivo, we identified the main activities and associated resources used along NCP co-production by a predefined typology (Clarke and Braun 2014; QSR International 2020). This typology was built on previous studies of agricultural NCP co-production and iteratively improved during coding (Palomo et al. 2016; Vallet et al. 2019; Bruley et al. 2021a). We drew the economic system boundaries as encompassing all resources, e.g. livestock, biomass or carbon storage and actors associated with the Beaufort production system in the valley.
Organising resources (CP0)
In our framework, we defined CP0, the organisation of a regional collective rule set, depending on social–ecological legacies and current resources of the social subsystem with its actors. The Beaufort consortium oversees the rule set of product specifications for the entire production area. It regularly consults its board composed of representatives of the cooperatives and producers (INAO 2015; Lynch and Harvois 2016). This rule set has not been externally imposed, but actors have negotiated it over the years. An actor casually remarked: “It’s the history, which governs the conduct of the people.”
In the interviews, actors repeatedly referred to three main rules that shape the type of agriculture and the associated resource use along the NCP co-production steps (INAO 2015). The first rule links production quantity to the social–ecological legacy landscape (grassland covers 26% of total area) by requiring that 75% of fodder be regionally sourced. The second rule limits production through absolute milk quota at both the livestock unit, farm and cooperative level. This keeps farm size at a moderate level (average 32 ha). The third rule requires that low yielding, regional cattle breeds (‘Abondance’ and ‘Tarine’) constitute 100% of livestock. These rules couple production to the landscape’s social–ecological legacies. This collectively agreed rule set maintains small-scale agriculture with extensive management embedded in a regional social–ecological context. While the rule set emerged from within the region, e.g. local actors defined the spatial boundaries of the PDO collection area and the rule set; today it depends on and corresponds to the standards of the PDO EU level.
We consider this rule set as the consolidated result of negotiations between differing interests over common values and knowledge and current resource use (activity attachment, technology, etc.) that has been evolving over time. The limited choice of cattle breeds is the result of a long negotiation process in the 1980s, where some farmers favoured high yielding cattle breeds over the local low yielding types in order to increase production quantity (Lynch and Harvois 2016). More recently, a debate focussed on the easing of the 75% local fodder requirement. While some actors prefer low production quantities, others would prefer more flexible fodder requirements to allow for higher production. Some actors question the third rule, which limits farm size. A fraction of farmers proposes stricter rules, such as a shift to organic labelling. Thus, the modification of these social social–ecological legacies could affect the NCP co-production steps and the ecological subsystem (landscape, genetic diversity). However, any modification prompts lengthy administrative processes at consortium level followed by a public enquiry and national approval by regulatory authorities. The results of the public enquiry are not binding, but as a leading actor on this level stated: “In any case, for modifications to be accepted in the field there must be maximum consensus and a majority of producers who ask for them.”
Producing fodder (CP1)
In the Beaufort production system, CP1 consists of the sum of available resources at farm level as limited by the commonly agreed rule set. Individual farmers manage the ecological subsystem by livestock grazing across different altitudes and by the management of meadows for haymaking in valley bottoms. These actors are represented in the management board of the consortium and can voice their opinion in an annual general assembly. The consortium controls the compliance to the rule set. Actors apply the currently formulated rule set (CP0) and use their current resources, labour and technology to manage (and maintain) the social–ecological legacies of the ecological subsystem. Individual perceptions of exogenous factors (recurrent droughts, urban spread) and financial flows (subsidy schemes) have led some actors to change how they use the resources available to them. They have increased technological input through irrigation since 2015. Still, the used amount of labour (2.06 LFU/h), irrigation (4% of agricultural surface) and livestock unit density (0.39 LSU/ha) of the Beaufort cooperative system are extensive management practices in a biophysically limited spatial area. But, even within a common rule set that regulates social–ecological legacies, management strategies are evolving, due to changing current resource use and possible individual preferences. Overall, farmers considered their agriculture as extensive and adjusted to the local conditions: “The PDO Beaufort and our practices are reasonable. It’s important to stay coherent in what you’re doing.”
Mobilising ecological resources (CP2)
In our framework, mobilising ecological resources (CP2) is defined as a function of current resources and social–ecological legacies from the social and the ecological subsystems. In Maurienne, individual farmers mobilise the current resources of the ecological subsystem by milking cows. They must comply with high quality and hygienic standards. Cooperatives collect the milk once a day from individual farms. The nearby transformation facilities enable the mobilisation and subsequently easy access to markets. The relevance of physical infrastructure in farms proximity for mobilisation has been shown to be important in other Alpine regions (Bruley et al. 2021b). Actors were aware of the relevance of mobilisation: “Here, no big player would come and get my milk. It just wouldn’t pay off for him.”
Appreciating NCP (CP3)
In the Beaufort production system CP3 (appreciating NCP) can be considered as the multiple outcomes of the entire production chain. These appreciations feedback as current resources into the social subsystem. Cooperatives transform the milk and sell the Beaufort cheese through whole or direct sale. Individual farmers use the remuneration for different aspects they consider as meaningful. The sale of the product supports households’ socioeconomic livelihood and implies by its specific local production a certain lifestyle. Actors use (and reproduce) current social resources such as activity attachment and place attachment to appreciate the outcomes. The activity attachment of the Beaufort cooperative system appears to be only slightly declining; there was a reduction of −3% of Beaufort producers over the past 7 years (2012–2019). However, 15% of the Maurienne’s grassland area was retired from agriculture from 1988 to 2010. In interviews, farmers expressed satisfaction with their socioeconomic livelihood (Grosinger et al. in review). The different steps of co-production interact. For example, the outcomes of CP3 such as place attachment and of the CP0 rule set reflect and shape each other. Place attachment affects how actors organise their rule set. For example, the compliance to the 75% local fodder requirement can be explained by the willingness of farmers to maintain certain landscape features (such as summer high pastures). Conversely, discussions about more flexible management rules may reflect the declining activity and place attachment of some farmers. Farmers might be less eager to pursue labour intensive, time-consuming activities in parcels difficult to access. In addition, a high appreciation of exclusive monetary benefits could motivate the desire for more flexible rule sets that favour greater production. The interdependency between place and activity attachment and rule sets is in particular evident when looking at the history of Beaufort. Actors with a strong activity and place attachment formalised and institutionalised their agricultural practices by the Beaufort cooperative in order to combat rural emigration and the decline of Alpine agriculture in the 1960s (Dubeuf 1996). It is yet unclear though how and if the Beaufort cooperative will be as effective to respond to ongoing and future challenges such as evolving life style expectations.
