Reg Environ Change
DOI 10.1007/s10113-015-0839-5
REVIEW ARTICLE
Communities and change in the anthropocene: understanding
social-ecological vulnerability and planning adaptations
to multiple interacting exposures
Nathan James Bennett1,2 • Jessica Blythe3 • Stephen Tyler4,5 • Natalie C. Ban6
Received: 26 January 2015 / Accepted: 4 July 2015
The Author(s) 2015. This article is published with open access at Springerlink.com
Abstract The majority of vulnerability and adaptation
scholarship, policies and programs focus exclusively on
climate change or global environmental change. Yet,
individuals, communities and sectors experience a broad
array of multi-scalar and multi-temporal, social, political,
economic and environmental changes to which they are
vulnerable and must adapt. While extensive theoretical—
and increasingly empirical—work suggests the need to
explore multiple exposures, a clear conceptual framework
which would facilitate analysis of vulnerability and adaptation to multiple interacting socioeconomic and biophysical changes is lacking. This review and synthesis paper
aims to fill this gap through presenting a conceptual
framework for integrating multiple exposures into vulnerability analysis and adaptation planning. To support
applications of the framework and facilitate assessments
and comparative analyses of community vulnerability, we
Editor: Jamie Pittock.
& Nathan James Bennett
nathan.bennett@ubc.ca;
http://nathanbennett.ca
develop a comprehensive typology of drivers and exposures experienced by coastal communities. Our results
reveal essential elements of a pragmatic approach for localscale vulnerability analysis and for planning appropriate
adaptations within the context of multiple interacting
exposures. We also identify methodologies for characterizing exposures and impacts, exploring interactions and
identifying and prioritizing responses. This review focuses
on coastal communities; however, we believe the framework, typology and approach will be useful for understanding vulnerability and planning adaptation to multiple
exposures in various social-ecological contexts.
Keywords Social-ecological systems Vulnerability
Adaptation Exposure Adaptive capacity Coastal
communities Drivers of change
The complexity, unpredictability and pace of events
in our world, and the severity of global environmental
stress, are soaring….Many societies, groups, and
people adapt reasonably well to our swiftly changing
world, but others have fallen behind and risk being
overwhelmed by converging pressures. Thomas
Homer-Dixon, The Ingenuity Gap, 2000.
1
Institute for Resources, Environment and Sustainability,
University of British Columbia, 2202 Main Mall, Vancouver,
BC V6T 1Z4, Canada
2
School of Marine and Environmental Affairs, University of
Washington, Seattle, WA, USA
Introduction
3
ARC Centre of Excellence for Coral Reef Studies and
WorldFish, James Cook University, Townsville, Australia
4
Adaptive Resource Management, Victoria, BC, Canada
5
Department of Geography, University of Victoria, Victoria,
BC, Canada
6
School of Environmental Studies, University of Victoria,
Victoria, BC, Canada
‘‘Change is the only constant…’’, Heraclitus might have
been talking about communities when he said this in ancient
Greece. For contemporary communities around the world,
each situated in a distinct social-ecological context and each
with their own histories and visions for the future, anthropogenic change is occurring with increasing rapidity,
complexity and uncontrollability (IPCC 2014; Steffen et al.
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N. J. Bennett et al.
2015). The drivers of these changes occur at different scales
and speeds and include environmental, climatic, economic,
technological, sociocultural, demographic and governance
factors (Millenium Ecosystem Assessment 2005; Zou and
Wei 2010; Bennett et al. 2014b). Communities are exposed
to these exogenous changes through direct and indirect
impacts on the interrelated components of social-ecological
systems (Turner et al. 2003; Perry et al. 2010). Multiple
socioeconomic and biophysical changes occurring simultaneously at different scales and speeds interact to produce
drastically different outcomes for communities in different
places (O’Brien and Leichenko 2003; O’Brien et al. 2004;
Tuler et al. 2008; Brklacich et al. 2009). Yet, the predominant focus of vulnerability and adaptation research, policy
and practice has been solely on climate change or global
environmental change. This focus on a single driver of
change is often the result of a problem-centered, rather than
community-centered, approach.
Understanding the multiple, interacting drivers and
impacts of these changes on social-ecological systems is
paramount for ecological sustainability and for human wellbeing. Authors from various disciplines, including socialecological systems and resilience (Berkes et al. 2003;
Turner et al. 2003; Walker et al. 2004), sustainable livelihoods (Ellis 2000; Scoones 2009), hazards research (Berkes
2007; Smith 2013), fisheries (Tuler et al. 2008; Perry et al.
2010; Kittinger et al. 2013), agriculture (Eakin 2005; Paavola 2008) and climate change vulnerability and adaptation
(Adger 2006; Marshall et al. 2010; Eriksen et al. 2011;
Roiko et al. 2012), have stressed the importance of considering multiple interacting exposures in research, policy and
practice. Initially, this discussion remained largely at the
conceptual realm (Turner et al. 2003; Brklacich et al. 2009).
A limited but increasing body of empirical work explores
the nature of drivers and exposures, and the interactions
between exposures as experienced by local groups and
communities (O’Brien and Leichenko 2000; Bunce et al.
2010b; Bennett et al. 2014b). Yet, in many cases the bottomup approaches taken in empirical studies have led to results
that: (a) fail to explore the breadth of changes to which
communities are exposed and (b) inadequately examine how
these changes interact to produce variable outcomes for
linked social and environmental assets that are important to
local communities. Indeed, few case studies of coastal
vulnerability are guided by conceptual frameworks, which
have led to limited comparability among sites, countries and
regions (Zou and Wei 2010). Typically, these conceptual
and empirical approaches simplify the scope of changes to
which communities are exposed, invariably leading to onedimensional adaptation policies, programs and actions that
fail to address the multifaceted and multi-scalar drivers of
change, and the complexity and uncertainty of changes in
local social-ecological systems.
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No single conceptual framework synthesizes the broad
range of theoretical advancements on multiple exposures.
Deliberate progress toward the goal of long-term sustainability requires an understanding of the dynamics of multiple drivers of change, and resulting exposures, impacts
and responses, in linked social-ecological systems. In this
article, we review and synthesize the existing theoretical
and empirical work on drivers of change in coastal socialecological systems to: (a) present a conceptual framework
for understanding vulnerability to multiple interacting
exposures, (b) develop a comprehensive typology of drivers, exposures and impacts being experienced by coastal
communities, (c) propose essential elements of a pragmatic
approach for vulnerability analysis and adaptation planning
and (d) explore methods for assessing the impacts of, and
responses to, multiple exposures in coastal social-ecological systems. To limit the scope of the paper, this review
focuses on coastal communities, which face both land- and
sea-based exposures. However, we believe the framework,
typology and approach can be applied to understand socialecological change and to develop appropriate response
strategies in various contexts.
Vulnerability to multiple exposures: key concepts
and conceptual framework
The concept of vulnerability is rooted primarily in scholarship on development and livelihoods (Sen 1982; Chambers and Conway 1992; Scoones 1998), hazards (Burton
et al. 1993; Watts and Bohle 1993; Mustafa 1998), global
environmental change (Vogel 1998; Turner et al. 2003; Smit
and Wandel 2006) and resilience (Holling 2001; Gunderson
and Pritchard 2002; Folke et al. 2003). There have been
several dominant ways of conceptualizing vulnerability
(Adger 2006). The first is to view vulnerability as an outcome through focusing on the impacts of a hazard, such as
climate change, and the ability of a system to respond. The
purpose of ‘‘end point’’ vulnerability analysis is to estimate
and reduce costs of hazards. A second perspective emphasizes vulnerability as the ‘‘starting point’’ and focuses on the
historical factors or current characteristics of individuals,
households, communities, sectors, nations, etc. that determine their differential susceptibility to harm. A more comprehensive view considers vulnerability to be the result of
the interaction between exposure, sensitivity and adaptive
capacity (Turner et al. 2003; Smit and Wandel 2006; Perry
et al. 2010). Exposure refers to the degree to which trends
and shocks, driven by changes at various scales, are experienced by a region, resource or group. Sensitivity is the
susceptibility of an entity or system to the effects of an
exposure. Historical, social, political, economic and environmental preconditions determine a system’s sensitivity.
