BULLETIN OF MARINE SCIENCE. 87(2):251–274. 2011
doi:10.5343/bms.2010.1089
Bridging the divide Between Fisheries
and Marine Conservation sCienCe
Anne K Salomon, Sarah K Gaichas, Olaf P Jensen, Vera N Agostini,
NA Sloan, Jake Rice, Tim R McClanahan, Mary H Ruckelshaus,
Phil S Levin, Nicholas K Dulvy, and Elizabeth A Babcock
aBstraCt
researchers from traditionally disparate disciplines and practitioners with
typically incongruent mandates have begun working together to better understand
and solve marine conservation and sustainable yield problems. Conservation
practitioners are recognizing the need to achieve conservation goals in seascapes
that are a source of livelihood and food security, while isheries management is
realizing that achieving economically and ecologically sustainable isheries requires
an understanding of the role of biodiversity and ecosystem dynamics in ishery
production. Yet, tensions still exist due to the unique histories, epistemologies,
cultures, values, and quantitative techniques of isheries and marine conservation
science, and the often-divergent objectives of the institutions and organizations
these academic disciplines inform. while there is general agreement on what
needs to be achieved (less overishing, recovery of depleted ish stocks, reduction
in bycatch and habitat impacts, jobs, food production), speciic objectives and
how best to achieve them remain contentious and unresolved. By analyzing
three contemporary yet controversial marine policies (ecosystem-based ishery
management, marine protected areas, and catch shares) and speciic case studies,
we demonstrate how both isheries and marine conservation science can be used
to provide clear scientiic advice to practitioners and provide empirical evidence of
the beneits of bridging the disciplinary divide. Finally, we discuss future prospects
for collaboration in an emerging issue at the nexus of conservation and ishery
management: eco-certiication. drawing on lessons learned from these empirical
examples, we outline general processes necessary for clearly deining multiple
conservation and isheries objectives in working seascapes. By bridging the divide,
we illuminate the process of navigating trade-ofs between multiple objectives in a
inite world.
a convergence between marine conservation and isheries science has begun.
Fisheries science is recognizing the need to move from conventional single-species
assessments of yield towards multi-species approaches, including assessing the larger ecosystem consequences of ishing. he ishery management community is also
expanding its use of policy instruments, from rights-based isheries to cooperative
structures and certiication. Concurrently, marine conservation science is drawing
increasingly on economics and the social sciences, and conservation practitioners are
working towards achieving ecosystem protection while maintaining economically
viable isheries, ishing communities, and other activities that depend on marine resources. Collectively, there is increasing acknowledgment that marine conservation
is largely about managing multiple human uses of the ocean. hough the terminology difers between disciplines, there is general agreement that science is needed to
support two broadly deined objectives: (1) conserve biodiversity and (2) sustain proBullein of Marine Science
© 2011 Rosensiel School of Marine and Atmospheric Science
of the University of Miami
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ductive isheries. achieving these two objectives, at least in the short- and mediumterm, will require diferent policies and management actions, as current measures
tend to achieve one at the expense of the other. it will also require increased communication, understanding, and integration of the sciences that underpin marine
conservation and isheries management—i.e., marine conservation biology, marine
ecology, isheries science, economics, and the social sciences.
while convergence toward common goals and perspectives has begun, the details
remain problematic. Fisheries and marine conservation science have diferent histories, epistemologies, cultures, and priorities, leading sometimes to strikingly divergent views on the state of isheries and marine ecosystems, and on how to achieve
sustainability (Ludwig et al. 1993, rosenberg et al. 1993, Myers and worm 2003,
walters 2003, hilborn 2006, worm et al. 2006). Moreover, their separate professional societies, distinct journals, and diferent norms can impede communication,
the sharing of scientiic tools, and the acceptance of new ideas, and can lead to wildly
diferent inferences made from the same data. Finally, the objective of maintaining
or restoring marine biodiversity often conlicts with the objective of maintaining or
increasing food supplies from the sea, because the level of ishing required to achieve
the latter typically compromises the former (Brander 2010). hese diferences in objectives, tools, and inferences need to be navigated and put into practice by a variety
of government agencies and nongovernmental organizations that often have conlicting mandates (Fig. 1). For example, Parks Canada is mandated to protect ecological
integrity (national Parks act 2000), while Fisheries and oceans Canada is mandated
to exploit isheries at maximum sustainable yield (MsY, Fisheries act 1985). real
structural incompatibilities (i.e., trade-of between extinction risk for species a and
exploitation of species B) can make conlicting mandates diicult to resolve unless
these underlying interactions are quantiied and the trade-ofs are made explicit.
we argue that the opposing views arise from a lack of clearly stated and often
conlicting objectives and divergent values. he vehemence with which these
contrasting views have been expressed has not helped to foster constructive dialogue
aimed at making values, objectives, and diferences more transparent. although
both communities are converging on a triple bottom line—ecosystem, social, and
economic sustainability—there are diverging views on how best to achieve these
goals (hilborn 2007a,b), creating a gap that needs to be bridged. Furthermore, both
expert and stakeholder groups often difer over the short-term policies and actions
they think should receive priority. it is our opinion that opposing scientiic views are
healthy and dialectic1 between disciplines should be preserved to propel scientiic
progress. however, conlicts over assumptions and unexpressed or misunderstood
objectives are symptoms of ideological clashes rather than of scientiic disputes, and
do little to advance our understanding of how best to conserve marine ecosystems
and the goods and services they deliver. here, we attempt to pinpoint the problems
and ofer several concrete solutions. our goal is to enhance the dialogue, bridge
the divide, and spark cultural integration among ishery and marine conservation
disciplines and institutions to improve the scientiic basis on which the management
of marine ecosystems is based.
1 a method of argument based on a dialogue between two or more people who may hold opposing views
yet wish to seek truth through the exchange of their viewpoints while using reason (Plato. he Republic,
Book X). his is in contrast to a debate, in which both sides are dedicated to their viewpoint and only
wish to win the argument by proving themselves right or the other side wrong.
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Figure 1. Fisheries and marine conservation objectives have traditionally differed. Bridging the
divide between isheries and marine conservation science will improve the effectiveness of conservation and management policy instruments. EBM = ecosystem-based management, MPA =
marine protected area.
one of the key research challenges in sustainability science is identifying the policy instruments and actions that best promote the sustainable use of ecosystems
(essington 2010). to demonstrate the “value added” from bridging the disciplinary
divide, we discuss three contemporary and increasingly common marine policies:
ecosystem-based management (eBM), marine protected areas (MPas), and catch
shares, as well as the emerging application of eco-certiication. all of these tools have
generated debate between the marine conservation and isheries sciences, yet their
design and implementation have the potential to beneit from the strengths of both
disciplines. For each policy, we describe speciic case studies, with which at least one
of the authors has irst-hand expertise, to add to the growing number of practical
examples illustrating the additional beneits from using both isheries and marine
conservation science techniques and approaches. hese case studies also serve as a
clear demonstration that to bridge the divide, both isheries and marine conservation
science need to broaden their interactions with other disciplines (including economists, anthropologists, sociologists, archaeologists, historians, political scientists),
and intensify their interactions with policy makers, resource users, local communities, and levels of governance in working seascapes. we propose that biodiversity and
food production objectives can be reconciled by using a combination of diverse management and conservation policies (including catch restrictions, gear modiications,
eBM, catch shares, and marine reserves) tailored to local social-ecological contexts.
Finally, we stress the critical importance of an inclusive stakeholder process to develop speciic objectives for regional science and management, and the critical importance of a legislative mandate to maintain the process. within this process, we
encourage diversity in the dialogue and recognize the need to navigate trade-ofs
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associated with any vision for the state and use of the marine environment. agreement on common objectives, clariication of the trade-ofs, and inding solutions that
minimize trade-ofs will help us move forward.
Multiple objectives
Fisheries and marine conservation scientists generally operate within two diferent
contexts as the application of their work is often linked to practitioners that need to
meet diferent management objectives: marine ecosystem conservation vs achieving
sustainable social and economic beneits from isheries. Fisheries managers typically
aim to keep stocks around a target reference point, typically the biomass that produces some proxy of MsY, and avoid going beyond biomass or ishing mortality limit
reference points (Caddy and Mahon 1995). increasingly, these management measures
are applied to non-target species as well as target species (e.g., reuter et al. 2010).