In analytical terms, the multiple individual cognitive dimensions of appreciations can render homogeneous, systemic quantification difficult. These deeply personal motivations might be difficult to upscale without losing the specific nature of such dimensions that contribute to a good quality of life. For example, an actor described her current activity as a realised desire from her childhood: “Since I’ve been a child, I always wanted to have a farm. Me, the pasture land, I only see myself there.”
Discussion
We conceptualised NCP co-production within the context of a coupled SES. This allowed us to analyse the intentional society-ecosystem interactions within the SES and to elucidate the importance of social–ecological legacies and social activities for NCP production. Below, we first discuss possible applications and empirical limits of this framework. We then explore the complexities of integrating social–ecological legacies into NCP research. We conclude by highlighting the interplay between social–ecological legacies and social dynamics.
Applications of the framework
We believe this conceptual framework may most easily be applied in systems where social and ecological boundaries are delineated by formal institutions, such as areas falling within geographical indications (Santini et al. 2015; Belletti et al. 2017). This enables detailed analysis of linkages between collective rule sets and landscape features. Nevertheless, the framework could also be applied in less strongly structured systems like cultural landscapes. Their boundaries are delineated by informal rule sets and only subsequently regularised by formal institutions such as official labelling bodies (e.g. high nature value landscapes) (Oppermann et al. 2012; Beaufoy and HNV Link Partners 2017; Benedetti 2017). In addition, the framework might not be able to adequately assess structures with a high inflow of external resources, such as industrialised agricultural systems with possible less social–ecologically evolved patterns. We suggest that the framework is best applicable where society is intrinsically linked to local ecosystems by physical and cultural interlinkages that are expressed by common norms and practices.
From an academic perspective, the framework can facilitate collaboration between different fields. First, it can raise awareness of natural scientists about the relevance of social–ecological legacies and social activities for NCP co-production at a regional scale (Hysing and Lidskog 2021). Secondly, the framework can accommodate a variety of interdisciplinary research questions, including the relations between collective values, ecosystems and regional governance rules (Ostrom 1990; Bodin 2017). From an analytical perspective, it integrates the economic dimensions of NCP co-production and associated actors with their surrounding ecosystem. In particular, the disaggregation of the steps of NCP co-production can highlight the multitude of actors and their social characteristics (and associated power in decision making) who are intimately linked by the resources used throughout co-production. Thus, it can facilitate a further integration of social sciences into assessments of society–ecosystem interactions (Stenseke and Larigauderie 2018).
Interdisciplinary approaches face the challenge of finding appropriate terms and underlying concepts that are intuitive and logical for multiple disciplines. For example, social sciences frequently use the term “capital” when referring to what we named social–ecological legacies (Guerry et al. 2015). On the other hand, natural sciences consider social–ecological legacies as memories from the past and not as a potential resource for NCP co-production (Essl et al. 2015). We believe that our framework can support meaningful exchanges for reconciling these diverging conceptualisations of available resources. We expect this will help further advancing research on value generation and associated modes of production in SES.
The framework deliberately emphasises the complementarity of resources from the social and ecological subsystems to co-produce different dimensions of appreciation. Thereby, it embodies the vision of strong sustainability (Daly 1997). The aim of analysing NCP co-production is not to quantify the relative share of co-production between the two subsystems (e.g. 1 tonne of maize is co-produced by 60% social and 40% ecological input.). The continuation of this thought would inevitably imply substitutability of ecological by social resources (Stiglitz 1997). Further, substitutability does neglect the impact of social–ecological legacies in NCP co-production processes. Nevertheless, we support suggestions from other research to investigate the effects of increasing levels of social resources in co-production on ecological degradation more thoroughly (Palomo et al. 2016; Outeiro et al. 2017). From a methodological perspective, the integration of social–ecological legacies like infrastructure might enable bridging the gap between research on NCP and other methods to analyse human–nature interactions, such as Material Flow Analysis or Life Cycle Analysis. The framework is relatively flexible. It does not assume to what extent NCP co-production is driven by social–ecological legacies or social activities. Some research suggests that NCP co-production is not based on natural resource endowments, but on human agency (Ballet et al. 2011; Spangenberg et al. 2014; Schröter et al. 2020). On the other hand, long-term studies on legacies suggest that biophysical drivers might have more explanatory power than socioeconomic variables for current land use patterns (Price et al. 2017). The application of our framework can incorporate both approaches.
Empirical application of the framework might encounter several challenges to account for external factors. Our case study describes a system whose boundaries were defined from the perspective of regional economic dynamics. The framework cannot capture the larger social structures that influence the regional SES. This is in particular evident for the different aspects of appreciation in the Beaufort production system in the Maurienne. The declining activity and place attachment reflect the general trend of decreasing farms in Europe. For that it cannot entirely be explained by the variables in our framework (EC 2009; Flury et al. 2013). In addition, the Beaufort production system depends on larger institutional structures, such as the European PDO label that ensures an above market prize and the persistence of the this regional production system (Quiñones Ruiz et al. 2018). Also changing consumer patterns, such as favouring high quality can support this low yielding extensive agricultural system (Lamarque and Lambin 2015). The framework incorporates these diverse drivers as one black box factor (demand). Thus, we suggest linking this framework with recent telecoupling approaches that consider such indirect external factors more explicitly (Hull and Liu 2018). We acknowledge that distinguishing social–ecological legacies in the social and ecological subsystems remains complex and requires further quantification and systematisation. This is in particular evident when comparing the framework with comparable conceptualisations that frequently consider livestock as anthropogenic assets and not, as in the reasoning of this framework, as a social–ecological resource within the ecological subsystem (Díaz et al. 2015; Lescourret et al. 2015).
The framework is in line with the IPBES framework that underlines the pervasiveness of non-material, cognitive elements in all components of NCP (Díaz et al. 2018). However, a structured assessment of these cognitive factors, such as values and aspects of appreciations, usually requires some level of simplification. For that, the framework might not be able to capture the various aspects of appreciation by different actors (Schröter et al. 2020). For example, the indicators we used for place and activity attachment measure its effects, but not its intrinsic underlying mechanisms. This weakness is shared across NCP research overall (Schulz and Martin-Ortega 2018), though recent developments help addressing multiple values of nature and their incorporation into analyses of SES (Schröter et al. 2020; Pascual et al. 2021 Mar 25). While we support the use of a simple range of qualitative and quantitative key indicators (e.g. Schröter et al. 2020), we believe that applying the framework starts with qualitative research.