Communities and change in the anthropocene: understanding social-ecological vulnerability and…
Watts and Bohle (1993) suggest resource distribution,
political power and voice, rights, and access to institutions
mediate sensitivity. Exposure and sensitivity combined
define the potential impacts of a change. Impacts can be
unevenly experienced by various similarly exposed groups
(genders, ages, classes, racial groups, livelihoods, etc.)
based on differential sensitivities (O’Brien and Leichenko
2000). Adaptive capacity refers to ‘‘the ability to respond to
challenges through learning, managing risk and impacts,
developing new knowledge and devising effective approaches’’ (Marshall et al. 2010). Adaptive capacity is latent
potential until it is applied in response to a change. Adaptive
capacity is determined by access to assets (human, social,
physical, financial and natural), capacity to organize, leadership, learning and knowledge, imaginative resources and
capacity to self-organize (Folke et al. 2003; Cinner et al.
2009; Bussey et al. 2012; Bennett et al. 2014a). In this view
of vulnerability, the relationship between the three components of vulnerability might be simplified to an equation:
V = E ? S - AC—whereby vulnerability (V) is determined by exposure (E) plus sensitivity (S) minus adaptive
capacity (AC) (Adger 2006).
We next introduce seven key considerations that should
shape analysis of vulnerability and responses to help maintain a resilient system. We integrate these elements into a
conceptual framework for understanding community socialecological vulnerability (Fig. 1). First, while many analyses
of vulnerability focus on impacts and outcomes in either
social or ecological subsystems, we argue that either focus is
incomplete. Relevant systems for vulnerability analysis must
address linked social and ecological components (Turner
et al. 2003; Brklacich et al. 2009). Social-ecological systems
can be defined as complex, integrative and adaptive systems,
wherein humans are part of nature (Berkes and Folke 1998).
Even in urban areas, ecosystems are important elements of
resilience (Tyler and Moench 2012).
Second, large-scale exogenous conditions and trends
that operate at different scales and speeds (defined as
‘‘drivers’’) drive local exposures (Armitage and Johnson
2006; Perry et al. 2010). More rigorous understandings of
multi-scalar drivers will lead to insights into exposures and
responses (Hall 2011; Kittinger et al. 2013). Drivers of
change can be biophysical—i.e., climate change and other
environmental changes—and socioeconomic—i.e., economic transformation, technological change, sociocultural
evolution, demographic change and shifts in governance
structures and institutions.
Third, exposures have often been framed as being
affected by stressors, risks or hazards that lead to harms
(Sen 1982; Burton et al. 1993; Watts and Bohle 1993;
Berkes 2007). Yet, local exposure to trends and shocks
does not necessarily lead to negative outcomes for all
social or ecological components of systems. Exposures can
also be experienced as opportunities for reorganization and
renewal and may lead to either desirable or undesirable
outcomes (Holling 2001; Gunderson and Pritchard 2002).
Fourth, better incorporation of multiple exposures into
analysis of vulnerability will lead to more effective vulnerability research and adaptation policy (Leichenko and
O’Brien 2008; Brklacich et al. 2009; Bunce et al. 2010a;
Smith et al. 2013; Bennett et al. 2014b). Many vulnerability assessments rely on large-scale and top-down studies
using predetermined indicators that make implicit
assumptions about the nature of changes being experienced. More empirical studies are needed to ground theoretical work in the complexities of local experiences of
multiple exposures (Turner et al. 2003; Silva et al. 2010;
Zou and Wei 2010) and to better identify actions to
improve institutions and policies (Hall 2011).
Fifth, many analyses of vulnerability, resilience and
adaptive capacity are static snapshots of the present that do
not account adequately for interactions and feedbacks.
Systems are dynamic with constantly changing drivers,
exposures, impacts, responses and outcomes. Impacts can
be direct or interactive. Interactive impacts result from
interactions between drivers at higher scales, cascading
effects of direct impacts from exposures, autonomous
feedbacks between and among social and ecological components, and the feedbacks of adaptive responses to direct
impacts. For example, Friedman (2013) suggests that climate change can be a ‘‘scary hidden stressor’’ as distant
communities might indirectly experience rises in the price
of a staple food as a result of the impacts of climate change
elsewhere, leading to political unrest. Cinner et al. (2011)
argue that it is critical to understand whether adaptive
responses lead to amplifying or dampening feedbacks.
Amplifying feedbacks are those that increase vulnerability
or erode social-ecological resilience over the longer term,
whereas dampening feedbacks reduce the impact of negative trends. Outcomes slide back and forth on a continuum
between vulnerability to sustainability for both social and
ecological criteria and change over time.
Sixth, responses to exposures can be characterized as
coping or adapting (Smit and Wandel 2006; Bennett et al.
2014a). Coping refers to short-term reactive or unplanned
responses to moderate the impacts of, or reduce sensitivity
to, exposures. Sometimes, coping strategies can be maladaptive and increase overall sensitivity and vulnerability
in the longer term. For example, intensification of fishing
effort is a short-term strategy often employed by fishers
that will lead to longer-term reductions in fish productivity
and abundance. Adapting refers to proactive planning of
longer-term courses of action that lead to beneficial outcomes for social and ecological systems. Adaptations fall
within three categories: (a) preventive actions to reduce
exposure and sensitivity, (b) strengthening adaptive
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N. J. Bennett et al.
Fig. 1 Conceptual framework for understanding community social-ecological vulnerability to multiple interacting exposures
capacity and (c) measures that improve social and ecological outcomes (Smit and Wandel 2006). Adaptive
strategies reduce exposure and sensitivity over the long
term and thereby reduce system vulnerability.
Finally, adaptation options are limited by institutional
and material constraints as well as social structures and
governance processes, culture and values (Adger et al.
2009a; O’Brien 2009; Adger et al. 2009b, 2013; ElrickBarr et al. 2014; IPCC 2014). Values mediate perceptions
of risk, determine desired outcomes or goals and influence
courses of action or adaptations (Hicks and Cinner 2014).
O’Brien and Wolf (2010) argue ‘‘…what is considered as
effective and legitimate adaptation depends on what people
perceive to be worth preserving and achieving. How to
adapt to climate change therefore hinges on the values
underlying people’s perspectives on what the goals of
adaptation should be.’’ Adaptation decision-making processes should make explicit and incorporate diverse values
as well as feasibility and constraints.
The aforementioned considerations are incorporated into a
conceptual framework for understanding and analyzing local
community vulnerability to multiple exposures (Fig. 1)—
which builds on work by others (Turner et al. 2003; Smit and
Wandel 2006; Perry et al. 2010). The framework shows
vulnerability as a dynamic process and outcome of socialecological systems that results from exposure to multi-scalar
123
and dynamic drivers, contextualized and differential sensitivities, direct and interactive impacts. Responses to perceived vulnerability include multiple coping and adapting
measures mediated by adaptive capacity and values. Values
define what are considered desirable or undesirable outcomes
for social or ecological spheres of a community system.
Typology of drivers, exposures, impacts
and interactions in coastal communities
This section reviews and categorizes drivers, exposures and
impacts experienced by coastal communities (Table 1).