Conservation practitioners tend to be more concerned with the risk of exceeding
reference points and with risks to habitat and biodiversity than with maximizing
yield. while the contexts are separate (isheries management vs marine conservation), objectives can converge where there is agreement about the reference points,
the appropriate bufers, the status of stocks relative to the reference points, and appropriate measures to protect habitats. here is also increasing convergence around
the goal of maintaining populations of large, old spawners due to their disproportionately high contribution to the larval pool and their important ecological roles
(Caddy and seijo 2002).
he objective of most national and international isheries legal mandates is the
exploitation of populations to achieve sustainable social and economic beneits. in
the Us and some other countries, this is often translated as ishing to MsY (hilborn
and stokes 2010). achieving MsY generally means reducing target stocks to between
20% and 40% of their historical biomass—the level where net productivity or surplus
production is theoretically greatest (hilborn and walters 1992). as ishing drives a
stock down toward the biomass at which MsY is achieved, a number of its biological
characteristics change. For example, a higher total mortality rate shifts the age distribution toward younger, faster growing individuals with potentially negative efects
on future recruitment, and ecosystem-level processes. he aim is to make the stock
as productive as possible, which necessarily means a high turnover of individuals—
many recruits, and many deaths.
in contrast, marine conservation objectives are typically aimed at protecting biodiversity and minimizing extinction risk. institutionally, this is often translated as
preventing any rapid decline in populations, or changes in its biological characteristics. Consequently, whereas the reduction of a ish population to 20% or 40% of its
unished biomass with concomitant changes in age structure may be considered a
necessary and acceptable outcome by isheries scientists and managers, these may
be viewed as unacceptably adverse impacts by some marine conservation scientists
and practitioners. Moreover, overexploitation of stocks and severe declines beyond
target reference points are rife; the median decline of 230 exploited ish populations
was 83% (hutchings and reynolds 2004). reductions on this scale far exceed isheries target reference points and often breach the limit reference points that deine
the point beyond which reproductive output is impaired by the process known as
“depensation” in the isheries literature and “allee efect” in the ecological literature
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(hutchings and reynolds 2004). Until recently, such declines were of concern only to
stock assessors, but now are of concern to a wide array of marine conservationists,
who have in turn increased awareness of these declines among policy makers and
the general public. some of these declines are severe enough to merit concern on a
wider stage. For example, until recently, 90% of assessed european stocks were ished
beyond the limit reference points (Piet and rice 2004); 17% had declined suiciently
to be classiied as threatened under the world Conservation Union (iUCn) reference
points based on population decline (dulvy et al. 2005), although they would not be
classiied as threatened under the iUCn abundance and range extent benchmarks
(rice and Legace 2007). a more recent analysis of biomass trends for exploited marine ish stocks (hutchings et al. 2010) ofers some hope that declines may have leveled of since the 1990s.
even when isheries management is successful in maintaining ishing mortality
and biomass at what are thought to be sustainable levels, the focus on single species
often clashes with the biodiversity goals of marine conservationists. For example,
even prudent and precautionary isheries management has the potential to remove
suicient predator biomass to produce substantial shifts in ecosystem structure and
function (Zabel et al. 2003, salomon et al. 2008). subsistence ishing, for food only,
was suicient to remove more than half of the invertivore biomass on Fijian reefs.
his removal of predators unleashed outbreaks of coral-eating starish, Acanthaster
plancii (Linnaeus, 1758), resulting in repeated island-scale phase shifts from coral
to algal dominated reefs only at the most heavily ished islands (dulvy et al. 2004).
generally speaking, such ecological impacts of ishing receive little attention in isheries management.
difering interpretations of the meaning and signiicance of declines in biomass
arise from the fact that isheries management focuses on the rate of change of growth
and recruitment of single species—the higher the better because the stock is more
productive. in contrast, marine conservation focuses on rates of change in mature
populations or communities—with the goal of maintaining “natural” age or community structure and increasing resiliency in the system, thus hedging against collapse. hese contrasts in objectives and perceptions of status correspond to present
competing views on the state of the world’s isheries and appropriate policy prescriptions. if one generalizes that population declines are part and parcel of sustainable
ishery management, one is likely to view the state of isheries as a mixed bag with
many successes and some failures. Conversely, one is likely to view the state of isheries as in crisis if one generalizes that observed population declines are indicators
of extinction risk and loss of ecological function (Clark 1990, hutchings 2001). in
truth, some population declines are inevitable where ishing occurs, but some are associated with failure to meet management objectives or unsustainably high harvest
goals. similarly, not all declines are indicators of extinction risk or loss of ecological
function, but some are.
another way to frame the divide is to consider the primacy of objectives: isheries
scientists often operate within a context in which managers strive to balance conservation, social, and economic objectives such as optimizing yield from isheries (e.g.,
diCosimo et al. 2010). nevertheless, in practice, primacy is frequently given to social
and economic objectives over conservation objectives in order to alleviate or prevent
short-term economic and social impacts. Marine conservation scientists, however,
often frame analyses assuming conservation as the primary objective on the theory
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that social and economic beneits low from conservation, and eventually long-term
socio-economic beneits will arise. here is increasing awareness of the need to seek
win-wins where tradeofs between objectives are minimized. he discourse becomes
dysfunctional when there is a lack of appreciation for the diferent values and goals,
and a full and nuanced understanding of each side’s assumptions and accepted tools.
his dysfunction is ampliied when there is a lack of real human-to-human communication about these values and associated tools (e.g., when discourse occurs solely
through press releases or publications). when these diferences in goals, values, and
tools are understood, and the tendency to generalize is avoided, the dialogue between the disciplines has been extremely fruitful (e.g., worm et al. 2009).
addressing Uncertainty and variability
Fisheries management has long identiied the quantiication of production parameters and their uncertainty as a central goal and a key management component
(walters 1986). in fact, many isheries models estimate both process and observation error, and in the past decades have begun to consider uncertainty about future
states of nature and that associated with implementation—both important for making management decisions about next year’s (or next decade’s) ishery. at the same
time, qualitative aspects of species interactions and variability in key mechanisms is
often overlooked or averaged out by isheries scientists [e.g., natural mortality (M) is
often still assumed to be 0.2 or some other constant number and stock recruitment
relationships are treated as stationary]. to be fair, many such assumptions are made
out of necessity (i.e., lack of data), not because they are believed to be unimportant
or true. nevertheless, it is argued that more complex and realistic models are usually
diicult to parameterize, do not necessarily lead to more accurate outcomes, and
have less, not more, precisions in estimates (adkison 2009). he model agnosticism
and the appreciation of diversity and surprises that many marine conservationists
share may be of beneit to the isheries management culture.
Marine conservation practitioners often view the variability and uncertainty inherent in any scientiic assessment of a population as cause for precaution. his relects a value judgment: that it is better to err on the side of conserving stocks and
biodiversity. such a value judgment can afect the framing of scientiic analyses conducted by marine conservation scientists. in contrast, isheries scientists are working
within the context of ishery management where the concrete short-term adverse
impacts of reductions in ishing opportunity need to be balanced with uncertain and
less quantiiable conservation and economic beneits in the long-term. indeed this is
the crux of the matter—policies that create jobs and revenue today are pitted against
policies that would protect biodiversity and generate revenue and employment options in the future. while many ishery managers and scientists operate within a
legal context of precautionary action in the face of uncertainty, which has resulted
in precautionary cuts in allowable harvest and other measures, economic and social
concerns make such actions diicult in many isheries. a mutual appreciation of the
diferent values, legal mandates, and respective operating management contexts that
drive behavior and attitudes with respect to dealing with uncertainty and variability
would probably reduce conlict between the disciplines and communities. Conservation measures designed to minimize adverse social and economic impacts, and/or to
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solve implementation problems (for example, with collaborative planning processes,
inancing transition costs, risk pooling, etc.) would also help.
he disciplinary divide may be further magniied by the diferent needs of smallscale vs industrial isheries and the experiences of scientists and practitioners working in these vastly diferent environments. indeed, the efectiveness of isheries
management and conservation tools will vary as a function of economic, social, and
ecological context. For example, what may be efective for industrial isheries in the
developed world, where isheries target few species and data necessary for stock assessments tend to be available, may be irrelevant for isheries in the developing world
that tend to be multi-species and data-deicient.
Bridging the divide
Fortunately, traditional barriers to communication between marine conservation and isheries scientists are beginning to break down and interdisciplinary collaborations between them, and with social scientists and economists, are emerging
(hughes et al. 2005). his trend is driven, in part, by an increasing awareness of the
magnitude and accelerating rate by which humans are altering the functioning of
marine ecosystems and awareness that many past eforts to halt, and where necessary reverse, these alterations are either inefective or working too slowly. Ultimately,
understanding the ecological, social, and economic performance of both isheries
and conservation initiatives requires an improved understanding of linked socialecological systems (Fig. 2; Mcevoy 1986, 1996, Francis et al. 2007). his awareness
has led to increasing acceptance of novel approaches to marine conservation and
management (e.g., catch shares, private buyouts, isheries funds to inance transition
costs), increasing acknowledgment of ecosystem approaches to management in the
mandates of governmental and intergovernmental agencies, and the growing role of
international conservation conventions like the Convention on Biodiversity (CBd)
and the Convention on international trade in endangered species (Cites) in solving marine conservation issues (doukakis et al. 2009).
ecosystem-Based Management
he shift toward an ecosystem approach to ishery management (Pikitch et al.