Integrating social–ecological legacies for understanding NCP co-production
The regional rule set of a given landscape emerges as a complex integration of interacting norms and behaviours over a period of time. The illustrative example of Beaufort NCP co-production in the Maurienne valley indicates that the way in which social–ecological legacies are organised by a common agreement (such as a collective rule set) among actors can affect the entire production system. For example, compliance to regional livestock breeds and fodder sourcing influence farm size and presumably different aspects of appreciation. The organisation of resources by a rule set can only be understood by integrating social–ecological legacies such as common values as a key resource. In case of the Beaufort production system, the organisation of collective values allowed an otherwise not competitive product to ensure the maintenance of mountain agriculture (Lynch and Harvois 2016). This suggests that the (re)organisation of non-material social–ecological legacies can facilitate possible adaptation strategies to other challenges (e.g. climate change) for regional SES (Berkes et al. 2000; Oteros-Rozas et al. 2013; Lavorel et al. 2020). To advance agroecological transitions, collective institutions may (re)formulate or adjust collective rule sets in accordance with the anticipated aspects of appreciation (Lamine et al. 2019). Thus, collective rule sets can be relevant for the preservation of landscapes with a specific biodiversity and cultural values, such as High Nature Value (HNV) landscapes. Recent research explicitly studying these linkages in Slovenia has highlighted the relevance of collective rule sets and associated collective value sets for these landscapes (Rac et al. 2020). Some research suggests that collective rule sets can promote biodiversity conservation, but more numerous and standardised, or at least comparable, studies exploring these interlinkages are needed (Chappell et al. 2016). However, as can be seen in the case study, actors currently rather favour easing restrictions (e.g. 75% local fodder requirement) and only a fraction support stricter environmental measures. Social–ecological legacies can impede the introduction of new practices, for example the proposition of organic labelling for the Beaufort production is considered as controversial. This is in line with a recent meta-analysis on the modifications of PDO labels which suggests that ecological considerations only play a minor role in the amendment processes of the products (Marescotti et al. 2020). Thus, collective rule sets can either facilitate or hamper (e.g. by institutional inertia, path dependency or “stickiness”) the continuation or change of NCP co-production (Waylen et al. 2015; Colloff et al. 2020; Lavorel et al. 2020).
Evolving current resources and types of appreciation
We showed that actors need to comply with a certain rule set, but are then relatively free to set their current resource use in their management activities. Changes in energy and material regimes, embodied as current resources, can profoundly impact current and future NCP co-production and subsequently modify these social–ecological legacies (Plutzar et al. 2016; Le Noë et al. 2020). In line with previous studies on natural resource management, our analysis of the Beaufort production system showed that the rule set could influence the use of current resources in management practices (Ostrom 1990). Social–ecological legacies coupled with evolving current resources and aspects of appreciation can lead to new management practices like increasing irrigation (Waylen et al. 2015). In our case study, new irrigation technology can lead to undesirable effects on the social–ecological legacies of the ecosystem (e.g. modifying soil carbon) (Mudge et al. 2021). Therefore, the rigidity of collective rule sets combined with changing current resources can lead to social–ecological traps, with the unintentional degradation of ecosystems (Boonstra and de Boer 2014). On the other hand, social–ecological legacies and evolving types of appreciations have also led to new forms of non-material NCP, such as landscape appreciation. In the case of the Beaufort production system, the cooperatives acknowledge this aspect and offer regular tourist visits to their transformation facilities or to grazing cattle on nearby pastures. On a larger scale, some European national or supranational subsidy schemes prioritise this non-material dimension of NCP co-production indirectly. The subsidies favour landscape management over production quantity to maintain a desired aesthetic appearance (von Glasenapp and Thornton 2011; Flury et al. 2013; Daugstad 2019). More research investigating the links between current resources, social–ecological legacies, individual management practices and types of appreciation are needed to better understand the role of social–ecological legacies in NCP co-production.
Conclusion
Our conceptual framework showed how regional societies make use of available resources for aspects they consider as relevant. We integrated social–ecological legacies and social activities to thoroughly analyse biophysical constraints and modifiable conditions SES are embedded in. The framework highlights the relevance of consensus among actors on the management of regional landscapes. We argued that a balanced recognition of social–ecological legacies of the social and the ecological subsystem is essential for describing agricultural systems. Further, the relations of outcomes with collective rule sets facilitate the understanding of actors’ choices in their resource use. While the framework is conceptually complex and requires knowledge from multiple disciplines, we argue it will advance analyses of agricultural development, social–ecological legacies and regional governance systems because it decidedly focusses on the contextual specifics of these systems. Additionally, it allows rapidly identifying relevant key stakeholders. We believe that the explicit linking of society and ecosystems through social–ecological legacies provides a common ground for natural and social sciences in a regional context. This can nurture the discourse on value pluralism and foster research of non-material aspects that people consider as meaningful to their life.
References
Alessa L, Kliskey A, Altaweel M (2009) Toward a typology for social–ecological systems. Sustain Sci Pract Policy 5(1):31–41. https://doi.org/10.1080/15487733.2009.11908026
Anderies JM, Janssen MA, Ostrom E. 2004. A framework to analyze the robustness of social–ecological systems from an institutional perspective. Ecol Soc 9(1). https://doi.org/10.5751/ES-00610-090118. [Accessed 2021 Feb 12]. http://www.ecologyandsociety.org/vol9/iss1/art18/
Ballet J, Bazin D, Dubois J-L, Mahieu F-R (2011) A note on sustainability economics and the capability approach. Ecol Econ 70(11):1831–1834. https://doi.org/10.1016/j.ecolecon.2011.05.009
Barnaud C, Corbera E, Muradian R, Salliou N, Sirami C, Vialatte A, Choisis J-P, Dendoncker N, Mathevet R, Moreau C (2018) Ecosystem services, social interdependencies, and collective action. Ecol Soc 23(1):14
Beaufoy G, HNV Link Partners (2017) The HNV-Link Compendium. Comparative collection of high nature value innovations, experiences, needs and lessons from 10 European “Learning Areas” (HNV-Link H2020 Project). HNV-Link WP2, Deliverable 2.6.1. EFNCP, Cuacos, Spain, CIHEAM-IAMM, Montpellier, France. http://www.hnvlink.eu/download/D2.6_HNVLinkCOMPENDIUM.pdf
Belletti G, Marescotti A, Touzard J-M (2017) Geographical indications, public goods, and sustainable development: the roles of actors’ strategies and public policies. World Dev 98:45–57. https://doi.org/10.1016/j.worlddev.2015.05.004
Benedetti Y (2017) Trends in high nature value farmland studies: a systematic review. Eur J Ecol 3(2):19–32. https://doi.org/10.1515/eje-2017-0012
Bennett EM, Cramer W, Begossi A, Cundill G, Díaz S, Egoh BN, Geijzendorffer IR, Krug CB, Lavorel S, Lazos E et al (2015) Linking biodiversity, ecosystem services, and human well-being: three challenges for designing research for sustainability. Curr Opin Environ Sustain 14:76–85. https://doi.org/10.1016/j.cosust.2015.03.007
Bergeret A, Lavorel S. in press. Stakeholder visions for trajectories of adaptation to climate change in the Drôme catchment (French Alps). Reg Environ Change.