The typology is separated into biophysical and socioeconomic drivers and exposures. Interactions within and
between the two spheres are also discussed.
Bio-physical drivers, exposures and impacts
Climate change related
Between 1955 and 2010, the temperature of top 700 meters
of the planet’s oceans increased by an average of 0.18 C,
with direct impacts on marine life and the human communities that rely on marine resources (Bunce et al. 2010b;
Levitus et al. 2012). One consequence of warming water is
Communities and change in the anthropocene: understanding social-ecological vulnerability and…
the reduction in sea ice. In Alaska, earlier spring ice break-up
is limiting spring fishing (a critical source of protein following the winter), while unpredictable ice conditions hinder
winter travel and access to marine resources (Moerlein and
Carothers 2012). As a result of the decline of polar ice sheet
mass, global mean sea level has risen by 0.19 meters during
the last century and could potentially surpass a 1-m rise by
2100 (Pfeffer et al. 2008; Church and White 2011). Sea level
rise will have profound impacts on coastal ecosystems, such
as a projected loss of 10–20 % of global mangroves by 2100
(McGranahan et al. 2007). Moreover, sea level rise poses
serious socioeconomic risk since 10 % of the world’s population lives in low-elevation (\10 m) coastal zones (Nicholls et al. 2007). Climate change is increasing the
frequency and magnitude of extreme weather events such as
tropical storms, which threaten coastal infrastructure and
exacerbate dangers fishers face at sea (Knutson et al. 2010;
Blythe et al. 2013). The warming of the upper layers of the
ocean is driving greater stratification of the water column,
changes in ocean circulation and variable precipitation patterns, all of which will perpetuate significant change in
coastal systems.
Climate change is also generating profound changes in
chemical ocean properties. Since the industrial revolution,
global oceans have absorbed 25 percent of anthropogenic
carbon dioxide (Le Quéré et al. 2012). As a result of this
uptake, the average pH of ocean surface waters has fallen
from 8.2 to 8.1 in a process known as ocean acidification
(Feely et al. 2009). While this decrease appears relatively
small, a decrease of 0.3–0.4 pH units by the end of this century
would represent the oceans’ lowest pH value in 40 million
years (Pelejero et al. 2010). Organisms that use carbonate
ions dissolved in sea water to form shells or skeletal structures, such as plankton, benthic molluscs, echinoderms and
corals, may be negatively impacted by lower ocean pH,
although species’ sensitivity will vary (Doney et al. 2009;
Kroeker et al. 2010). Since many of these organisms form the
foundation of marine trophic chains, ocean acidification may
have large ecological and social consequences (Fabricius
et al. 2011; Busch et al. 2013). Oceanic dissolved oxygen has
also decreased since 1960, albeit with strong regional variations (Keeling et al. 2010). Decreased dissolved O2 has
widespread implications for ocean productivity, nutrient
cycling, carbon cycling and marine habitats.
The changes in the physical and chemical conditions of
the world’s oceans have prompted a wide range of ecological
responses. Increasing evidence suggests that many reef fish
species are already living close to their thermal optima
(Rummer et al. 2014), meaning that that higher ocean temperatures will lead to reduced fitness or mortality (Munday
et al. 2008). Many marine species, ranging from turtles to
phytoplankton, have altered their distributions in response to
warming waters in order to maintain their optimal thermal
range (Polovina et al. 2008; Pike 2014). These relocations
Table 1 Typology of biophysical and socioeconomic drivers and exposures
Drivers of change
Exposures
Classification
Subclassification
Categories of exposure
Types of exposure
Biophysical
Climate change
Physical properties
Changing oceanic temperature
Reduced sea ice
Sea level rise
Extreme weather events and storm surges
Variable precipitation patterns
Changing atmospheric temperature
Chemical properties
Ocean acidification
Reduced dissolved oxygen
Ecological responses
Species range shifts
Reduced thermal optima
Coral bleaching
Ecosystem changes, invasive species, diseases and biodiversity loss
Other Environmental
Ocean-based
Overfishing
Habitat degradation
Hazards
Land-based
Earthquakes, tsunamis, fires, floods
Nutrient loading
Fresh water use
Pollution and garbage
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N. J. Bennett et al.
Table 1 continued
Drivers of change
Exposures
Classification
Subclassification
Categories of exposure
Socioeconomic
Demographic
Population
Types of exposure
Urbanization/gentrification
Changing age/sex distribution
Migration
In-migration from other regions or countries
Health
Chronic illness or acute diseases
Permanent or temporary out-migration
Injuries and disabilities
Economic
Macroscale economic
institutions and
processes
Mental, emotional and spiritual health
Economic globalization
National economic policies (e.g., market liberalization,
privatization, trade tariffs, subsidies)
Changing patterns of consumption
Changing livelihood opportunities and dependencies
Private sector investments and partnerships
Costs and credit
Increasing food costs
Rising livelihood costs (e.g., gear, fuel)
Access to credit
Market demand and prices
Changing demands for natural resource products
Changing market prices
Infrastructure and
technology
Increasing physical and
technological capacity
Coastal development
Bigger boats, larger engines, improved gear
Navigation and fish-finding technology (e.g., sonar, GPS)
Urbanization and restructuring of coasts
Tourism infrastructure
Extractive industries (Sand, mining, gas projects)
Aquaculture and mariculture
Basic services and social
infrastructure
Roads and public transportation
Schools, hospitals, electricity, water, waste treatment
Communication infrastructure and media
Engineered structures
Household
Dams, levees
Household infrastructure
Household assets
Governance and
policy
Changing governance
institutions and
structures
Organizational jurisdictions and mandates
Decision-making structures, processes (centralization,
inclusion, scale) and legitimacy
Societal norms and values
Networks of organizations and actors
Capacity and resourcing
Changing regulations
Changes in tenure and rights (property, harvest, access,
management)
Natural resource management, fisheries and conservation
policies
Conflict and security
Market-driven changes in allocations and harvesting
Conflicts between groups and resolution mechanisms
Politics and violence
Sociocultural
Shifting traditions,
knowledge and
values
Changing value systems
Networks and relationships
Shifting family relationships and gender roles
Loss or re-invigoration of traditional practices
Changing knowledge systems
Organizational networks and bridging social capital
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Communities and change in the anthropocene: understanding social-ecological vulnerability and…
may lead to local extinctions of fish populations, new species
interactions and profound changes in marine food webs
(Mueter and Litzow 2008). The southeastern Australian sea
urchin, for example, has recently expanded its range into
Tasmanian waters, where it has catalyzed a regime shift from
macro-algal communities into urchin barrens (Ling 2008). In
Norway, increases in ocean temperatures have driven collapses in the Barents Sea capelin stocks, with negative
impacts on both Arcto-Norwegian cod stocks and the fishing
communities in the region (Perry et al. 2011). Among the
most significant influences of climate change on the world’s
oceans are its impacts on habitat-forming species such as
corals. Mass coral bleaching and mortality, the result of
increasing temperatures, is already reducing the richness and
density of coral reef fishes with significant impact on reef fish
and fisheries (Bellwood et al. 2006; Cinner et al. 2012b).
Climate change is projected to change metabolic rates of
marine species, reduce primary productivity and increase
incidence of disease (O’Connor et al. 2009; McLeod et al.
2013). Climate change is also expected to challenge the
ocean’s capacity to meet the fish consumption demands of a
growing human population (Merino et al. 2012).
Other environmental
Overfishing may outweigh all other pervasive human disturbances to coastal ecosystems, including anthropogenic
climate change, pollution and degradation of water quality.