2004) has increased the applicability of ecological knowledge to the isheries and
marine resource management process. in particular, an understanding of predatorprey interactions and the transfer of energy between trophic levels has taken on new
importance in isheries science. hese insights are resulting in improved accounting
for variations in recruitment, e.g., by factoring in natural predation and cannibalism, and the need to reserve prey for dependent predators, e.g., managing isheries
on capelin and euphausiids to support predators like squid, ish, birds, seals, and
baleen whales. Moreover, increased sensitivity to the social and economic impacts
of conservation measures on isheries and other marine resource sectors within the
marine conservation community has led to eforts to minimize adverse impacts
(e.g., through the use of optimization processes to design small MPas that nevertheless meet conservation objectives, catch shares to achieve greater proitability, etc.).
while many challenges remain, such as the application of management and conservation measures at appropriate scales (e.g., scaling up protections to account for
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Figure 2. An improved understanding of coupled social-ecological system dynamics will yield
more effective isheries and marine conservation decisions (McEvoy 1986, 1996, Francis et al.
2007). EBM = ecosystem-based management, MPA = marine protected area.
migrations and large ecosystem processes, and scaling down isheries management
measures to account for local variations in species life history and ishing practices),
progress toward bridging the divide is being made.
Case studies
Arctic Fishery Management Plan.—he north Paciic Fishery Management Council, which develops management advice for the Us national Marine Fisheries service
for Us isheries in federal waters of alaska, recently developed an ecosystem-based
ishery management plan for Us arctic waters that is seen as a win-win for conservation and isheries (wilson and ormseth 2009). he plan anticipates future isheries
emerging as a result of climate change, and identiies potential target species, including arctic cod, Boreogadus saida Lepechin, 1774, which is the most abundant ish
in the Us arctic and commercially important in other regions. however, the plan
also identiied arctic cod as critically important forage for marine mammals and
seabirds in the ecosystem. Based on this inding, as well as the current expense of
operating commercial isheries in these distant waters and uncertainties regarding
ecosystem productivity and dynamics, the plan efectively closes Us arctic waters to
commercial ishing, but outlines conditions under which ishing would be allowed in
the future. hese conditions include suicient data and analysis to ensure that isheries will not harm the ecosystem and can be conducted sustainably. an exception is
the transition of existing subsistence isheries to commercial isheries; the plan puts
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in place a process for scoping and managing such isheries if they arise. he Council
explicitly recognized ecological, economic, and social axes of sustainability:
“his management policy recognizes the need to balance competing uses
of marine resources and diferent social and economic goals for sustainable
ishery management, including protection of the long-term health of the
ecosystem and the optimization of yield from its ish resources. his policy
recognizes the complex interactions among ecosystem components, and
seeks to protect important species utilized by other ecosystem component
species, potential target species, other organisms such as marine mammals
and birds, and local residents and communities.”
(north Paciic Fishery Management Council 2009)
we note that almost no other Us ishery management plans have preemptively
closed potentially valuable isheries in response to ecological considerations. his
is an example of ecosystem-based ishery management which can prevent diiculties balancing the conservation of fragile ecosystems with initially unplanned and
unregulated ishing.
Kenyan Coastal Community Management.—he Kenyan government had two
main objectives in management of coastal resources shortly after independence
in 1963: (1) increase tourism and (2) develop ishery resources for food and export.
hese economic objectives lead to the establishment of a series of four isheries closures (10–25 km2) that covered ~7% of the nearshore and a policy of largely unrestricted access to isheries resources in the remaining areas (wells et al. 2007). he
result was a strongly dichotomized social-ecological system where a few protected
areas maintained largely undisturbed ecosystems for tourism while heavy ishing
was undertaken in most of the remaining shallow ecosystems. Fishing efort ranged
from 4 to 16 ishers km−2 and small-meshed seine nets were most frequently used,
capturing the few ish species that could maintain production under the heavy exploitation (McClanahan et al. 2008). Catches in these isheries were seldom more
than 2–3 kg per person per day and incomes less than a few dollars per day. his
created a strong sense of ecological and economic disparity between the isheries
and tourism-dependent communities, as well as large diferences in reef ecology and
biodiversity in these two systems. government eforts to increase the areas in isheries closures were meet with hard opposition from ishing communities who were
concerned about loss of access and further economic marginalization.
Management actions to control isheries efort were largely unsuccessful and large
closures of > 5 km2 were becoming increasingly diicult to establish (McClanahan
2007). gear restrictions were implemented in some areas, but not others, dependent
on local support for government regulations. declining inances and ability of the
government to control local ishers and their ishing behaviors led to the recognition that progress could not be made unless ishers took a larger role in their own
management. his lead to legislation that created what are now commonly called
Beach Management Units (BMUs). BMUs allow for local bylaws and management
of local resources by BMU committees composed of ishers and other stakeholders
who propose regulations to the director of Fisheries. he implementation of this local management system is new and untested, but it is leading to greater recognition
of the need for local responsibility and planning of isheries and coastal economic
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development. one of the irst achievements of this BMU process was the local planning and implementation of small community closures, called Tengefu, which means
“set aside” in swahili. Communities plan to use these tengefu to attract tourism to
their reefs and also create refuge for the key isheries species. he concept and implementation is only partially being evaluated, but it is anticipated that the tengefu will
reduce the strong dichotomy in management and create some intermediate system
that may potentially beneit the ecosystems and communities that are not being protected by the few larger isheries closures.
European Union’s Ecosystem Approach to Fisheries Policy.—he declining productivity of european waters coupled with leet building in the early 1970s set the
stage for widespread overexploitation of many species, including the near regional
extinction of formerly abundant elasmobranchs, such as the common skate and the
angel shark (Brander 1981, walker 1998, dulvy 2000). he hopelessness of managing
ish stocks around the knife edge of limit reference points, increasing concerns for
weaker, less productive species such as skates and other elasmobranchs, and a decline in the inluence of stock assessments led to radical change in european isheries
science and management. stock assessors, even into the new millennium, were increasingly despondent at the challenges from industry regarding the quality of stock
assessments. he challenges were frustratingly valid, because it was widely known
that stock assessments weakened year-on-year as they overlooked an ever increasing
proportion of illegal and unreported landings—up to 40% of the landings of cod and
saithe were illegal in the late 1990s (Clover 2006). stock assessors and isheries managers, instead of being afraid of conservationists, were desperate for a new paradigm
that has subsequently been illed by the development of an ecosystem approach to
isheries management.
at that time, the upcoming cadre of senior european isheries scientists had come
from more ecological or conservation related disciplines than their predecessors,
ranging from plant ecology to bird community ecology to coral reef ecology. Many
more had lived through attempts to bring food-web realism to isheries through the
development of multispecies stock assessment models—an eU-wide scientiic endeavor that reached a pinnacle with the 1991 “Year of the stomach” survey of ish
diets (rice et al. 1991, hollowed et al. 2000). notably, an inluential number of senior scientists have now moved from a niche-based view of shelfseas ecosystems to
a size-based perspective (Bianchi et al. 2000, Jennings and Blanchard 2004, Pope et
al. 2006)
although the modern era of eU isheries management could be considered to be
dominated by indicators after a decade of efort and the discovery of several thousand
potential metrics (rice 2003), there has been a stark realization that indicators alone
do not constitute an ecosystem approach. indicators have to be “it-for-purpose” and
need to be selected to report on ecological objectives (rice and rochet 2005). he
more recent focus has been on determining what it-for-purpose means, and understanding of what objectives are reasonable (rogers et al. 2007). his has lead to
the articulation of vision statements (what society actually desires of our oceans),
leading to clear policy statements such as the UK vision for “safe, clean, healthy,
productive, biologically diverse oceans,” for example. his vision encompasses water quality, harmful algal blooms, shellish diseases, food security, biodiversity, and
climate change. in reductionist scientiic terms, this vision might seem vague and
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contradictory, but such vision statements provide valuable guidance for the formulation of speciic objectives, appropriate indicators, and reference points given the
constraints of available monitoring data. Critically, such visions explicitly recognize
the inevitable trade-ofs that need to be made.
he ongoing challenge is to develop spatial management and complementary
measures to realize all elements of the vision, while recognizing and attempting to
minimize trade-ofs among them. with respect to spatial management, this might
mean that in some areas an active decision is made to forgo the “biologically diverse” aspiration and allow high ishing pressures to meet the “productive” element
of such a vision; and in others to forego “production” and eliminate benthic trawling
on biologically diverse areas such as coldwater coral reefs or other biogenic habitats. it is unlikely that we can achieve all ecological quality elements in each spatial
management unit, but conceivably, a spatial management portfolio exists that allows
us to maximize parts of the societal vision across the full portfolio of spatial units.
with respect to other measures, addressing tradeofs may mean creating new kinds
of ishing privileges (e.g., catch shares) and institutions (e.g., common pool resource
co-management entities). Meeting these challenges in order to operationalize the
ecosystem approach to isheries management will require many diferent disciplines.