Berkes F, Colding J, Folke C (2000) Rediscovery of traditional ecological knowledge as adaptive management. Ecol Appl 10(5):1251. https://doi.org/10.2307/2641280
Bodin Ö (2017) Collaborative environmental governance: achieving collective action in social–ecological systems. Science 357(6352):eaan1114. https://doi.org/10.1126/science.aan1114
Boonstra WJ, de Boer FW (2014) The historical dynamics of social–ecological traps. Ambio 43(3):260–274. https://doi.org/10.1007/s13280-013-0419-1
Bruley E, Locatelli B, Lavorel S (2021) Nature’s contributions to people: coproducing quality of life from multifunctional landscapes. Ecol Soc 26(1). https://doi.org/10.5751/ES-12031-260112. [Accessed 2021 Apr 26]. https://www.ecologyandsociety.org/vol26/iss1/art12/
Bruley E, Locatelli B, Vendel F, Bergeret A, Elleaume N, Grosinger J, Lavorel S (2021) Historical reconfigurations of a social–ecological system adapting to economic, policy and climate changes in the French Alps. Reg Environ Change 21(2). https://doi.org/10.1007/s10113-021-01760-8. [Accessed 2021 Apr 26]. http://link.springer.com/10.1007/s10113-021-01760-8
Bryman A (2016) Social research methods, 5th edn. Oxford University Press, London
Carrasco LR, Chan J, McGrath FL, Nghiem LTP (2017) Biodiversity conservation in a telecoupled world. Ecol Soc 22(3). https://doi.org/10.5751/ES-09448-220324. [Accessed 2021 Mar 1]. https://www.ecologyandsociety.org/vol22/iss3/art24/
Chaigneau T, Brown K, Coulthard S, Daw TM, Szaboova L (2019) Money, use and experience: identifying the mechanisms through which ecosystem services contribute to wellbeing in coastal Kenya and Mozambique. Ecosyst Serv 38:100957. https://doi.org/10.1016/j.ecoser.2019.100957
Chan KMA, Guerry AD, Balvanera P, Klain S, Satterfield T, Basurto X, Bostrom A, Chuenpagdee R, Gould R, Halpern BS et al (2012) Where are cultural and social in ecosystem services? A framework for constructive engagement. Bioscience 62(8):744–756. https://doi.org/10.1525/bio.2012.62.8.7
Chappell MJ, Moore JR, Heckelman AA (2016) Participation in a city food security program may be linked to higher ant alpha- and beta-diversity: an exploratory case from Belo Horizonte. Brazil Agroecol Sustain Food Syst 40(8):804–829. https://doi.org/10.1080/21683565.2016.1160020
Clarke V, Braun V (2014) Thematic analysis. In: Teo T, editor. Encyclopedia of Critical Psychology. Springer New York, New York, NY pp 1947–1952. [Accessed 2021 Apr 4]. http://link.springer.com/10.1007/978-1-4614-5583-7_311
Clavel C (2014) Etude prospective coopérative de La Haute Maurienne- Etat des lieux. Savoie Mont Blanc- Chambre d’agriculture, Lanslebourg
Colding J, Barthel S (2019) Exploring the social–ecological systems discourse 20 years later. Ecol Soc 24(1). https://doi.org/10.5751/ES-10598-240102. [Accessed 2021 Feb 26]. https://www.ecologyandsociety.org/vol24/iss1/art2/
Colloff MJ, Wise RM, Palomo I, Lavorel S, Pascual U (2020) Nature’s contribution to adaptation: insights from examples of the transformation of social–ecological systems. Ecosyst People 16(1):137–150. https://doi.org/10.1080/26395916.2020.1754919
Cook EM, Hall SJ, Larson KL (2012) Residential landscapes as social–ecological systems: a synthesis of multi-scalar interactions between people and their home environment. Urban Ecosyst 15(1):19–52. https://doi.org/10.1007/s11252-011-0197-0
Cuddington K (2011) Legacy effects: the persistent impact of ecological interactions. Biol Theory 6(3):203–210. https://doi.org/10.1007/s13752-012-0027-5
Daly H (1997) Georgescu-Roegen versus Solow/Stiglitz. Ecol Econ 22(3):261–266. https://doi.org/10.1016/S0921-8009(97)00080-3
Daugstad K (2019) Resilience in mountain farming in Norway. Sustainability 11(12):3476. https://doi.org/10.3390/su11123476
Dearing JA, Wang R, Zhang K, Dyke JG, Haberl H, Hossain MS, Langdon PG, Lenton TM, Raworth K, Brown S et al (2014) Safe and just operating spaces for regional social–ecological systems. Glob Environ Change 28:227–238. https://doi.org/10.1016/j.gloenvcha.2014.06.012
Díaz S, Demissew S, Carabias J, Joly C, Lonsdale M, Ash N, Larigauderie A, Adhikari JR, Arico S, Báldi A et al (2015) The IPBES conceptual framework—connecting nature and people. Curr Opin Environ Sustain 14:1–16. https://doi.org/10.1016/j.cosust.2014.11.002
Díaz S, Pascual U, Stenseke M, Martín-López B, Watson RT, Molnár Z, Hill R, Chan KMA, Baste IA, Brauman KA et al (2018) Assessing nature’s contributions to people. Science 359(6373):270–272. https://doi.org/10.1126/science.aap8826
Dubeuf B (1996) La construction d’un produit de terroir haut de gamme : le Beaufort. Économie Rurale 232(1):54–61. https://doi.org/10.3406/ecoru.1996.4784
Eakin H, Rueda X, Mahanti A (2017) Transforming governance in telecoupled food systems. Ecol Soc 22(4). https://doi.org/10.5751/ES-09831-220432. [Accessed 2021 Mar 1]. https://www.ecologyandsociety.org/vol22/iss4/art32/
EC (European Commission-DIRECTORATE-GENERAL FOR AGRICULTURE AND RURAL DEVELOPMENT) (2009) Peak performance—new insights into mountain farming in the European Union
Edens B, Hein L (2013) Towards a consistent approach for ecosystem accounting. Ecol Econ 90:41–52. https://doi.org/10.1016/j.ecolecon.2013.03.003
Egarter Vigl L, Schirpke U, Tasser E, Tappeiner U (2016) Linking long-term landscape dynamics to the multiple interactions among ecosystem services in the European Alps. Landsc Ecol 31(9):1903–1918. https://doi.org/10.1007/s10980-016-0389-3
Erb K-H, Haberl H, Jepsen MR, Kuemmerle T, Lindner M, Müller D, Verburg PH, Reenberg A (2013) A conceptual framework for analysing and measuring land-use intensity. Curr Opin Environ Sustain 5(5):464–470. https://doi.org/10.1016/j.cosust.2013.07.010
Ernstson H (2013) The social production of ecosystem services: a framework for studying environmental justice and ecological complexity in urbanized landscapes. Landsc Urban Plan 109(1):7–17. https://doi.org/10.1016/j.landurbplan.2012.10.005