Overfishing alters marine population demographics (removal
of older individuals), spatial dynamics (changes in spawning
grounds) and species abundance and thus reduces the ocean’s
ability to provide food, maintain water quality and recover
from perturbations (Worm et al. 2006; Rockström et al.
2009a; Watson et al. 2014). Historic exploitation of sea otters
in the Aleutian Islands removed the primary predator of sea
urchins, resulting in massive deforestation of kelp forests via
an unregulated sea urchin population (Steneck et al. 2002).
The ability of Atlantic cod stocks to tolerate environmental
variability has been eroded by fishing, which removes older
fish and thus the buffering capacity provided by older individuals (Ottersen et al. 2006). Perhaps the most detrimental
impact of overfishing on coastal systems is the negative
effects on food and livelihood security for millions of smallscale fishers and their families particularly in the developing
world. In Mozambique, for example, over 80 % of smallscale fishers surveyed reported food insecurity, which they
attributed to declining catch resulting from overfishing
(Blythe et al. 2014). Within a few years, aquaculture’s contribution to fish supply for human consumption will exceed
that of wild capture fisheries and the industry stands to make
important contributions to food security. However, the
explosive development of coastal aquaculture has been criticized for the destruction of mangroves, saline intrusion,
damaging runoff and collection of wild broodstock, as well
as for forcing local stakeholders off their land and for converting multiple-use coastlines into single-use monocultures,
and may pose a serious threat to the well-being of coastal
communities (Duke et al. 2007; Paul and Vogl 2011; Zou
et al. 2011). Many other forms of coastal development and
land-use changes impact previous livelihoods.
Land-based activities produce profound impacts on
coastal systems. Over the last five decades, conversion of
forests and other ecosystems into agricultural land has
occurred at an average global rate of 0.8 % per year (Millenium Ecosystem Assessment 2005). The manufacture of
fertilizer for food production and the cultivation of leguminous crops convert more nitrogen from the atmosphere into
reactive forms than all of the Earth’s terrestrial processes
combined (Rockström et al. 2009b). Much of this new
nitrogen ends up in the environment, polluting coastal zones
and increasing incidence of hypoxia (Diaz and Rosenberg
2008). The extent and intensity of hypoxic zones in the Baltic
Sea, for example, have increased dramatically during the last
half-century with considerable impacts on biogeochemical
processes, ecosystem services and coastal habitats (Conley
et al. 2011). Annually over 8.5 million tonnes of phosphorous
flow into the world’s oceans, which is 8–9 times higher than
the natural background rate (Rockström et al. 2009a).
Phosphorus-induced anoxic events have been linked to mass
extinctions of marine life (Handoh and Lenton 2003).
Humans are currently the dominant driver of change in
global river flow (Shiklomanov and Rodda 2004). An estimated 25 % of the world’s river basins run dry before
reaching the oceans due to human use (Molden et al. 2007).
Global manipulations of the freshwater cycle affect biodiversity, food and health security, and ecological functioning,
such as provision of habitats for fish recruitment, carbon
sequestration and climate regulation (Rockström et al.
2009b). In central Mozambique, poor dam management has
contributed to severe flooding and villagers report saltwater
spreading up the estuary when the dam is closed, which
harms agricultural crops and contaminates drinking water
(Bunce et al. 2010b). Furthermore, humans are increasing the
river transport of sediment through soil erosion activities and
decreasing transport to the coastal zone through sediment
retention in reservoirs (Syvitski and Kettner 2011). Changes
in sediment supply can create significant changes in the
benthic environment of coastal estuaries, coral reefs, sea
grass communities and coastal fisheries.
Socioeconomic drivers, exposures and impacts
Demographic
Earth’s population is expected to grow by one billion
between 2013 and 2025, reaching over 8 billion people
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N. J. Bennett et al.
(UNDP 2013). Rapid increase in population density has been
prevalent in coastal zones, exposing coastal systems to new
risks (Nelson et al. 2005; Mee 2012). For example, migration
is one of the central drivers of increased exposure to flooding
as low-lying coastal areas are becoming urbanized (Adelekan 2010; Hanson et al. 2011). In Kenya and Mozambique,
increasing population along the coast, resulting from both
local population growth and migration of people in search of
economic opportunity, represents the main force exerting
pressure on the coastal fishery (Mangi et al. 2007; Blythe
et al. 2013). Brewer et al. (2012) demonstrate a negative
relationship between coastal population density and the
diversity and function of coral reef fishes.
Migration is another demographic change exerting
pressures on coastal systems. For example, in Mozambique, fighting inland during the civil war drove millions of
people to the coast, many of whom turned to fishing
(Blythe et al. 2013). Migrant fishers can be marginalized in
their new communities and exposed to poor living conditions, such as lack of safe drinking water or adequate living
quarters (Njock and Westlund 2010). Gentrification in
fishing communities in the USA, driven by increasing
coastal populations, changing demographics, and a desire
for access to natural amenities, is accelerating a move
toward non-marine-based economies that displace local
residents and their dependence on fishing (Colburn and
Jepson 2012). Another dimension of coastal migration is
the movement of young people out of fishing communities
to larger urban centers, resulting in the aging of traditional
fishing communities (Ommer and Team 2007).
Economic
The increasingly interconnected nature of our globalized
economy can create opportunities and challenges for coastal
communities. Increasing international trade has exposed
local producers to boom and bust cycles associated with
expanding luxury markets for marine products such as
shrimp (Blythe et al. 2014), shark fins and sea cucumbers
(Eriksson and Clarke 2015) and live reef fish (Fabinyi and
Dalabajan 2011). In India, Chinese interest in a range of
species that had previously been ignored by local fishers
produced an export-induced economic surge in the coastal
fishery in the late 1980s (Armitage and Johnson 2006).
However, the boom proved unsustainable and collapsed
following the Asian financial crisis in 1997. Trade-induced
increases in demand for marine resources have also resulted
in sequential depletions of internationally targeted species
(Berkes et al. 2006). Unregulated harvest of green sea urchin,
driven by demand from Japanese sushi markets, led to rapid
stock depletion in Maine (Steneck et al. 2002). However,
increasing international demand for sea cucumber has driven
overexploitation of stocks in the Western Indian Ocean
123
(Eriksson et al. 2010). Changes in the compositions of people’s diets, driven by rising per capita income and globalization of our food systems, have been characterized by less
consumption of starchy staples (rice, wheat and potatoes) and
more of fat, meat, fish, fruits and vegetables (Nelson et al.
2005). In some cases, this has led to better nutrition. However, in other cases, such as the Solomon Islands, traditional
diets have been replaced by consumption of processed foods
and associated with rising health concerns such as diabetes
(Schwarz et al. 2011).
Coastal communities are vulnerable to drastic price
changes driven by global market dynamics. In Mozambique, rising food prices have eroded traditional reciprocal
sharing networks and worsened food insecurity (Bunce
et al. 2010b; Blythe et al. 2014). Moreover, increasing
prices for fuel have led to reduced fishing days (Tuler et al.
2008; Bunce et al. 2010b). These impacts are exacerbated
for marginalized coastal people, including migrant and
subsistence fishers, who typically do not have access to
credit (Mills et al. 2011; Blythe et al. 2014). In some areas,
declining prices for marine products are reducing fishers’
income and driving increasing fishing pressure (Bennett
et al. 2014b). Constantly shifting prices and seasonal
demand for marine resources and tourism affect income and
household stability (Tuler et al. 2008; Bennett et al. 2014b).