Marine Protected areas
Marine conservation scientists and practitioners have often supported the notion
of permanent spatial closures, i.e., marine reserves to protect population and community dynamics and biodiversity. hose advocating the use of marine reserves have
also explicitly recognized the need to manage isheries sustainably in the rest of the
ocean, recommending spatial protection as only part of an overall isheries management scheme (i.e., as an insurance mechanism against inevitable management uncertainties or natural catastrophes; i.e., allison et al. 1998, Pauly et al. 2002). he risk
aversion characteristic of this community results in a preference for management
tools and science that fully supports a precautionary approach and facilitates the
preservation of at least some part of an area’s habitat and associated communities.
Marine protected areas ofer an avenue to bridge the quantitative and methodological diferences between disciplines. Marine ecology, an essential element of marine
conservation science, has traditionally emphasized a mechanistic understanding of
marine community dynamics (key ecological processes such as competition and predation) via experimental manipulations. his approach was limited to small spatial
and temporal scales owing primarily to the logistical constraints of experimentation
and replication. information gathered at small scales can result in relatively strong
inference due to the use of controls, but is diicult to scale up to the much larger
scales at which many isheries operate. Fisheries science depends heavily on long
time series of data and parameterization of population models designed to describe
phenomena over very large spatial and temporal scales while experimental manipulations are rare. Furthermore, isheries stock assessments are not usually spatially
explicit, and hence have a hard time incorporating closed areas or MPas (except
by adjusting ishing mortality or abundance estimates for the whole stock assessment region). nonetheless, examples of convergence exist; marine reserves can be
treated as large-scale management and policy experiments (depending on how the
reserves have been selected, established, and managed) and can be evaluated based
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on their ability to achieve both biodiversity and isheries objectives via adult and
larval spill over. hey are also potential controls for ishing experiments and can
therefore satisfy the technical needs of adaptive isheries management programs, as
well as provide data for harvest control rules (Babcock and MacCall 2011, Mcgilliard
et al. 2011). Moreover, isheries management measures are now being assessed using
Management strategy evaluation (e.g., Mapstone et al. 2008) and Before-after Control impact (BaCi)–like approaches (e.g., essington 2010) in order to draw stronger
inferences about their performance.
historically, rigorous consideration of social science concepts or tools (e.g., governance, institutional analysis, the nature of ishing rights, occupational multiplicity,
economic valuation of ecosystem services, social capital, and proitability) by either
discipline was rare (but see Fujita et al. 1997). however, this is rapidly changing
(McClanahan et al. 2009a,b, Fujita et al. 2010). Marine conservation and isheries
management could beneit from insights from social science related to the design
of management measures that are aligned with social and economic incentives, and
that minimize adverse social and economic impacts or even produce net increases in
welfare. arguably, understanding the efects of policies on human behavior is just as
important as understanding the distribution and abundance of ish populations, as it
is one of the only variables that management can afect.
Many eforts are underway to bridge the quantitative divide between isheries management and marine conservation. Convergence can be seen in the increasing use of
meta-analysis by conservation scientists to overcome scale issues (Mosquera et al.
2000, Lester et al. 2009), and in the increasing interest among isheries scientists in
regional and local scale assessments and management (Prince 2005). Meta-analyses
of low- or no-replication management measures, such as marine reserves, have been
used by conservation biologists to derive general principles and to investigate the
performance of these management measures. Meta-analysis will provide a powerful way to increase the scale and relevance of management for both conservation
and resource use and is a useful tool for both disciplines where space and research
efort are often constraining the development of robust general principles. stock assessment models can now incorporate sub-regional information about growth rates,
mixing, and ishing efort.
Case studies
Ecosystem Approach to MPAs in Indonesia.—Located of the coast of west Papua
in eastern indonesia, the Birds head seascape (Bhs) is the center of the Coral triangle, the most biodiverse marine region in the world (veron et al. 2009). a system of MPas has been established to protect this incredible biodiversity. a wide
range of monitoring, education, and outreach activities has made the MPa network
an accepted tool on the ground to achieve conservation in Bhs while maintaining
the livelihoods of local people. Participatory processes were key, as were insights
into social structure (e.g., the existence of traditional marine tenure systems and the
avoidance of areas of active conlict for MPa implementation). MPas in this area
are tools for both ecosystem conservation and sustainable isheries. he area is also
increasingly becoming the target for development of a wide variety of economic sectors (e.g., isheries, energy extraction, and tourism). as a result, local governments
in this region are facing diicult decisions in their attempt to balance sustainable
development of an incredibly rich array of marine resources with conservation of
globally signiicant marine diversity. he growing range of diverse objectives within
SALOMON ET AL.: BRIdgINg ThE dIVIdE
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the seascape, as well as the obvious existing ecological, governance, and human connections, have made the adoption of an ecosystem-based approach to management
an increasing priority and focus for the Bhs. as a result, conservation and isheries
objectives are addressed side by side by the practitioners working in this area.
he nature Conservancy (tnC), Conservation international (Ci), and world wide
Fund for nature (wwF) have been working in partnership with local stakeholders
to explore and describe the ecological, socioeconomic, and governmental processes
that are most important to understand and include in management decisions in the
Bhs. Based on the results of these studies, tnC, Ci, and wwF are in the process
of assisting local and provincial governments to develop environmentally sound development policies able to address multiple objectives (including conservation). effectively demonstrating the links between eBM and MPas, and leveraging existing
buy-in on the ground for MPas to address use issues both within, as well as outside
of the MPas, will clearly be a powerful avenue for the adoption of eBM in the Bhs
(agostini 2009).
Density Ratio Approach Based on Marine Reserves.—Many small-scale, nearshore
isheries lack historical abundance and catch data, which are needed to parameterize conventional isheries stock assessment models. however, ecological monitoring
from in and around marine reserves can also inform the historical impact of ishing
on ish populations. Mcgilliard et al. (2011) and Babcock and MacCall (2011) have
proposed using the ratio of the measured density of ish outside a no-take marine
reserve to that inside a reserve each year (the density ratio) as the input to a control
rule which managers could use to specify the appropriate direction and magnitude of
change in ishing efort or catches in the next year. a lower density ratio would trigger a reduction in the allowable ishing efort or mortality, which would allow biomass to recover in the ished area, thus increasing the density ratio. he density ratio
can be calculated from marine reserve monitoring data, and the allowable change in
ishing efort (or catch) is calculated relative to the current efort (or catch) so that
no historical data are required. wilson et al. (2010) apply a similar approach within
a decision tree framework to facilitate the use of additional data on size structure to
reine allowable yield estimates.
according to simulation studies based on California rockish species (Mcgilliard
et al. 2011, Babcock and MacCall 2011), in the long term, the density ratio control
rules performed well by increasing total biomass and maintaining yield for all species
and several scenarios about leet distribution and ish biology, provided that migration of adult ishes across the reserve boundary was minimal. advantages of using
density ratio control rules are that no historical catches or stock assessments are required, the control rules are driven by monitoring data (requiring fewer assumptions
and parameters), and they allow the management system to respond appropriately to
environmental luctuation. in addition, density ratio control rules can be applied at
more local spatial scales than is common for stock assessment-based control rules.
density ratio control rules are only efective for species that tend to accumulate density in marine reserves, and the method would be most efective for reserves that
have been established long enough for ish density to build up in reserves.
he density ratio control rule was developed through a collaborative process that
included marine ecologists, isheries scientists, social scientists, and ishermen. it remains to be seen whether this methodology will work well in practice, but the larger
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point is that there is a need for “outside the box” ideas for how to achieve ishery
management and conservation objectives given the data that are available or can be
acquired.