Essl F, Dullinger S, Rabitsch W, Hulme PE, Pyšek P, Wilson JRU, Richardson DM (2015) Historical legacies accumulate to shape future biodiversity in an era of rapid global change. Kueffer C, editor. Divers Distrib 21(5):534–547. https://doi.org/10.1111/ddi.12312
Europarc F (2018) European protected areas & sustainable agriculture working in partnership for biodiversity and rural development. [Accessed 2021 Apr 7]. https://www.europarc.org/news/2018/03/position-paper-sustainable-agriculture/
Fedele G, Locatelli B, Djoudi H (2017) Mechanisms mediating the contribution of ecosystem services to human well-being and resilience. Ecosyst Serv 28:43–54. https://doi.org/10.1016/j.ecoser.2017.09.011
Feranec J, Soukup T, Feranec G, Jaffrain G, eds (2016) European landscape dynamics: CORINE land cover data. 6000 Broken Sound Parkway NW, Suite 300 Boca Raton, FL 33487-2742: CRC Press. [Accessed 2021 Apr 7]. http://www.crcnetbase.com/doi/book/10.1201/9781315372860
Fischer A, Eastwood A (2016) Coproduction of ecosystem services as human–nature interactions—an analytical framework. Land Use Policy 52:41–50. https://doi.org/10.1016/j.landusepol.2015.12.004
Flury C, Huber R, Tasser E. 2013. Future of mountain agriculture in the Alps. In: Mann S, eds. The Future of Mountain Agriculture. Springer Berlin Heidelberg, Berlin, Heidelberg. pp 105–126. [Accessed 2020 Oct 8]. http://link.springer.com/10.1007/978-3-642-33584-6_8
Folke C (2006) Resilience: the emergence of a perspective for social–ecological systems analyses. Glob Environ Change 16(3):253–267. https://doi.org/10.1016/j.gloenvcha.2006.04.002
Foster D, Swanson F, Aber J, Burke I, Brokaw N, Tilman D, Knapp A (2003) The importance of land-use legacies to ecology and conservation. Bioscience 53(1):77. https://doi.org/10.1641/0006-3568(2003)053[0077:TIOLUL]2.0.CO;2
Garcia-Pausas J, Romanyà J, Montané F, Rios AI, Taull M, Rovira P, Casals P (2017) Are soil carbon stocks in mountain grasslands compromised by land-use changes? In: Catalan J, Ninot JM, Aniz MM, (eds). High Mountain Conservation in a Changing World. Vol. 62. Springer International Publishing, Cham, pp 207–230. [Accessed 2020 Nov 4]. http://link.springer.com/10.1007/978-3-319-55982-7_9
von Glasenapp M, Thornton TF (2011) Traditional ecological knowledge of Swiss Alpine farmers and their resilience to socioecological Change. Hum Ecol 39(6):769–781. https://doi.org/10.1007/s10745-011-9427-6
Guerry AD, Polasky S, Lubchenco J, Chaplin-Kramer R, Daily GC, Griffin R, Ruckelshaus M, Bateman IJ, Duraiappah A, Elmqvist T et al (2015) Natural capital and ecosystem services informing decisions: from promise to practice. Proc Natl Acad Sci 112(24):7348–7355. https://doi.org/10.1073/pnas.1503751112
Haberl H, Erb KH, Krausmann F, Gaube V, Bondeau A, Plutzar C, Gingrich S, Lucht W, Fischer-Kowalski M (2007) Quantifying and mapping the human appropriation of net primary production in earth’s terrestrial ecosystems. Proc Natl Acad Sci 104(31):12942–12947. https://doi.org/10.1073/pnas.0704243104
Haines-Young R, Potschin M (2010) The links between biodiversity, ecosystem services and human well-being. In: Raffaelli DG, Frid CLJ, (eds). Ecosystem Ecology. Cambridge University Press, Cambridge, pp 110–139. [Accessed 2021 Jan 18]. https://www.cambridge.org/core/product/identifier/CBO9780511750458A013/type/book_part.
Hanspach J, Loos J, Dorresteijn I, Abson DJ, Fischer J (2016) Characterizing social–ecological units to inform biodiversity conservation in cultural landscapes. Di Minin E, editor. Divers Distrib 22(8):853–864. https://doi.org/10.1111/ddi.12449
Hernández-Morcillo M, Hoberg J, Oteros-Rozas E, Plieninger T, Gómez-Baggethun E, Reyes-García V (2014) Traditional ecological knowledge in Europe: status quo and insights for the environmental policy agenda. Environ Sci Policy Sustain Dev 56(1):3–17. https://doi.org/10.1080/00139157.2014.861673
Herrero-Jáuregui C, Arnaiz-Schmitz C, Reyes M, Telesnicki M, Agramonte I, Easdale M, Schmitz M, Aguiar M, Gómez-Sal A, Montes C (2018) What do we talk about when we talk about social–ecological systems? A literature review. Sustainability 10(8):2950. https://doi.org/10.3390/su10082950
Hinojosa L, Lambin EF, Mzoughi N, Napoléone C (2016) Place attachment as a factor of mountain farming permanence: a survey in the French Southern Alps. Ecol Econ 130:308–315. https://doi.org/10.1016/j.ecolecon.2016.08.004
Hull V, Liu J (2018) Telecoupling: a new frontier for global sustainability. Ecol Soc. 23(4). https://doi.org/10.5751/ES-10494-230441. [Accessed 2021 Mar 1]. https://www.ecologyandsociety.org/vol23/iss4/art41/
Hysing E, Lidskog R (2021) Do conceptual innovations facilitate transformative change? The case of biodiversity governance. Front Ecol Evol. 8.https://doi.org/10.3389/fevo.2020.612211. [Accessed 2021 Apr 18]. https://www.frontiersin.org/articles/10.3389/fevo.2020.612211/full
INAO (Institut national de l’origine et de la qualité) (2015) Cahier des charges de l’appellation d’origine « Beaufort »
Jäger H, Peratoner G, Tappeiner U, Tasser E (2020) Grassland biomass balance in the European Alps: current and future ecosystem service perspectives. Ecosyst Serv 45:101163. https://doi.org/10.1016/j.ecoser.2020.101163
Jones L, Norton L, Austin Z, Browne AL, Donovan D, Emmett BA, Grabowski Z, Howard DC, Jones JPG, Kenter J et al (2016) Stocks and flows of natural and human-derived capital in ecosystem services. Land Use Policy 52:151–162. https://doi.org/10.1016/j.landusepol.2015.12.014
Kim G, Vaswani RT, Lee D (2017) Social–ecological memory in an autobiographical novel: ecoliteracy, place attachment, and identity related to the Korean traditional village landscape. Ecol Soc. 22(2). https://doi.org/10.5751/ES-09284-220227. [Accessed 2021 Mar 24]. https://www.ecologyandsociety.org/vol22/iss2/art27/.