In some cases, lower incomes have caused fishers to fish
longer hours, in increasingly dangerous conditions (Tuler
et al. 2013). Globalization has also driven a dramatic
increase in international tourism, with varying results for
coastal communities. On the Andaman coast of Thailand,
for example, some people have profited from tourism
through sales, restaurants and ocean tours, while others are
experiencing loss of livelihood options due to exclusions
from national marine parks (Bennett et al. 2014a). This
example demonstrates how rapid and drastic changes in
market characteristics and prices can benefit some and not
others, which can reinforce inequities for vulnerable groups.
Technology and infrastructure
Coastal landscapes are being transformed as a consequence
of new technology. Larger engines, more efficient gear and
improved fish-finding capabilities have significantly changed our relationship with marine resources. In many
countries, increasing fishing capacity has led to initial
increases in marine landings, followed by a marked decline
(Tuler et al. 2008; Perry et al. 2011; Blythe et al. 2013;
Kittinger et al. 2013). In India, the rise of trawling combined with motorization of the small-scale fleet has led to
conflicts between trawlers and small-scale fishers (Armitage and Johnson 2006). In Nunavut territory of Canada,
new technologies, such as citizen band (CB) radios, global
positioning systems (GPS), personal location beacons and
Communities and change in the anthropocene: understanding social-ecological vulnerability and…
consultation of satellite images of sea ice prior to travel,
have both increased safety for Arctic hunters by allowing
them to avoid dangerous areas and situations while
increasing risks for less experienced hunters in the case of
gear malfunction (Ford et al. 2006).
Rapid coastal development has many consequences.
Close to one quarter of the world’s population lives within
100 km of the coast, meaning that coastal systems have
experienced disproportionately rapid expansion of economic
activity and infrastructure development (Small and Nicholls
2003). Coastal dredging for land reclamation and port construction increases sedimentation and turbidity and has been
linked with significantly higher incidence of coral disease in
Western Australia (Pollock et al. 2014). Extractive industries, including mining and fossil fuel exploitation, can create
exposure to new stressors in coastal communities. During the
development of a gas project in Tanzania, promises of
equipment that would allow fishers to fish offshore went
unmet, villagers were forced to relocate, and protests escalated into violent conflicts (Bunce et al. 2010b).
In many areas, improvements in basic services have led
to better access to markets, schools, hospitals and communication technologies, such as cell phones, with primarily
positive impacts on coastal communities. Within weeks of
installation of a cell tower in south India, the local price of
fish converged where previously it varied highly from
market to market (Jensen 2007). By calling ahead from sea,
fishermen travelled to markets where fish were in low
supply leading to an average 5 % reduction in the price of
fish for consumers and a 9 % gain in income for fishers.
Infrastructure developments such as increasing road access
can reduce vulnerability in remote rural areas, which have
been geographically isolated and characterized by high
transaction costs, limited access to markets and low provision of government services or infrastructure (Béné 2009).
Governance and policy
Governance refers to the prevailing set of processes, institutions and policies through which the rules shaping the use
of coastal resources are set and revised (Bennett 2015).
Governance systems produce profound consequences for
coastal communities and linked ecosystems. Organizational
mandates, agency jurisdictions, formal decision-making
structures and processes are often realigned by governments
or through the interactions of influential stakeholders with
the governance system (Ommer and Team 2007; Chuenpagdee 2011). Changing societal norms and values can also
manifest in governance systems by stimulating new policy
directions (e.g., in fisheries or conservation) and determining
what constitutes appropriate governance processes (e.g.,
levels of participation, transparency, accountability). In
general, institutions can serve as enablers or inhibitors of
adaptive capacity and corrective adaptations (Tyler and
Moench 2012)—for example, in the adoption of an ecosystem-based approach to climate change (Elrick-Barr et al.
2014; Lukasiewicz et al. 2015). Levels of resourcing and
organizational capacity determine whether agencies are able
to learn through research, engage with the knowledge produced and implement management actions (Jantarasami
et al. 2010; Cvitanovic et al. 2014). Shifting relationships and
levels of collaboration between networks of organizations
and individuals involved in governance can also determine
the level of participation of local communities and the
effectiveness of coastal management initiatives (Bodin and
Crona 2009; Alexander and Armitage 2015).
Governance structures and decision-making processes
strongly affect whose voices are heard in decision-making
and how local knowledge and needs are incorporated. This
means that in order to engage local knowledge in evidencebased decision-making, governance processes themselves
may need to be revised. There is a growing literature on the
potential for combining local knowledge systems with scientific knowledge to cope with change in resource and
ecosystem management (Haggan et al. 2007; Armitage et al.
2007). For example, in the Solomon Islands, indigenous
knowledge and sea tenure systems were used in combination with scientific knowledge to establish marine protected
areas for bumphead parrotfish conservation (Aswani and
Hamilton 2004). Community-based and collaborative (e.g.,
co-management) initiatives have reduced exposure to
threats such a stock declines (Pinto da Silva and Kitts 2006)
and have created a greater degree of democracy in regard to
resource governance (Cinner et al. 2012a) in many coastal
communities, although the impacts of collaborative initiatives vary widely within the social-ecological complexity of
coastal systems (Cohen and Alexander 2013).
In other cases, regulatory changes can create negative
consequences for coastal communities when marine resources or spaces are reallocated or when ‘‘ocean grabbing’’
occurs (Bennett et al. 2015). The establishment of marine
protected areas (MPAs) alters resource-use rights and has
been associated with increasing incidence of elite control of
resources, the exclusion of resource users and the criminalization of local people (West et al. 2006; Bennett and Dearden
2014). In Tanzania, conflict over resource access in a MPA
escalated to the use of tear gas by police on local fishers
(Bunce et al. 2010b). Even when reserves are specifically
designated for the benefit of local users, such as the 3000-m
limit in Thailand, conflict can arise between illegally fishing
commercial vessels and small-scale fishers (Bennett et al.
2014b). Quota systems in the USA can increase unsafe
decision-making and risk-taking by fishers (Tuler et al. 2008).
For example, when a fishery is approaching its quota, fishers
may race to finish their fishing before the quota is reached,
even if it means venturing out in bad weather. Furthermore,
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N. J. Bennett et al.
consequences of regulatory change extend beyond those
directly involved in marine resource harvesting. Tuler et al.
(2013) documented how a regulatory change, introduced by
the New England fishery Management Council in 2010, led to
fewer fishing trips meaning that onshore workers lost hours
and that the availability of dockage shrunk, since more vessels remained in port longer.
Sociocultural
In many coastal communities, concern about shifting values
and norms is rising. Along numerous coasts, the use of
marine resources has been regulated through taboos and
beliefs controlled by community elders. These informal
restrictions on fishing practices acted to maintain social
control and access to common pool resources (Foale et al.
2011). Recently, many of these traditions have been eroded
due to changing religious and cultural norms and declining
interest of younger generations (Mangi et al. 2007; Blythe
et al. 2013). A second, quite different impact of shifting
values and norms can be seen in the Canadian Arctic. As Inuit
hunters become more integrated into a ‘‘Western culture,’’
traditional knowledge is being lost and risk-taking behavior
has risen. Time off from formal employment must be booked
months in advance, so hunters feel committed to a particular
time regardless of weather or safety concerns (Aporta 2004).
Younger hunters rely less on traditional knowledge and
practice less caution due to perceived safety nets provided by
technological developments (Ford et al. 2006). Changing
family dynamics are creating exposure to new stressors.
Following the cod moratorium in Newfoundland, Canada,
some families replaced male fishing crew with wives in order
to concentrate diminished earnings within the household
(Grzetic 2004). In Kenya, the capacity to participate in traditional family reciprocity is being challenged by growing
food insecurity (Casale et al. 2010). These examples reflect
how shifting values and norms can create exposure to new
stressors in coastal systems.