Catch shares
Fisheries management and marine conservation both face the challenge of managing common property resources. he primary goals of ishery management are to
provide ishing opportunities, generate revenue and livelihoods, and maintain sustainable levels of ishing mortality and spawning stock biomass. he marine conservation community has tended to focus on the goals of conserving ish biomass,
diversity, and ecosystem integrity over relatively long time horizons. Conventional
approaches to isheries management and conservation tend to create conlict among
these goals, due to the incentives created by common measures, such as input or
efort controls (e.g., gear restrictions, restrictions on vessel length and horsepower,
seasons, etc.) and output controls (e.g., total allowable catch limits).
in the absence of strong collective action institutions, such as ishery cooperatives
or ishing rights regimes (also termed catch shares where individuals or groups of
individuals are allocated a percentage of the total allowable catch), individual ishermen face incentives to overexploit ish populations. individuals who are not embedded within a well designed and functional collective resource management system,
whether based on cooperation or on market forces, tend to compete with others to
maximize share of the catch since individuals do not have secure shares or incentives to cooperate with the goals of maximizing values, minimizing ishing costs, and
minimizing incidental catch and habitat damage. Under these incentives, overcapitalization, destructive ishing, and the use of gear that can catch very large volumes
of ishes (often indiscriminantly, leading to enormous amounts of waste) become
rational, even though these behaviors result in unsustainable ishing.
imposition of input/efort controls aimed at controlling ishing mortality by limiting ishing power in the context of this common pool resource problem (i.e., in the
absence of collective action institutions or catch shares) tends to increase ishing
costs and create a “cat-and-mouse” game between regulators and ishermen, in which
ishermen face strong incentives to innovate solutions that get around regulations in
order to maximize catch. imposition of output controls like total allowable ishing
levels tends to exacerbate this race for ishes (more vessels, larger gear, more rapid
ishing), increase ishing costs, and reduce value (by glutting markets). hus, these
types of conservation and management measures create economic distress and are
not aligned with strong social and economic incentives. discount rates are very high,
since ishes only have value when caught and individual ishermen can never be sure
what their share of the catch will be. it is not surprising, then, that in this context additional conservation measures such as MPas intended to protect whole ecosystems
and biodiversity, perceived as investments in long-term sustainability by marine conservation community, are perceived as threats to livelihoods by many ishermen and
ishery managers.
Management approaches based on dedicated access privileges (or catch shares),
such as individual transferable Quotas (itQs), territorial Use rights for Fishing
(tUrFs), or community development quotas (CdQs) are designed to help solve
the common pool resource problem by creating incentives that encourage behavior
SALOMON ET AL.: BRIdgINg ThE dIVIdE
265
consistent with conservation. Consequently, they ofer a way to align isheries management and marine conservation, that can minimize the tradeof between strong
conservation and good economic and social performance in isheries. he transformation in the governance of Chile’s coastal marine resources via isher collectives
that co-manage tUrFs, locally known as “caletas” (gelcich et al. 2010), provides
compelling evidence of the beneits of these approaches. Furthermore, experience
with collective action institutions (ostrom 1990, 1999), a meta-analysis of over 200
catch shares systems (Costello et al. 2008), and a recent synthesis of literature and
expert opinion on catch share design (Bonzon et al. 2010) suggest that good institutional design, strong governance, the re-alignment of incentives, and increased
accountability can enable isheries to overcome the problems that plague many isheries (overishing, high bycatch rates, and habitat impacts). Yet, catch shares have
their ecological and social limitations (Pinkerton and edwards 2009, essington 2010,
gelcich et al. 2010, Pinkerton and edwards 2010, sumaila 2010, turris 2010) and
thus remain controversial.
although designed to promote economically eicient exploitation and ecological
stewardship among ishers over the long-term, catch shares do not always address
the negative impacts of ishing on marine ecosystems (Branch 2008, essington 2010)
and can impede equity and social justice in resource use (Pinkerton and edwards
2009). hus, to meet ecological, economic, and social sustainability, the trifecta of
modern isheries management, some observers maintain that catch shares need to
be designed as part of an integrated ecosystem-based management plan (sumaila
2010), one that addresses the dynamics of linked social-ecological systems (Fig. 2).
others argue that catch share systems can be designed to achieve this trifecta better
than other management policies alone, if appropriate measures (e.g., robust catch
limits, MPas, transition inancing, equitable allocation formulae, community quotas, etc.) are included and implemented well (Bonzon et al. 2010). Consequently, we
see the improved design and implementation of catch shares as an area that is ripe for
bridging the divide between conservation, isheries and social scientists, economists,
resource managers, and resource users.
Case study
Private Trawl Permit Buyback in California.—a 2001 lawsuit by conservation
groups provided impetus for the Paciic Fishery Management Council and noaa to
implement the essential Fish habitat mandate of the Us sustainable Fisheries act of
1996. he marine conservation community was calling for the creation of large notrawl zones; ishermen were generally opposed. in 2005, he nature Conservancy
(tnC) and the environmental defense Fund (edF) initiated a private buyout of trawl
vessels and permits conditioned on the establishment of no-trawl zones collaboratively designed with ishermen to optimize conservation gains and minimize impacts
on ishermen and ishing communities. as a result, trawl efort based in Morro Bay,
California, was reduced from six vessels to one, the F/v south Bay, and three notrawl zones totaling 3.8 million acres of diverse habitat were established by noaa.
subsequently, a community-based ishing association (CBFa) was created, consisting of these two ngos, two commercial isherman’s associations, two harbormasters, and the California department of Fish and game. his CBFa successfully
applied for an exempted Fishing Permit (eFP) to allow tnC to lease the trawl permits it had acquired to ishermen willing to use hook and line or trap gear only. tnC
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also completed an innovative Conservation Fishing agreement with a trawl ishermen who agreed to comply with stringent spatial and gear restrictions in order to
target groundish (e.g., latish) that could not be captured with hook and line or trap
gear. hese arrangements amounted to a hybrid catch share–collective action ishery; the eFP includes caps on multiple species aimed at ensuring sustainable harvest
and bycatch rates (essentially, a catch share allocation to a community). a collective
action institution (the CBFa) was developed to implement the eFP ishery by sharing
information and creating economic and social incentives aimed at maximizing the
value of the entire portfolio of isheries included within the eFP.
nested within a ishery with high bycatch and discard rates that constrained ishing opportunity, the CBFa’s ishery resulted in 100% compliance with hard catch
limits and near-zero bycatch in the past two ishing seasons. data from ishermen
and observers low into an electronic database, know as “eCatch”, which is used to
inform in-season adjustments in order to avoid bycatch and extend ishing opportunity by reducing mortality rates on species for which landings are approaching hard
caps. tnC is testing the use of a video-based electronic monitoring recording system
developed by archipelago Marine research Ltd. to determine whether it is a feasible
alternative to 100% human based observer coverage for ixed gear vessels ishing in
the eFP.
Project partners are developing niche markets and new distribution channels for
local, fresh ish to generate higher values in order to ofset economic losses resulting
from the trawl buyout. Business planning support and low-interest loans from the
California Fisheries Fund (developed by edF, California’s ocean Protection Council,
and private funders) are being employed to support these activities. his project has
resulted in signiicant conservation gains and shows promise for the creation of a
new, higher value, lower impact ishery to replace a trawl ishery. however, the project also resulted in substantial economic and social impacts. information on these
impacts is still preliminary, but early results suggest that the project is on a trajectory
toward ameliorating them. initial transition payments from tnC helped to alleviate
the immediate economic distress associated with the reduction of trawling. value
per pound increased from $0.81 in 1990 to $1.69 in 2009 (wise 2010). since the Central Coast groundish Project ishery, which includes both the trawl Conservation
Fishing agreement and the eFP, started in late 2007, 1.51 million pounds of ish have
been landed, resulting in ex-vessel revenues of $2.34 million.
eco-Certification
eco-certiication of isheries products as coming from sustainable isheries ofers
another opportunity for bridging the gap between the isheries management and
marine conservation communities. eco-certiication is well established for some resource-based industries, such as forestry, agriculture (hatanaka et al. 2005), and biofuels (Lewandowski and Faaij 2006). here are many controversial issues associated
with using economic instruments in isheries management (rice 2007), but a thorough review of the potential strengths, weaknesses, and complicating factors with
regard to certiication (Fao 2001, 2005) concluded that use of market tools including eco-certiication may be a constructive factor in increasing the sustainability of
isheries, if they are properly designed and implemented. his means that there have
to be clear and explicit standards for certiication assessments that must be sound
SALOMON ET AL.: BRIdgINg ThE dIVIdE
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and objective, use best available information, take full account of uncertainties, and
be conducted by credible assessors that are held accountable.
it is in these evidence-based assessments and their review that the two communities must come together. he language of the Marine stewardship Council (MsC,
probably the most widely recognized isheries certiication body) scoring Criteria and assessment guidelines is the language of isheries science: limit reference
points, target reference points, harvest control rules, etc. however, the concepts to
which those standards are applied include not just seven criteria about the status
and exploitation of the target species assessed under Principle 1, but also 15 criteria
regarding the ecosystem efects of the ishery (Principle 2), and nine criteria related
to the governance of the ishery (Principle 3). Under Principle 2, a ishery must have
demonstrated to be sustainable with regard to its impact on all bycatch species, all
habitat impacts, trophodynamic consequences, and species given special protection
under, for example, endangered species legislation. Language in the scoring guidelines for passing scores on sustainability closely relects the language of sustainability and precaution in agenda 21 of the rio declaration, the basis for much of the
progress in conservation science during the last 20 yrs. a ishery cannot receive a
score below 60% on any single criterion under any of the Principles, and must have
at least an average of 80% for all the criteria under each of the three principles. existing ish stock assessments are often the basis for scoring against the P1 criteria,
but for P2 and P3, the certiication assessment process requires analyses rarely done
for isheries managers (rice 2010). in the work to prepare analyses and reviews for
evaluations of P2 and some aspects of P3, and in the sequence of opportunities for
review and engagement of experts and stakeholders throughout the MsC assessment
process, there are many opportunities for collaborative work of experts from the two
disciplines, and a meeting of minds over evaluating ecosystem factors familiar to
conservation scientists in a framework familiar to isheries scientists.