Kofinas GP, Chapin FS. 2009. Sustaining livelihoods and human well-being during social–ecological change. In: Folke C, Kofinas GP, Chapin FS, (eds) Principles of Ecosystem Stewardship. Springer New York, New York, NY, pp 55–75. [Accessed 2021 Mar 23]. http://link.springer.com/10.1007/978-0-387-73033-2_3.
Koohafkan P, Altieri MA (2011) Globally important agricultural heritage systems: a legacy for the future. Food Agriculture Organization of the United Nations, Rome
Lamarque P, Lambin EF (2015) The effectiveness of marked-based instruments to foster the conservation of extensive land use: the case of Geographical Indications in the French Alps. Land Use Policy 42:706–717. https://doi.org/10.1016/j.landusepol.2014.10.009
Lamine C, Magda D, Amiot M-J (2019) Crossing sociological, ecological, and nutritional perspectives on agrifood systems transitions: towards a transdisciplinary territorial approach. Sustainability 11(5):1284. https://doi.org/10.3390/su11051284
Lavorel S, Locatelli B, Colloff MJ, Bruley E (2020) Co-producing ecosystem services for adapting to climate change. Philos Trans R Soc B Biol Sci 375(1794):20190119. https://doi.org/10.1098/rstb.2019.0119
Le Noë J, Roux N, Billen G, Gingrich S, Erb K-H, Krausmann F, Thieu V, Silvestre M, Garnier J (2020) The phosphorus legacy offers opportunities for agro-ecological transition (France 1850–2075). Environ Res Lett 15(6):064022. https://doi.org/10.1088/1748-9326/ab82cc
Lescourret F, Magda D, Richard G, Adam-Blondon A-F, Bardy M, Baudry J, Doussan I, Dumont B, Lefèvre F, Litrico I et al (2015) A social–ecological approach to managing multiple agro-ecosystem services. Curr Opin Environ Sustain 14:68–75. https://doi.org/10.1016/j.cosust.2015.04.001
Lynch E, Harvois F. 2016. Le Beaufort: réinventer le fruit commun. Lyon: Libel.
Madelrieux S, Bergeret A, Fillion L (2018) Forms of territorial embeddedness in dairy value chains—case of the Chartreuse massif (French Alps): geographical and historical perspectives. Open Agric 3(1):618–631. https://doi.org/10.1515/opag-2018-0065
Marescotti A, Quiñones-Ruiz XF, Edelmann H, Belletti G, Broscha K, Altenbuchner C, Penker M, Scaramuzzi S (2020) Are protected geographical indications evolving due to environmentally related justifications? An analysis of amendments in the fruit and vegetable sector in the European Union. Sustainability 12(9):3571. https://doi.org/10.3390/su12093571
Martín-López B, Palomo I, García-Llorente M, Iniesta-Arandia I, Castro AJ, García Del Amo D, Gómez-Baggethun E, Montes C (2017) Delineating boundaries of social–ecological systems for landscape planning: a comprehensive spatial approach. Land Use Policy 66:90–104. https://doi.org/10.1016/j.landusepol.2017.04.040
Mastrángelo ME, Pérez-Harguindeguy N, Enrico L, Bennett E, Lavorel S, Cumming GS, Abeygunawardane D, Amarilla LD, Burkhard B, Egoh BN et al (2019) Key knowledge gaps to achieve global sustainability goals. Nat Sustain 2(12):1115–1121. https://doi.org/10.1038/s41893-019-0412-1
McGinnis MD (2011) An introduction to IAD and the language of the Ostrom workshop: a simple guide to a complex framework. Policy Stud J 39(1):169–183. https://doi.org/10.1111/j.1541-0072.2010.00401.x
McGinnis MD, Ostrom E (2014) Social–ecological system framework: initial changes and continuing challenges. Ecol Soc 19(2). https://doi.org/10.5751/ES-06387-190230. [Accessed 2020 Oct 23]. http://www.ecologyandsociety.org/vol19/iss2/art30/.