Interactions between exposures and adaptations
A key challenge for those living and working in coastal
social-ecological systems is that multiple exposures do not
simply converge—they interact. Moreover, most coastal
systems are characterized not by single interactions
between exposures but by multiple overlapping interactions. Furthermore, multiple exposures interact through
autonomous, cascading, cross-scale and adaptive feedbacks
leading to differential impacts and community social and
ecological vulnerability outcomes depending on the context. Interactions and feedbacks can amplify, dampen or
mitigate the impact of individual exposures. Due to the
123
unlimited number of different contexts and factors
involved, it is neither possible nor desirable to attempt to
describe the multitude of expected and unexpected interactions between different exposures. Additionally, many
impacts and interactions are unanticipated or novel, making vulnerability outcomes unpredictable. Below we provide two illustrative examples of interactions among
exposures and adaptations.
In the coastal city of Quy Nhon, Vietnam, an analysis of
sources of flood risk in peri-urban areas found that existing
residents were placed at increased risk of catastrophic
flooding due primarily to urban development patterns and
livelihood threats, rather than climate and hydrological
changes per se (DiGregorio and Huynh 2012). The lack of
integration between construction of new transportation
infrastructure, dikes, urban development zones with land
fill to raise surface elevation and drainage in low-lying
coastal floodplains combined with displacement due to
urban land acquisition created a flood risk profile for
community members that had increased in unexpected
ways. While climate change was not yet a central factor in
this case, increased likelihood of extreme climate events
will contribute both to uncertainty and magnitude of
adverse outcomes. This pattern of multiple exposure and
unintended consequences creates dynamic and unanticipated risks for those community members who have limited choices.
The vast majority of the literature on interactions
focuses only on the negative impacts of interacting stressors, neglecting to take into account the opportunities that
can arise from macro- and mesoscale changes or the ways
that responses (or adaptations) can amplify, dampen or
mitigate single or multiple exposures. Our second example
illustrates how drivers of change at various scales can
interact to create both opportunities and constraints at the
community scale. In the early 1990s in Mozambique,
macroeconomic policy shifts (market liberalization)
opened the economy to foreign investment for the first
time, which led to the establishment of a French-owned,
export-oriented shrimp farm on the central coast. The
shrimp farm created local employment opportunities,
benefitting several hundred people in a context where wage
work is extremely limited. Yet, it also exposed shrimp farm
employees to a new stressor (termination of their jobs due
to shrimp disease outbreak) and it blocked access to previously communal land used by the greater community for
making salt. As a result, people are moving into coastal
fisheries, where climate changes are causing more frequent
and severe storm events and increasing the risks fishers
face at sea. Thus, macroscale drivers of changes created
exposure to new stressors that created positive and negative
impacts on community vulnerability (Blythe et al. 2015).
Communities and change in the anthropocene: understanding social-ecological vulnerability and…
Assessing vulnerability and identifying
adaptations: a pragmatic approach
In this section, we propose a pragmatic yet comprehensive
approach for assessing coastal community vulnerability
based on the framework and typology introduced in the
previous sections. The intent of this approach is to shift the
analytical focus from a particular hazard or exposure to the
community itself, which will inevitably be dealing with
multiple exposures. The aim is to provide practical guidance to researchers, practitioners, managers and policy
makers for identifying key drivers of change, exposures
and impacts and for developing contextually appropriate
response strategies without being overly prescriptive. In
brief, the following elements are essential for analyzing
social-ecological vulnerability and identifying adaptive
responses.
1.
2.
3.
4.
5.
6.
7.
8.
9.
10.
Identify important social and ecological components
of the system of interest and establish criteria for
evaluating each component;
Characterize the nature and severity of socioeconomic and biophysical drivers and resulting exposures and potential impacts;
Describe the autonomous interactions and feedbacks
between drivers, exposures and impacts within and
between social and ecological systems;
Analyze components of latent adaptive capacity and
potential barriers to adaptation;
Identify potential adaptations that reduce sensitivity
or exposure, improve adaptive capacity and enhance
social-ecological outcomes to individual stressors;
Characterize interactions resulting from adaptations
(i.e., amplifying, dampening, and mitigating) and
analyze trade-offs among social and ecological
outcomes of potential adaptations;
Identify adaptations that lead to win–win and mostbenefit social-ecological outcomes;
Prioritize actions to reduce sensitivity, improve
adaptive capacity and enhance social-ecological
outcomes based on feasibility (adaptive capacity)
and desirability (values) of outcomes;
Identify who is responsible for implementation and
what resources will be provided; and
Implement, monitor and adapt.
These elements build on and extend rich literature in
various fields. For example, there is extensive literature
exploring characterization of social-ecological systems
(Folke et al. 2003; Turner et al. 2003; Walker et al. 2004)
and analysis of adaptive capacity (Marshall et al. 2010;
Engle 2011; Bennett et al. 2014a). Climate change vulnerability and adaptation planning literature have
emphasized important best practices—e.g., facilitating
inclusive and place-based analyses, focusing on building
adaptive capacity, strengthening institutions, integrating
diverse knowledges, identifying no-regrets adaptations,
prioritizing actions, clarifying resourcing and responsibility, understanding differential impacts, implementing
cooperative and adaptive management (Smith et al. 2003;
Leary et al. 2008; Burton 2009; Leary et al. 2009; Ensor
and Berger 2009; Hall 2011; Bundy et al. 2015; Nalau et al.
2015). Yet, the majority of the previous literature has
focused on single stressors and, in particular, climate
change.
Lacking are simple methods for understanding vulnerability to multiple interacting exposures and clear and
effective processes for identifying adaptations that take
into account multiple exposures. Below we discuss methods for: (a) characterizing exposures and impacts, (b) interrogating the interactions between exposures and
(c) identifying effective adaptations to multiple exposures
that reduce sensitivity, increase adaptive capacity and
enhance outcomes. Descriptions, uses and examples of
applications of these methods are provided in Table 2.
Characterizing exposures and impacts
The majority of studies that have sought to characterize the
nature and severity of exposures in a given locale have
been externally driven efforts that focus on single hazards.
We suggest that the typology presented here could provide
a comprehensive frame of reference for future communitycentered vulnerability assessments using qualitative,
quantitative or mixed methods with a focus on local perspectives and experiences. For example, each category of
driver or type of exposure in the framework could be
explored through qualitative interviews, or results emerging from interviews could be compared with or coded
against the framework. Interviewing could be used to
examine local perceptions of the presence or absence of
specific exposures that are occurring in each locale, the
severity of exposures and the drivers of local exposures
(Blythe et al. 2015). Different exposures could be ranked
by importance or rated (e.g., on a Likert scale of 1–5) to
determine the relative severity of the exposure or the sensitivity of communities, households or groups (Tschakert
2007; Bennett et al. 2014b). As Eakin and Leurs (2006)
argue, it is essential to distinguish the most relevant and
impactful drivers. In particular, it is crucial to identify
extreme events—e.g., irregular or unpredictable exposures
to which communities are highly sensitive—and ‘‘Achilles
heel’’ vulnerabilities—i.e., those slow variables that significantly outweigh other stressors and that might undermine adaptations if sensitivity is not reduced through
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N. J. Bennett et al.
mitigative actions. Two examples of acute exposures are
the 2004 tsunami in Southeast Asia or rapid hypoxic events
that undermine localized conservation measures. Examples
of chronic stressors include the steadily increasing impacts
of ocean acidification for the shellfish industry or of sea
level rise for communities that are situated in low-lying
coastal areas. Quantitative analysis of exposures would
also allow for scaling up research for broader-scale comparisons of exposures, sensitivities and differential
impacts—for example, among communities and across
regions or countries (e.g., Cinner et al. 2011). Our typology
could be used as the basis of participatory focus groups or
discussions on historical, present or future changes (e.g.,
Bennett et al. 2014c). Yet, future work in this area needs to
move beyond just describing the drivers and exposures to
understanding their impact, importance, causal mechanisms and interactions between exposures (Bunce et al.