Certainly, when research used to certify seafood comes from the industry itself,
conlicts of interest (i.e., industry-funded labels) can arise quickly. hus, a key
challenge for eco-certiication is to ensure that it has high integrity and is a force
for sustainability and thus free from the conlicts of interest that plague it now
(Jacquet et al. 2010). eco-labeling can help break the tyranny of the market chain that
constrains prices and drives a race to ish, or it can become another method of brand
diferentiation to sustain further supermarket sales. his latter process may well aid
security of supply over larger spatial scales, but it remains an open question as to
its net beneit for the viability of ishing communities and exploited ecosystems. of
course the costs of acquiring eco-labeling sets small developed and developing world
isheries at a distinct disadvantage compared to industrialized capital-intensive
isheries (Jacquet et al. 2010) unless grants or loans are made available to address
this inequity.
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General Recommendations to Bridge the Disciplinary Divide
In order to bridge the isheries-conservation science disciplinary divide, improve the scientiic basis of marine resource management, and ultimately facilitate sustainable use of
marine resources and the protection of marine ecosystems, we make the following recommendations:
Objectives
1.
2.
3.
4.
Clarify values and objectives of agencies, NGOs, stakeholder groups, and indigenous
peoples at the outset of decision-making processes so that scientiic analyses are
framed and interpreted appropriately.
Tailor the quantitative, qualitative, and policy tools that address both isheries and
conservation objectives to the ecological, economic, and governance structure where
they are applied.
Implement measurable performance standards that relect speciic social values; such
standards are necessary for meeting biodiversity and conservation objectives. Prescriptions without clear performance indicators often introduce incentives to game
the regulatory system. Shifting the discourse to objective measures of progress and
their stated values can help defuse polarized ideological arguments by focusing on
the pragmatic and objective measures.
The best available science and data need to be available to managers and practitioners
to deine objectives and measure progress in the future. This requires open access
to data to facilitate transparency. The availability of isheries data and accessibility
of the stock assessment process must increase outside of the isheries science community.
Tools
1.
2.
3.
4.
Apply tools that measure trade-offs among the full suite of objectives and make these
trade-offs clear in the analyses and methodology.
Apply tools and policy measures that minimize or eliminate trade-offs. For example,
align institutional and economic incentives with indicators of performance and sustainability for economic, ecological, and social objectives.
Develop tools that allow inclusion or explicit consideration of the multiple and differing scales over which dynamics of isheries, ecology, and human dimensions occur
(Fujita et al. 2010) .
When evaluating biodiversity and conservation objectives, determine the outcome
of a variety of social and economic objectives that are achievable over short and
medium time frames. Design tools that convert future value of conservation into
net present value for ishermen and ishery managers (e.g., catch shares, loans, new
markets for ecosystem services).
Practice
1.
Converge on “one window” for science advice for all agencies with overlapping mandates so the isheries agencies, species-at-risk agencies, the ecosystem integrated
planners, and the MPA managers all get the same advice from the same group of
experts. That group of experts should include the full spectrum of types of expertise
and perspectives, and may be producing a variety of products tailored for management and policy bodies with different duties.
SALOMON ET AL.: BRIdgINg ThE dIVIdE
2.
3.
4.
269
Both isheries and marine conservation scientists need to interface more regularly
with social scientists, isheries managers, conservation practitioners, policy makers,
and ishermen to recognize the profound importance of understanding ishermen/
leet/institution behavior. For example, experienced ishers can be helpful in identifying important research questions and designing alternative exploitation practices.
Develop governance and inancial systems that create incentives for ishermen to
engage in conservation and stewardship. These tools include dedicated access
privileges (catch shares), loans, permit and quota banks, and cooperative structures
(Ostrom 1990).
Employ trade-off analysis and stakeholder processes to explicitly identify and assess
ecosystem service and biodiversity trade-offs in order to ind optimal solutions outside of the “normal” solution space that is constrained by unclear values, goals, and
relationships among ecosystem services.
Communication
1.
2.
3.
Identify, evaluate, and communicate shared values. Communication focused on understanding people’s interests and points of view rather than focusing discourse on
their positions.
Increase the variety of technical input represented in formal isheries management
decision-making. Increase power sharing in the ishery management process to include diverse stakeholder groups and conservation non-governmental orginizations
that fully engage within the decision making process.
Clearly articulate the social, environmental, and isheries consequences of policy
options for all sectors affected by potential management actions (isheries, conservation, marine transportation, energy, coastal zone development, etc.). Quantify societal preferences for the delivery of different combinations of ecosystem services,
and provide decision makers with information about how various stakeholders might
weigh trade-offs based on their preferences and values.
Conclusion
with the growing awareness that marine conservation and resource use problems
are by nature interdisciplinary (Fig. 2), researchers from traditionally disparate disciplines have begun working together to better understand and solve them. Bridging the disciplinary divide between isheries and marine conservation science and
achieving multiple objectives will require lively dialogue and a diversity of expertise.
to that end, we have attempted to illustrate the major features of the disciplinary divide and to provide guidance and examples of how isheries and marine conservation
science can come together to create a better scientiic basis for decision making and
generate solutions that can improve human welfare while protecting and restoring
marine biodiversity and marine ecosystems.
acknowledgments
we thank K Brander, L Fritz, C Faunce, and two anonymous reviewers whose insights
vastly improved this manuscript. he authors gratefully acknowledges the many partners who
have worked diligently to make the Central Coast groundish Project a success, including C
Cook, r Fujita, M Bell, e Feller, M gleason, s reinecke, M spring, K Bonzon, P higgins, M
delapa, r algert, J elder, s Mcgrath, C Kubiak, J o’Brien, M vojkavich, B Blue, r Cullen, d
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rose, r hawkins, g Bettencourt, J Pepper, h Pontarelli, and d oberhof. aKs and oJ were
supported in part by a david h smith Conservation research Fellowship. aKs also thanks
the hakai research network and nserC, and eaB thanks Commonweal. he indings and
conclusions in this paper are those of the authors and do not necessarily represent the views
of the national Marine Fisheries service.
Literature Cited
adkison Md. 2009. drawbacks of complex models in frequentist and Bayesian approaches
to natural-resource management. ecol appl. 19:198–205. PMid:19323183. doi:10.1890/071641.1
agostini vn. 2009. ecosystem-based management and marine protected areas: coming together in working seascapes. Mar ecosyst Manage. 2:6.
allison gw, Lubchenco J, Carr Mh. 1998. Marine reserves are necessary but not suicient for
marine conservation. ecol appl. 8:s79–s92.
Babcock ea, MacCall ad. 2011. how useful is the ratio of ish density outside versus inside
no-take marine reserves as a metric for ishery management control rules? Can J Fish aquat
sci. 68:343–359. doi:10.1139/F10-146
Bianchi g, gislason h, graham K, hill L, Jin X, Koranteng K, Manickchand-heileman s, Payá
i, sainsbury K, sanchez F, et al. 2000. impact of ishing on size composition and diversity of
demersal ish communities. iCes J Mar sci. 57:558–571.
Bonzon K, Mcilwain K, strauss CK, van Leuvan t. 2010. Catch share design manual: a guide
for managers and ishermen. environmental defense Fund.
Branch t. 2008. how do individual transferable quotas afect marine ecosystems? Fish Fish.
9:1–19.
Brander K. 1981. disappearance of Common skate Raia batis from irish sea. nature. 290:48–
49. doi:10.1038/290048a0
Brander K. 2010. reconciling biodiversity conservation and marine capture isheries production. Curr opin environ sustainability. 2:416–421. doi:10.1016/j.cosust.2010.09.003
Caddy JF, Mahon r. 1995. reference points for isheries management. Food and agriculture
organisation, rome.