MEA MEA (Porgram) (2005) Ecosystems and human well-being. Island Press, Washington, D.C
Meyfroidt P, Roy Chowdhury R, de Bremond A, Ellis EC, Erb K-H, Filatova T, Garrett RD, Grove JM, Heinimann A, Kuemmerle T et al (2018) Middle-range theories of land system change. Glob Environ Chang 53:52–67. https://doi.org/10.1016/j.gloenvcha.2018.08.006
Mudge PL, Millar J, Pronger J, Roulston A, Penny V, Fraser S, Eger A, Caspari T, Robertson B, Mason NWH et al (2021) Impacts of irrigation on soil C and N stocks in grazed grasslands depends on aridity and irrigation duration. Geoderma 399:115109. https://doi.org/10.1016/j.geoderma.2021.115109
Muhar A, Raymond CM, van den Born RJG, Bauer N, Böck K, Braito M, Buijs A, Flint C, de Groot WT, Ives CD et al (2018) A model integrating social-cultural concepts of nature into frameworks of interaction between social and natural systems. J Environ Plan Manag 61(5–6):756–777. https://doi.org/10.1080/09640568.2017.1327424
Oppermann R, Beaufoy G, Jones G (2012) High nature value farming in Europe. Verlag Regionalkultur, Ubstadt-Weiher
Ostrom E (1990) Governing the commons: the evolution of institutions for collective action. Cambridge University Press, Cambridge, New York (The Political economy of institutions and decisions)
Ostrom E (2000) Collective action and the evolution of social norms. J Econ Perspect 14(3):37–158
Ostrom E (2009) A general framework for analyzing sustainability of social–ecological systems. Science 325(5939):419–422. https://doi.org/10.1126/science.1172133
Oteros-Rozas E, Ontillera-Sánchez R, Sanosa P, Gómez-Baggethun E, Reyes-García V, González JA (2013) Traditional ecological knowledge among transhumant pastoralists in Mediterranean Spain. Ecol Soc 18(3). https://doi.org/10.5751/ES-05597-180333. [Accessed 2020 Nov 23]. http://www.ecologyandsociety.org/vol18/iss3/art33/
Outeiro L, Ojea E, Garcia Rodrigues J, Himes-Cornell A, Belgrano A, Liu Y, Cabecinha E, Pita C, Macho G, Villasante S (2017) The role of non-natural capital in the co-production of marine ecosystem services. Int J Biodivers Sci Ecosyst Serv Manag 13(3):35–50. https://doi.org/10.1080/21513732.2017.1415973
Pachoud C (2019) Identity, feeling of belonging and collective action in localized agrifood systems. Example of the Serrano cheese in the Campos de Cima da Serra, Brazil. Cah Agric 28:28. https://doi.org/10.1051/cagri/2019028
Pachoud C, Delay E, Da Re R, Ramanzin M, Sturaro E (2020) A relational approach to studying collective action in dairy cooperatives producing mountain cheeses in the Alps: the case of the Primiero cooperative in the Eastern Italians Alps. Sustainability 12(11):4596. https://doi.org/10.3390/su12114596
Palomo I, Felipe-Lucia MR, Bennett EM, Martín-López B, Pascual U (2016) Disentangling the pathways and effects of ecosystem service co-production. In: Advances in Ecological Research. Vol. 54. Elsevier. pp 245–283. [Accessed 2020 Aug 25]. https://linkinghub.elsevier.com/retrieve/pii/S0065250415000276
Pascual U, Adams WM, Díaz S, Lele S, Mace GM, Turnhout E (2021) Biodiversity and the challenge of pluralism. Nat Sustain. https://doi.org/10.1038/s41893-021-00694-7. [Accessed 2021 Apr 21]. http://www.nature.com/articles/s41893-021-00694-7
Plieninger T, Kizos T, Bieling C, Le Dû-Blayo L, Budniok M-A, Bürgi M, Crumley CL, Girod G, Howard P, Kolen J, et al. (2015) Exploring ecosystem-change and society through a landscape lens: recent progress in European landscape research. Ecol Soc 20(2). https://doi.org/10.5751/ES-07443-200205. [Accessed 2020 Oct 16]. http://www.ecologyandsociety.org/vol20/iss2/art5/
Plutzar C, Kroisleitner C, Haberl H, Fetzel T, Bulgheroni C, Beringer T, Hostert P, Kastner T, Kuemmerle T, Lauk C et al (2016) Changes in the spatial patterns of human appropriation of net primary production (HANPP) in Europe 1990–2006. Reg Environ Chang 16(5):1225–1238. https://doi.org/10.1007/s10113-015-0820-3
Potschin-Young M, Haines-Young R, Görg C, Heink U, Jax K, Schleyer C (2018) Understanding the role of conceptual frameworks: reading the ecosystem service cascade. Ecosyst Serv 29:428–440. https://doi.org/10.1016/j.ecoser.2017.05.015
Price B, Kaim D, Szwagrzyk M, Ostapowicz K, Kolecka N, Schmatz DR, Wypych A, Kozak J (2017) Legacies, socio-economic and biophysical processes and drivers: the case of future forest cover expansion in the Polish Carpathians and Swiss Alps. Reg Environ Chang 17(8):2279–2291. https://doi.org/10.1007/s10113-016-1079-z
QSR International (2020) NVIVO (released in March 2020). https://www.qsrinternational.com/nvivo-qualitative-data-analysis-software/home.
Quétier F, Thébault A, Lavorel S (2007) Plant traits in a state and transition framework as markers of ecosystem response to land-use change. Ecol Monogr 77(1):33–52. https://doi.org/10.1890/06-0054
Quétier F, Rivoal F, Marty P, de Chazal J, Thuiller W, Lavorel S (2010) Social representations of an Alpine grassland landscape and socio-political discourses on rural development. Reg Environ Chang 10(2):119–130. https://doi.org/10.1007/s10113-009-0099-3
Quiñones Ruiz XF, Forster H, Penker M, Belletti G, Marescotti A, Scaramuzzi S, Broscha K, Braito M, Altenbuchner C (2018) How are food Geographical Indications evolving?—an analysis of EU GI amendments. Br Food J 120(8):1876–1887. https://doi.org/10.1108/BFJ-02-2018-0087
Rac I, Juvančič L, Erjavec E (2020) Stimulating collective action to preserve high nature value farming in post-transitional settings. A comparative analysis of three Slovenian social–ecological systems. Nat Conserv 39:87–111. https://doi.org/10.3897/natureconservation.39.51216
Remme RP, Schröter M, Hein L (2014) Developing spatial biophysical accounting for multiple ecosystem services. Ecosyst Serv 10:6–18. https://doi.org/10.1016/j.ecoser.2014.07.006
Renard D, Rhemtulla JM, Bennett EM (2015) Historical dynamics in ecosystem service bundles. Proc Natl Acad Sci 112(43):13411–13416. https://doi.org/10.1073/pnas.1502565112
Reyers B, Biggs R, Cumming GS, Elmqvist T, Hejnowicz AP, Polasky S (2013) Getting the measure of ecosystem services: a social–ecological approach. Front Ecol Environ 11(5):268–273. https://doi.org/10.1890/120144
RGD SMB R de G des données SMB (2014) Mise à jour des données d’occupation réelle des sols sur les départements de Savoie et Haute Savoie. https://www.rgd.fr
Riechers M, Balázsi Á, Betz L, Jiren TS, Fischer J (2020) The erosion of relational values resulting from landscape simplification. Landsc Ecol 35(11):2601–2612. https://doi.org/10.1007/s10980-020-01012-w
van Riper CJ, Thiel A, Penker M, Braito M, Landon AC, Thomsen JM, Tucker CM (2018) Incorporating multilevel values into the social–ecological systems framework. Ecol Soc 23(3). https://doi.org/10.5751/ES-10047-230325. [Accessed 2020 Oct 12]. https://www.ecologyandsociety.org/vol23/iss3/art25/.