2010b).
suggest that a more systematic approach is required. Mixed
methods approaches and triangulation of data from perceptual studies, biophysical studies, historical methods and
policy studies will create a cohesive picture of how different trends, shocks and adaptations are interacting. Multisited, spatial and historical accounts should be incorporated
to help to reconcile different scales and speeds of change
and to tease out the impact of contextual factors (e.g.,
geography, ecology, demographics, economics) and
specific events. Whichever methods are employed, there is
a need to better understand and typify whether the interactions are mitigative (o), amplifying (?) or dampening
(-) across different categories and indicators of social and
ecological change and to demonstrate effect size—which
will require meta-analyses drawing on the results of multiple local studies.
Exploring interactions
The cataloging and ranking of exposures and their interactions may seem like an academic exercise. However, as
Hall (2011) argues ‘‘…the relative importance of the various drivers and the pathways through which they might act
must be weighed to help prioritize actions.’’ This signals an
important shift from research about change to research for
change (Fazey et al. 2015). The identification and prioritization of effective adaptations, in the context of multiple
interacting exposures, is a significant challenge requiring
foresight and long-term thinking to avoid coping strategies
or ‘‘manipulations’’ (Thomsen et al. 2012) that lead to
maladaptations and increased sensitivity. Whenever possible, it behooves decision makers to identify first ‘‘noregrets’’ adaptations that reduce sensitivity and lead to
win–win outcomes. Addressing shortcomings in some
facets of adaptive capacity may always be a ‘‘no-regrets’’
solution (Adger et al. 2003). Resilience scholars suggest
that organizational and institutional learning, diversity of
livelihoods and knowledge, access to assets and adaptive
co-management processes decrease vulnerability (Folke
et al. 2003; Cinner et al. 2009; Bennett et al. 2014a). Mills
et al. (2011) propose that non-sectoral interventions, such
as improved community sanitation, might have the greatest
effect on reducing vulnerability for the most people.
However, it will often be necessary to recognize and make
trade-offs in order to identify ‘‘least-harm’’ adaptations that
will lead to the most beneficial outcomes.
In a similar manner to how interactions are classified,
the mitigative (o), amplifying (?) or dampening (-)
effects of potential adaptations on social and ecological
outcome criteria might be explored. There are numerous
trade-off approaches, deliberative decision-making methods and participatory research methods that can facilitate
choice of adaptation in the face of multiple exposures such
The dynamic interactions between multiple exposures have
been examined using numerous participatory, qualitative
and/or quantitative methods. Qualitative, ethnographic and
visual methods will lead to rich narratives and historical
accounts of local experiences of the interactions between
stressors (Moerlein and Carothers 2012; Bennett and
Dearden 2013). For participatory methods, previous studies
have used mental models (Bunce et al. 2010a, b), the
Driver-Pressure-State-Impact-Response (DPSIR) framework (Mangi et al. 2007; Suckall et al. 2014) and community-based scenario planning processes (Bennett et al.
2014c) to explore interactions between stressors. The following qualitative or semiquantitative methods also show
some promise for exploring interactions—Bayesian networks, inference trees, expert judgments, influence diagrams, participatory mapping, historical timelines, trend
lines, importance–incidence charts and causal dynamics
(Bunce et al. 2000; Tomei et al. 2006; Chevalier and
Buckles 2008; Gregory et al. 2012; Chevalier and Buckles
2013; Ban et al. 2014). Quantitative methods and multivariate statistical approaches—including factorial multiple
ANOVA, ANCOVA, regression, canonical correlation,
multi-way frequency, logistic regression, discriminate
function, non-metric, cluster and principle component
analyses—can also be useful for exploring the relationships
between interacting exposures (see Menzie et al. 2007).
Spatial approaches (O’Brien et al. 2004) are also useful but
may be more applicable at broader scales.
Researchers are applying a miscellany of methods in
diverse contexts to understand the interactions between
multiple exposures—usually with a greater focus on either
the social or the ecological components of the system. We
123
Identifying and prioritizing adaptations
Communities and change in the anthropocene: understanding social-ecological vulnerability and…
Table 2 Examples of methods for characterizing exposures and impacts, exploring interactions and identifying adaptations
Topic
Methods
Description
Examples and references
Characterizing
Exposures
and Impacts
(Nature and
Severity)
Qualitative
interviews
Open-ended interviews with community members, knowledge holders
or experts allows for rich and contextualized narratives and
historical descriptions of perceived exposures, potential drivers and
associated risks or impacts. Perceptions are understood as relational
and subject to multiple meanings based on interpretations
Bunce et al. (2010b), Fabinyi
(2010), Moerlein and Carothers
(2012), MacDonald et al. (2013),
Bennett et al. (2014b), McCubbin
et al. (2015)
Participatory
methods
Workshops or focus groups with stakeholders, decision makers and/or
experts can employ a variety of participatory methods to elicit lists,
narratives, matrices, historical timelines or artistic expressions of the
changes that are occurring and how these are impacting
communities. Severity can be documented numerically, through
participatory ranking or rating exercises, or qualitatively. Skilled
facilitation is required to ensure all voices are heard
Kindon et al. (2007), Tschakert
(2007), CARE 2009, Mills et al.
(2011a), Chevalier and Buckles
(2013)
Quantitative
rating or
ranking
Household surveys in single or multiple sites can be used to
quantitatively rate or rank the impact of stressors or exposures on
different social, economic and ecological outcomes. Surveys allow
for incorporation of larger samples and comparison among groups
(livelihoods, genders, socioeconomic status, ethnicity),
communities, regions or countries. All exposures need to be
included
Bunce et al. (2010b), Mills et al.
(2011a), Cinner et al. (2012b);
Bennett et al. (2014b), Blythe et al.
(2015)
Spatial
approaches
People’s spatial knowledge of exposures and their impacts can be
elicited using participatory methods—e.g., collaborative mapping,
transect walks, hazard mapping, participatory geographic
information systems—and spatial information management tools.
Maps can also be useful tools for sharing and discussing interactions
and potential adaptations
Ban et al. (2009), Raymond et al.
(2009)
Expert
elicitation
techniques
Opinions regarding exposures and their relative impacts can be
elicited from experts, who are knowledgeable about social or
ecological aspects of the system, through such methods as Bayesian
methods, Delphi processes or nominal groups. This can be done
individually or in a focus group setting
Richards et al. (2013), Ban et al.
(2014)
Arts-based
methods
Various arts-based methods (e.g., participatory drawing, photovoice,
participatory video, photohistory, documentary film making, digital
storytelling) can provide in-depth empirical insights into exposures
and impacts to community well-being and environmental health.
These can serve as basis for conversations and deliberations around
adaptations
Kunuk and Mauro (2010), Walker
(2012), Bennett and Dearden
(2013), Lemelin et al. (2013),
Willox et al. (2013)
Mental
models
Mental models are people’s cognitive frameworks of the world. They
can provide insights into perceived relationships and feedbacks
between different exposures. Data are collected through individual
or group interviews and analyzed using content analysis, procedural
mapping, task analysis, cognitive mapping and consensus analysis
Bunce et al. (2010b), Jones et al.