Caddy JF, seijo JC. 2002. reproductive contributions foregone with harvesting: a conceptual
framework. Fish res. 59:17–30. doi:10.1016/s0165-7836(02)00011-5
Clark Cw. 1990. Mathematical bioeconomics: the optimal management of renewable
resources. J wiley & sons, new York.
Clover C. 2006. he end of the line: how overishing is changing the world and what we eat.
University of California Press, Berkeley and Los angeles.
Costello C, gaines sd, Lynham J. 2008. Can catch shares prevent isheries collapse? science.
321:1678–1681. PMid:18801999. doi:10.1126/science.1159478
diCosimo J, Methot rd, ormseth oa. 2010. Use of annual catch limits to avoid stock depletion in the Bering sea and aleutian islands management area (northeast Paciic). iCes J
Mar sci. 67:1861–1865. doi:10.1093/icesjms/fsq060
doukakis P, Parsons eCM, Burns wCg, salomon aK, hines e, Cigliano Ja. 2009. gaining traction: retreading the wheels of marine conservation. Conserv Biol. 23:841–846.
PMid:19627316. doi:10.1111/j.1523-1739.2009.01281.x
dulvy nK, Freckleton rP, Plunin nvC. 2004. Coral reef cascades and the indirect efects of predator removal by exploitation. ecol Lett. 7:410–416. doi:10.1111/j.1461-0248.2004.00593.x
dulvy nK, Jennings s, goodwin nB, grant a, reynolds Jd. 2005. Comparison of threat and
exploitation status in north-east atlantic marine populations. J appl ecol. 42:883–891.
doi:10.1111/j.1365-2664.2005.01063.x
dulvy nK, Metcalfe Jd, glanville J, Pawson Mg, reynolds Jd. 2000. Fishery stability, local extinctions and shifts in community structure in skates. Conserv Biol. 14:283–293.
doi:10.1046/j.1523-1739.2000.98540.x
SALOMON ET AL.: BRIdgINg ThE dIVIdE
271
essington te. 2010. ecological indicators display reduced variation in north american catch
share isheries. Proc natl acad sci Usa. 107:754–759. PMid:20080747. PMCid:2818897.
doi:10.1073/pnas.0907252107
Fao. 2001. Product certiication and eco-labeling for isheries sustainability. rome.
Fao. 2005. report of the technical consultation on international guidelines for the ecolabelling
of ish and ishery products from marine capture isheries. 19–22 october, 2004. rome.
Fisheries act. 1985. Minister of Justice. Canada. Chapter F-14. p. 1–50.
Francis rC, hixon Ma, Clarke Me, Murawski sa, ralston s. 2007. Fisheries management—
ten commandments for ecosystem-based isheries scientists. Fisheries. 32:217–233.
doi:10.1577/1548-8446(2007)32[217:tCFBFs]2.0.Co;2
Fujita r, honey K, Morris a, wilson J, russell h. 2010. Cooperative strategies in isheries management: integrating across scales. Bull Mar sci. 86:251–271.
Fujita rM, Foran t, Zevos i. 1997. innovative approaches for fostering conservation in marine
isheries. ecol appl. 8(suppl):139–150.
gelcich s, hughes tP, olsson P, Folke C, defeo o, Fernandez M, Foale s, gunderson Lh,
rodriguez-sickert C, schefer M, et al. 2010. navigating transformations in governance of Chilean marine coastal resources. Proc natl acad sci Usa. 107:16,794–16,799.
PMid:20837530. doi:10.1073/pnas.1012021107
hatanaka M, Bain C, Busch L. 2005. hird-party certiication in the global agrifood system.
Food Policy. 30:354–369.
hilborn r. 2006. Faith-based isheries. Fisheries. 31:554–555.
hilborn r. 2007a. Moving to sustainability by learning from successful isheries. ambio.
36:296–303. doi:10.1579/0044-7447(2007)36[296:MtsBLF]2.0.Co;2
hilborn r. 2007b. reinterpreting the state of isheries and their management. ecosystems.
10:1362–1369. doi:10.1007/s10021-007-9100-5
hilborn r, stokes K. 2010. deining overished stocks: have we lost the plot? Fisheries. 35:113–
120. doi:10.1577/1548-8446-35.3.113
hilborn r, walters C. 1992. Quantitative isheries stock assesment. Chapman & hall, new
York.
hollowed aB, Bax n, Beamish r, Collie J, Fogarty M, Livingston P, Pope J, rice JC. 2000. are
multispecies models an improvement on single-species models for measuring ishing impacts on marine ecosystems? iCes J Mar sci. 57:707–719. doi:10.1006/jmsc.2000.0734
hughes tP, Bellwood dr, Folke C, steneck rs, wilson J. 2005. new paradigms for supporting the resilience of marine ecosystems. trends ecol evol. 20:380–386. doi:10.1016/j.
tree.2005.03.022
hutchings Ja. 2001. inluence of population decline, ishing, and spawner variability on the
recovery of marine ishes. J Fish Biol. 59:306–322. doi:10.1111/j.1095-8649.2001.tb01392.x
hutchings Ja, Minto C, ricard d, Baum JK, Jensen oP. 2010. trends in the abundance of marine ishes. Can J Fish aquat sci. 67:1205–1210. doi:10.1139/F10-081
hutchings Ja, reynolds Jd. 2004. Marine ish population collapses: consequences for recovery
and extinction risk. Bioscience. 54:297–309. doi:10.1641/0006-3568(2004)054[0297:MFPC
CF]2.0.Co;2
Jacquet J, Pauly d, ainley d, holt s, dayton P, Jackson J. 2010. seafood stewardship in crisis.
nature. 467:28–29. PMid:20811437. doi:10.1038/467028a
Jennings s, Blanchard J. 2004. Fish abundance with no ishing: predictions based on macroecological theory. J anim ecol. 73:632–642. doi:10.1111/j.0021-8790.2004.00839.x
Lester se, halpern Bs, grorud-Colvert K, Lubchenco J, ruttenberg Bi, gaines sd, airame s,
warner rr. 2009. Biological efects within no-take marine reserves: a global synthesis. Mar
ecol Prog ser. 384:33–46. doi:10.3354/meps08029
Lewandowski i, Faaij aPC. 2006. steps towards the development of a certiication system
for sustainable bio-energy trade. Biomass energy. 30:83–104. doi:10.1016/j.biombioe.2005.11.003
272
BULLETIN OF MARINE SCIENCE. VOL 87, NO 2. 2011
Ludwig d, hilborn r, walters C. 1993. Uncertainty, resource exploitation, and conservation:
lessons from history. science. 260:17–36. PMid:17793516. doi:10.1126/science.260.5104.17
Mapstone B, Little L, Punt a, davies C, smith a, Pantus F, Mcdonald a, williams a, Jones a.
2008. Management strategy evaluation for line ishing in the great Barrier reef: balancing conservation and multi-sector ishery objectives. Fish res. 94:315–329. doi:10.1016/j.
ishres.2008.07.013
McClanahan tr. 2007. Management of area and gear in Kenyan coral reefs. In: McClanahan
tr, Castilla JC, editors. Fisheries management: progress towards sustainability. Blackwell
Press, London. p. 166–185.
McClanahan tr, Castilla JC, white at, defeo o. 2009a. healing small-scale isheries by facilitating complex socio-ecological systems. rev Fish Biol Fish. 19:33–47. doi:10.1007/s11160008-9088-8
McClanahan tr, Cinner Je, graham naJ, daw tM, Maina J, stead sM, wamukota a, Brown
K, venus v, Polunin nvC. 2009b. identifying reefs of hope and hopeful actions: contextualizing environmental, ecological, and social parameters to respond efectively to climate
change. Conserv Biol. 23:662–671. PMid:19245493. doi:10.1111/j.1523-1739.2008.01154.x
McClanahan tr, hicks CC, darling es. 2008. Malthusian overishing and eforts to overcome
it on Kenyan coral reefs. ecol appl. 18:1516–1529. PMid:18767626. doi:10.1890/07-0876.1
Mcevoy aF. 1986. he isherman’s problem: ecology and law in California isheries, 1850–1980.
Cambridge University Press, new York. doi:10.1017/CBo9780511583681
Mcevoy aF. 1996. historical interdependence between ecology, production, and management
in California isheries. Usda Forest service technical report.
Mcgilliard Cr, hilborn r, MacCall a, Punt ae, Field JC. 2011. Can information from marine
protected areas be used to inform control-rule-based management of small-scale, datapoor stocks? iCes J Mar sci. 68:201–211. doi:10.1093/icesjms/fsq151
Mosquera i, Côté iM, Jennings s, reynolds Jd. 2000. Conservation beneits of marine reserves
for ish populations. anim Conserv. 3:321–332. doi:10.1111/j.1469-1795.2000.tb00117.x
Myers ra, worm B. 2003. rapid worldwide depletion of predatory ish communities. nature.