Santini F, Guri F, Aubard A, Gomez y Paloma S (2015) Geographical indications and territories with specific geographical features in the eu: the cases of mountain and island areas. Pap Prep 145th EAAE Semin “Intellectual Prop Rights Geogr Indic What Stake TTIP.”
Schoch M (2013) Etude prospective coopérative de la Chambre—Etat des lieux. Savoie Mont Blanc- Chambre d’agriculture, Saint Jean de Maurienne
Schoch M (2014) Etude prospective coopérative de la Vallée des Arves—Etat des lieux. Savoie Mont Blanc- Chambre d’agriculture, Saint Jean de Maurienne
Schröter M, Başak E, Christie M, Church A, Keune H, Osipova E, Oteros-Rozas E, Sievers-Glotzbach S, van Oudenhoven APE, Balvanera P et al (2020) Indicators for relational values of nature’s contributions to good quality of life: the IPBES approach for Europe and Central Asia. Ecosyst People 16(1):50–69. https://doi.org/10.1080/26395916.2019.1703039
Schulz C, Martin-Ortega J (2018) Quantifying relational values—why not? Curr Opin Environ Sustain 35:15–21. https://doi.org/10.1016/j.cosust.2018.10.015
Spangenberg JH, Görg C, Truong DT, Tekken V, Bustamante JV, Settele J (2014) Provision of ecosystem services is determined by human agency, not ecosystem functions. Four case studies. Int J Biodivers Sci Ecosyst Serv Manag 10(1):40–53. https://doi.org/10.1080/21513732.2014.884166
Spiegelberger T, Hegg O, Matthies D, Hedlund K, Schaffner U (2006) Long-term effects of short-term perturbation in a subalpine grassland. Ecology 87(8):1939–1944. https://doi.org/10.1890/0012-9658(2006)87[1939:LEOSPI]2.0.CO;2
SPM (Syndicat du pays de Maurienne) (2020) Schéma de cohèrence territoriale
Stenseke M, Larigauderie A (2018) The role, importance and challenges of social sciences and humanities in the work of the intergovernmental science-policy platform on biodiversity and ecosystem services (IPBES). Innovation Eur J Soc Sci Res. https://doi.org/10.1080/13511610.2017.1398076
Stiglitz JE (1997) Georgescu-Roegen versus Solow/Stiglitz. Ecol Econ 22(3):269–270. https://doi.org/10.1016/S0921-8009(97)00092-X
Tengberg A, Fredholm S, Eliasson I, Knez I, Saltzman K, Wetterberg O (2012) Cultural ecosystem services provided by landscapes: assessment of heritage values and identity. Ecosyst Serv 2:14–26. https://doi.org/10.1016/j.ecoser.2012.07.006
Upton C (2008) Social capital, collective action and group formation: developmental trajectories in post-socialist Mongolia. Hum Ecol 36(2):175–188. https://doi.org/10.1007/s10745-007-9158-x
Vallet A, Locatelli B, Levrel H, Dendoncker N, Barnaud C, Quispe Conde Y (2019) Linking equity, power, and stakeholders’ roles in relation to ecosystem services. Ecol Soc 24(2). https://doi.org/10.5751/ES-10904-240214. [Accessed 2020 Aug 25]. https://www.ecologyandsociety.org/vol24/iss2/art14/
Vanpeene-Bruhier S, Moyne M-L, Brun J-J. 1998. La richesse spécifique : un outil pour la prise en compte de la biodiversité dans la gestion de l’espace - Application en Haute Maurienne (Aussois, Savoie). :47–59.
Vilá B, Arzamendia Y (2020) South American camelids: their values and contributions to people. Sustain Sci. https://doi.org/10.1007/s11625-020-00874-y. [Accessed 2021 Apr 6]. http://link.springer.com/10.1007/s11625-020-00874-y
Walker B, Carpenter SR, Anderies JM, Abel N, Cumming G, Janssen MA, Lebel L, Norberg J, Peterson GD, Pritchard R (2002) Resilience management in social–ecological systems: a working hypothesis for a participatory approach. Conserv Ecol 6(1). https://doi.org/10.5751/ES-00356-060114. [Accessed 2021 Feb 11]. http://www.ecologyandsociety.org/vol6/iss1/art14/
Walker B, Gunderson L, Kinzig A, Folke C, Carpenter S, Schultz L (2006) A handful of heuristics and some propositions for understanding resilience in social–ecological systems. Ecol Soc 11(1). https://doi.org/10.5751/ES-01530-110113. [Accessed 2021 Feb 10]. http://www.ecologyandsociety.org/vol11/iss1/art13/
Waylen KA, Blackstock KL, Holstead KL (2015) How does legacy create sticking points for environmental management? Insights from challenges to implementation of the ecosystem approach. Ecol Soc 20(2). https://doi.org/10.5751/ES-07594-200221. [Accessed 2020 Nov 9]. http://www.ecologyandsociety.org/vol20/iss2/art21/
Winkler KJ, Dade MC, Rieb JT (2021) Mismatches in the ecosystem services literature—a review of spatial, temporal, and functional-conceptual mismatches. Curr Landsc Ecol Rep. https://doi.org/10.1007/s40823-021-00063-2. [Accessed 2021 Mar 25]. http://link.springer.com/10.1007/s40823-021-00063-2
Winner L (1980) Do artifacts have politics? In: Marchant GE, Wallach W, (eds). Emerging Technologies: Ethics, Law and Governance. 1st ed. Routledge. pp 15–30. [Accessed 2021 Mar 23]. https://www.taylorfrancis.com/books/9781000108927/chapters/10.4324/9781003074960-3
Wu X, Wei Y, Fu B, Wang S, Zhao Y, Moran EF (2020) Evolution and effects of the social–ecological system over a millennium in China’s Loess plateau. Sci Adv 6(41):eabc0276. https://doi.org/10.1126/sciadv.abc0276
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This work was supported by the Université Grenoble Alpes Cross-Disciplinary Project Trajectories funded by the French National Research Agency “Investissements d’avenir” program (ANR-15-IDEX-02). This work was carried out within the eLSTER site Zone Atelier Alpes.
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Grosinger, J., Potts, M.D., Buclet, N. et al. Memory over matter?—a conceptual framework to integrate social–ecological l legacies in agricultural NCP co-production. Sustain Sci 17, 761–777 (2022). https://doi.org/10.1007/s11625-021-01061-3
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DOI: https://doi.org/10.1007/s11625-021-01061-3