(2011), Lynam et al. (2012)
DriversPressuresStatesImpactsResponses
The DPSIR framework provides a tool to organize information on
drivers, exposures (pressures) and impacts (states and impacts) on
social and ecological outcomes (states). The DPSIR framework can
help to identify trade-offs between adaptation, mitigation and
development response options and to avoid maladaptations. Does
not help to understand bridges, barriers or steps to achieve actions
Tscherning et al. (2012); Suckall
et al. (2014), Maccarrone et al.
(2014), Breslow (2015)
Participatory
methods
Participatory methods, such as force field, causal dynamics,
vulnerability matrix, influence diagrams, can be used to assess the
perceived level of positive or negative impact of key factors (drivers
and exposures) on social and/or ecological problems and to identify
how these factors interact to produce net positive, negative or
neutral outcomes
Chevalier and Buckles (2008),
CARE (2009), Mills et al. (2011b),
Gregory et al. (2012), Chevalier
and Buckles (2013)
Quantitative
and
multivariate
analyses
Multiple case studies, meta-analyses or a systematic reviews would
allow for quantitative comparisons and multivariate analyses (e.g.,
factorial multiple ANOVA, ANCOVA, regression, canonical
correlation, multi-way frequency, logistic regression, discriminate
function, non-metric, cluster and principle component analyses) to
explore relationships between interacting exposures
Menzie et al. (2007)
Exploring
Interactions
(Additive or
Dampening)
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N. J. Bennett et al.
Table 2 continued
Topic
Identifying and
Prioritizing
Responses
(Amplifying,
Mitigative and
Adaptive)
Methods
Description
Examples and references
Spatial
approaches
See above description. Interactions between the different exposures
might also be explored using spatial overlays and qualitative
discussions of maps
(O’Brien et al. 2004)
Structured
decisionmaking
Structured decision-making (SDM) is an approach that seeks to
identify options, evaluate the outcomes of alternate courses of
action, find ‘‘win–win’’ solutions, clarify trade-offs and provide a
space for communicating views regarding options and trade-offs. It
does not provide solutions but can inform deliberations on difficult
decisions while making processes transparent and efficient. SDM
employs rigorous decision-making methods, such as strategy tables,
consequence tables, participatory cost–benefit analysis, to identify
trade-offs and prioritize responses
(Espinosa-Romero et al. 2011;
Gregory et al. 2012)
Multi-criteria
decision
analysis
Stakeholder judgments are used to evaluate different alternatives or
options using ranking or weighting algorithms. The results can be
communicated to facilitate decision-making. Primary data (from
document reviews, interviews or focus groups) are required to
identify the range of options. MCDA is useful when decisions
involve uncertainty but need to be made quickly
(Kiker et al. 2005; Scheuer et al.
2011; Porthin et al. 2013;
Sahin et al. 2013; Munaretto
et al. 2014)
Cost–benefit
and costeffectiveness
analysis
Cost–benefit and cost-effectiveness analysis provides tools for
comparing net economic efficiencies of adaptation options across
multiple climatic and other exposures. It is useful for examining
public policies or actions when key effects can be easily monetized
(Leary 1999; Wegner and
Pascual 2011; Kull et al. 2013;
Mechler and Nabiul Islam
2013; Watkiss et al. 2014; Nay
et al. 2014)
Futures,
planning and
deliberation
methods
Futures planning methods—e.g., scenario planning, visioning,
backcasting, participatory integrated assessments, adaptation
pathways approaches, transformation planning—can provide a
forum for exploring possible and/or desirable futures given current
and unknown trends or shocks and deliberating on response
strategies. Analysis of drivers, exposures, impacts, responses and
outcomes can be done using participatory, technological or
combined approaches
(Swart et al. 2004; Evans et al.
2006; Salter et al. 2010;
Sheppard et al. 2011; Cinner
et al. 2011; Smith et al. 2013;
Hamilton et al. 2013; Moore
et al. 2014; Butler et al. 2014;
Wise et al. 2014; Reid et al.
2014)
Multiple case
study
comparisons,
synthesis and
historical
methods
Methods that draw on multiple case studies and historical cases for
syntheses or comparisons provide a tool for identifying similar cases
and insights into past adaptations that have worked. These
understandings can provide general lessons that can be applied to
current contexts
(Bussey et al. 2012; Bundy et al.
2015; Fazey et al. 2015)
as: structured decision-making processes (EspinosaRomero et al. 2011; Gregory et al. 2012), participatory
and weighted multi-criteria analysis (Scheuer et al. 2011;
Heck et al. 2011; Bhave et al. 2014), quantitative or
qualitative cost–benefit analysis (van den Bergh 2004) or
the (DPSIR) framework (Mangi et al. 2007; Suckall et al.
2014). Efforts to identify adaptations could also draw on
future methodologies such as scenario planning, visioning
or backcasting (Berkhout et al. 2002; Kloprogge and
Sluijs 2006; Sheppard et al. 2011; Hamilton et al. 2013;
Evans et al. 2013).
Whichever approach is used to select adaptation actions,
a number of important decision criteria should be incorporated from earlier steps in the analysis including: key
social and ecological system components to maintain system stability; normative criteria and values for social and
ecological outcomes; nature and severity of drivers and
123
exposures; contextual factors that influence sensitivity;
potential impacts on social-ecological systems; interactions
among stressors and resulting from adaptations; and the
feasibility of and barriers to adaptations based on adaptive
capacity and institutional context. Exploring these criteria
may require using several different decision-making
approaches in combination. Qualitative or quantitative
analysis of trade-offs will not lead to decisions but can
contribute to evidence-based deliberative decision-making
processes that incorporate various perspectives and values.
Further work is needed that compares the processes, outputs and outcomes of the different decision-making tools
and trade-off approaches, particularly in the context of
adaptation planning. A review and comparison of the
strengths, weaknesses, insights and implications of different approaches for assessing adaptive capacity is also
warranted.
Communities and change in the anthropocene: understanding social-ecological vulnerability and…
Concluding thoughts
In this paper, we provided a framework and typology of
drivers and exposures to analyze community social-ecological vulnerability and suggested processes and methods
for better understanding how multiple interacting exposures
act on coastal communities. We hope that this article will
provide stimulus for future empirical work on vulnerability
and adaptation to multiple interacting exposures, including
facilitating further exploration of interactions, broader-scale
analyses and comparisons between sites. However, we want
to emphasize that this is not just an academic exercise.
Change is a ubiquitous force that has very real impacts for
communities and the ecosystems on which they rely.
Management interventions tend to be driven by the policy
du jour—whether it is biodiversity conservation, marine
protected areas, climate change adaptation or disaster
management—resulting in a narrow analytical focus that
ignores or downplays the complications of multiple interacting exposures. This can result in the identification and
implementation of well-intended policy and expensive
programmatic responses that do not adequately address the
issues or, worse yet, that further exacerbate sustainability
challenges for local communities. We contend that our
framework, typology and pragmatic approach will improve
understanding of the types of socioeconomic and biophysical changes occurring and how these are interacting and
impacting communities in order to identify more effective
leverage points (whether via local actions or broader policies and programs) within the system for decreasing the
vulnerability of communities to change.
Acknowledgments The initial meeting that led to this paper was
hosted by the Centre for Global Studies at the University of Victoria.
The lead author (NJB) was supported by a SSHRC Postdoctoral
Fellowship and a Liber Ero Fellowship during the writing of this
manuscript. All authors would like to acknowledge the support of
their respective institutions.
Open Access This article is distributed under the terms of the Creative Commons Attribution 4.0 International License (http://creative
commons.org/licenses/by/4.0/), which permits unrestricted use,
distribution, and reproduction in any medium, provided you give
appropriate credit to the original author(s) and the source, provide a link
to the Creative Commons license, and indicate if changes were made.
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