4:280–283. PMid:12748640. doi:10.1038/nature01610
national Parks act. 2000. department of Justice. Canada sC. 2000, c. 32. p. 1–164.
north Paciic Fishery Management Council. 2009. Fishery management plan for ish resources
of the arctic management areas. anchorage, alaska. p. 1–146.
ostrom e. 1990. governing the commons: the evolution of institutions for collective action.
Cambridge University Press, new York.
ostrom e. 1999. Coping with tragedies of the commons. annu rev Polit sci. 2:493–535.
doi:10.1146/annurev.polisci.2.1.493
Pauly d, Christensen v, guenette s, Pitcher tJ, sumaila Ur, walters CJ, watson r, Zeller
d. 2002. towards sustainability in world isheries. nature. 418:689–695. PMid:12167876.
doi:10.1038/nature01017
Piet gJ, rice JC. 2004. of precautionary reference points in providing management advice
on north sea ish stocks. iCes J Mar sci. 61:1305–1312. doi:10.1016/j.icesjms.2004.08.009
Pikitch eK, santora C, Babcock ea, Bakun a, Bonil r, Conover do, dayton PK, doukakis
P, Fluharty d, heneman B, et al. 2004. ecosystem-based ishery management. science.
305:346–347. PMid:15256658. doi:10.1126/science.1098222
Pinkerton e, edwards dn. 2009. he elephant in the room: the hidden costs of leasing individual transferable ishing quotas. Mar Policy. 33:707–713. doi:10.1016/j.marpol.2009.02.004
Pinkerton e, edwards dn. 2010. ignoring market failure in quota leasing? Mar Policy. 34:1110–
1114. doi:10.1016/j.marpol.2010.01.012
Pope J, rice J, daan n, Jennings s, gislason h. 2006. Modelling an exploited marine ish community with 15 parameters - results from a simple size-based model. iCes J Mar sci.
63:1029–1044.
Prince J. 2005. Combating the tyranny of scale for haliotids: micro-management for microstocks. Bull Mar sci. 76:557–577.
SALOMON ET AL.: BRIdgINg ThE dIVIdE
273
reuter rF, Conners e, diCosimo J, gaichas s, ormseth o, tenbrink t. 2010. Managing nontarget, data-poor species using catch limits: lessons from the alaskan groundish ishery.
Fish Manag ecol. 17:323–335.
rice J. 2003. environmental health indicators. ocean Coast Manag. 46:235–259. doi:10.1016/
s0964-5691(03)00006-1
rice J. 2007. an ecologist’s view of economic instruments and incentives. int J glob environ
issues. 7:191–204. doi:10.1504/iJgenvi.2007.013573
rice J, daan n, Pope Jg, gislason h. 1991. he stability of estimates of suitabilities in MsvPa
over 4 years of data from predator stomachs. In: daan n, sissenwine MP, editors. Multispecies models relevant to management of living resources. international Council exploration
sea, Copenhagen. p. 34–45.
rice J, rochet M. 2005. a framework for selecting a suite of indicators for isheries management. iCes J Mar sci. 62:516–527. doi:10.1016/j.icesjms.2005.01.003
rice JC. 2010. ecocertiication, assessments, and advice: implications of market measures for
traditional practices. iCes CM. d:02.
rice JC, Legace e. 2007. when control rules collide: a comparison of isheries management
reference points and iUCn criteria for assessing risk of extinction. iCes J Mar sci. 64:718–
722. doi:10.1093/icesjms/fsm011
rogers s, tasker M, earll r, gubbay s. 2007. ecosystem objectives to support the UK vision for
the marine environment. Mar Poll Bull. 54:128–144. PMid:17223138. doi:10.1016/j.marpolbul.2006.11.015
rosenberg aa, Fogarty MJ, sissenwine MP, Beddington Jr, shepherd Jg. 1993. achieving sustainable use of renewable resources. science. 262:828–829. PMid:17757341. doi:10.1126/
science.262.5135.828
salomon aK, shears nt, Langlois tJ, Babcock rC. 2008. Cascading efects of ishing can
alter carbon low through a temperate coastal ecosystem. ecol appl. 18:1874–1887.
PMid:19263885. doi:10.1890/07-1777.1
sumaila Ur. 2010. a cautionary note on individual transferable quotas. ecol soc. 15.
turris Br. 2010. a rejoinder to e Pinkerton et al., the elephant in the room: the hidden costs of
leasing individual transferable ishing quotas. Mar Policy. 34:431–436. doi:10.1016/j.marpol.2009.09.009
veron Jen, devantier LM, turak e, green aL, Kininmonth s, staford-smith M, Peterson
n. 2009. delineating the Coral triangle. galaxea. galaxea, J Coral reef stud. 11:91–100.
doi:10.3755/galaxea.11.91
walker Ph, hislop Jrg. 1998. sensitive skates or resilient rays? spatial and temporal shifts in
ray species composition in the central and north-western north sea between 1930 and the
present day. iCes J Mar sci. 55:392–402. doi:10.1006/jmsc.1997.0325
walters C. 1986. adaptive management of renewable resources. MacMillan Publishing Company, new York.
walters C. 2003. Folly and fantasy in the analysis of spatial catch rate data. Can J Fish aquat sci.
60:1433–1436. doi:10.1139/f03-152
wells s, Burgess n, ngusaru a. 2007. towards the 2012 marine protected area targets in eastern africa. ocean Coast Manage. 50:67–83. doi:10.1016/j.ocecoaman.2006.08.012
wilson Jr, Prince J, Lenihan hs. 2010. a management strategy for nearshore sedentary species
using marine protected areas (MPas) as a reference. Mar Coast Fish: dyn Manage ecosyst
sci. 2:14–27.
wilson wJ, ormseth oa. 2009. a new management plan for the arctic waters of the United
states. Fisheries. 34:555–558.
wise L. 2010. Morro Bay and Port san Luis business plan update. Lisa wise Consulting, inc.
worm B, Barbier eB, Beaumont n, dufy Je, Folke C, halpern Bs, Jackson JBC, Lotze hK,
Micheli F, Palumbi sr, et al. 2006. impacts of biodiversity loss on ocean ecosystem services.
science. 314:787–790. PMid:17082450. doi:10.1126/science.1132294
274
BULLETIN OF MARINE SCIENCE. VOL 87, NO 2. 2011
worm B, hilborn r, Baum JK, Branch ta, Collie Js, Costello C, Fogarty MJ, Fulton ea,
hutchings Ja, Jennings s, et al. 2009. rebuilding global isheries. science. 325:578–585.
PMid:19644114. doi:10.1126/science.1173146
Zabel rw, harvey CJ, Katz sL, good tP, Levin Ps. 2003. ecologically sustainable yield - marine
conservation requires a new ecosystem-based concept for isheries management that looks
beyond sustainable yield for individual ish species. am sci. 91:150–157.
date submitted: 12 october, 2010.
date accepted: 24 February, 2011.
available online: 4 april, 2011.
addresses: (aKs) School of Resource and Environmental Management, Simon Fraser
University, 8888 University Drive, Burnaby, BC, Canada V5A 1S6. (sKg) Resource Ecology
and Fisheries Management Division, Alaska Fisheries Science Center, National Marine
Fisheries Service, NOAA, 7600 Sand Point Way NE, Seattle, Washingon 98115. (oPJ) Institute
of Marine and Coastal Sciences, Rutgers University, 71 Dudley Road, New Brunswick, New
Jersey 08901. (vna) Global Marine Initiative, he Nature Conservancy, 255 Alhambra
Circle, Ste 312, Miami, Florida 33149. (nas) Gwaii Haanas National Park Reserve, National
Marine Conservation Area Reserve, and Haida Heritage Site, Box 37, Queen Charlotte, BC,
Canada V0T 1S0. (Jr) Ecosystem Sciences, Department of Fisheries and Oceans, 200 Kent
Street, Ottawa, Ontario, Canada K1A 0E6. (trM) Wildlife Conservation Society, Marine
Programs, Bronx, New York 10460. (Mhr) Stanford University, Woods Institute for the
Environment. Stanford, California 94305. (PL) Northwest Fisheries Science Center, National
Marine Fisheries Service, NOAA, Seattle, Washington. (nKd) Department of Biology, Earth to
Ocean Research Group, Simon Fraser University, 8888 University Drive, Burnaby, BC, Canada
V5A 1S6. (eaB) Division of Marine Biology and Fisheries, Rosenstiel School of Marine and
Atmospheric Science, University of Miami, 4600 Rickenbacker Cswy., Miami, Florida 33149.
Corresponding author: (aKs) E-mail: <anne.salomon@sfu.ca>.