Major Changes in the Ecology of the Wadden Sea: Human Impacts, Ecosystem Engineering and Sediment Dynamics
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Shallow soft-sediment systems are mostly dominated by species that, by strongly affecting sediment dynamics, modify their local environment. Such ecosystem engineering species can have either sediment-stabilizing or sediment-destabilizing effects on tidal flats. They interplay with abiotic forcing conditions (wind, tide, nutrient inputs) in driving the community structure and generating spatial heterogeneity, determining the composition of different communities of associated species, and thereby affecting the channelling of energy through different compartments in the food web. This suggests that, depending on local species composition, tidal flats may have conspicuously different geomorphology and biological functions under similar external conditions. Here we use a historical reconstruction of benthic production in the Wadden Sea to construct a framework for the relationships between human impacts, ecosystem engineering and sediment dynamics. We propose that increased sediment disturbances by human exploitation interfere with biological controls of sediment dynamics, and thereby have shifted the dominant compartments of both primary and secondary production in the Wadden Sea, transforming the intertidal from an internally regulated and spatially heterogeneous, to an externally regulated and spatially homogenous system. This framework contributes to the general understanding of the interaction between biological and environmental control of ecosystem functioning, and suggests a general framework for predicting effects of human impacts on soft-bottom ecosystems.
Key wordsbivalves deposit feeders internal regulation human transformation soft sediment food-webs historic trends
Across the world, human dominated coastal ecosystems are losing populations and species at an accelerating rate, with a strong risk of permanent impairment to key ecosystem functions and recovery potential (Lotze and others 2006; Worm and others 2006). Coastal soft-sediment systems comprise intertidal flats and estuaries which are highly productive, usually with a strong tradition of human exploitation (Costanza and others 1997; Lotze and others 2006; Airoldi and Beck 2007). The Wadden Sea is such a shallow estuarine area bordering the North Sea. In the course of intensified urbanization of coastal habitats, intertidal areas in Europe have been subjected to a dramatic degradation of food-web complexity and ecosystem services by multiple stressors. These include: pollution with nutrients and chemicals, the development of increasingly intense forms of exploitation (for example, shellfish dredging, bottom trawling), natural habitat destruction through large-scale hydraulic engineering (for example, diking and reclamation), which not only acts locally but also changes hydrodynamic conditions and increases suspended sediment concentrations over large areas (Wolff 2000; Cloern 2001; Lotze and others 2005; Wolff 2005; Lotze and others 2006; Airoldi and Beck 2007). Although many studies have shown that ecosystem engineers, such as reef forming bivalves and seagrasses, fulfil key-functions in structuring intertidal soft-bottom ecosystems (Verwey 1952; Reise 1985; Bouma and others 2009 and references therein) there is an ongoing debate on their relevance as independent and significant drivers of change in the Dutch part of the Wadden Sea (the western part). Current integrative analyses of causes of ecological change in the the Dutch Wadden Sea have emphasized processes acting on primary producers (temperature, nutrient inputs) much more than changes in top-down processes resulting from exploitation of higher trophic levels (for example, Weijerman and others 2005; Philippart and others 2007). Here we argue that failure to detect and document clear consequences of the intense human exploitation of multiple trophic levels in the western Wadden Sea mainly result from poor recognition of the importance of non-linear dynamics caused by the biological feedbacks that characterize benthic soft-sediment systems (Verwey 1952).
In marine ecosystems at large, the tightly integrated relationship between trophic structure and ecosystem processes for maintaining ecosystem functioning is widely acknowledged (Menge 2000; Worm and others 2002; Daskalov and others 2007; Österblom and others 2007). Interactions between top–down and bottom–up regulation have been demonstrated in a wide variety of systems and scales, and consensus is now emerging on the importance of considering the joint effects of fisheries and eutrophication in management of marine resources (Österblom and others 2007; Eriksson and others 2009). However, soft-sediment ecosystems are also controlled by strong non-trophic interactions from the critical feedbacks that many soft-sediment organisms have on the environmental conditions that in turn affect their own and other organism’s performance (‘ecosystem engineers’; sensu Jones and others 1994; Bouma and others 2009; Olff and others 2009).
Species that dominate the shallow benthos of soft-sediment systems have a high impact on environmental conditions related to sediment properties, such as sediment stability, texture, aeration, resuspension and sedimentation (Hall 1994; Schaffner and others 2001; Montserrat and others 2008; Bouma and others 2009; Van Colen and others 2009). These species include seagrasses, biogenic reefs of suspension feeding bivalves and a number of bioturbating polychaete worms and crustaceans, all of which not only respond to sediment stability and texture but also strongly affect it (Reise 1985; Flach 1992; van de Koppel and others 2005a; Huxham and others 2006, van der Heide and others 2007). Altering local sediment dynamics by either increasing the erosion of the sediment or promoting the settlement of finer particles causes these species to be a major force on regional landscape-forming processes, interacting with the hydrodynamics imposed upon the system by waves and currents (Bouma and others 2009).
Due to the prevalence of ecosystem engineering, effects of human exploitation may have highly persistent implications for soft-bottom communities. Modelling studies from both marine and limnic soft-sediment communities with strong feedbacks between dominating species groups and the environment suggest that distinctly different communities structured by different processes may develop under similar external conditions (Scheffer and others 2001; Rietkerk and others 2004; van de Koppel and others 2005a). This suggests that tidal flats may have conspicuously different geomorphology and biological functions largely depending on the local dominance of species. Furthermore, human impacts on soft-sediment systems commonly have direct effects on sediment conditions (for example, Piersma and others 2001; Erftemeijer and Lewis 2006). Thus, exploitation of specific benthic fauna together with disruption of the sediment dynamics may result in a highly resistant modification of the biological community by deleting the biological feedback mechanisms that determine the sedimentary environment (‘hysteresis’). Here we use available historic estimations and time-series data on nutrients, light, primary production (PP) and abundances of ecosystem engineers from the western part of the Dutch Wadden Sea to construct a conceptual framework on the ways in which human impacts may have caused fundamental changes in soft-sediment ecosystems. We propose that human impacts have modified coastal production and caused non-linear effects on community structure by increasing sediment disturbance, and thereby have changed the Wadden Sea from an internally to an externally regulated ecosystem.
Trends in Primary Producers
The second important intensification of human impacts on PP was a large-scale eutrophication of the system in the 1970–1980s, where microalgal production at first was significantly stimulated by high loads of phosphorus from poor waste water treatment and agricultural runoff (De Jonge and others 1993) and then decreased again with declining nutrient loads from improved management of water quality (van Raaphorst and de Jonge 2004; Philippart and others 2007). Thus, in the 1970s increasing nutrient loads restore the pre-1930 pelagic production, but subtidal seagrass did not recover and light availability continued to decrease (Figure 2A, B). Nutrient enrichment is often fatal to diversity of primary producers with strong effects on community composition (for example, Eriksson and others 2006), but we have no century-long data series on trends in the diversity of pelagic plankton. Nevertheless, during the period of eutrophication (1970–1990), smaller flagellates increased the most (Philippart and others 2007). Later, when nutrient levels and pelagic production dropped back to pre-eutrophication levels, it was mainly larger diatoms that declined. Since 1995 the light levels in the water have continued to decrease and there is still no significant recovery of subtidal seagrasses in the Dutch Wadden Sea.
Trends in Benthic Fauna
Most of the species of the benthic fauna in the Wadden Sea have strong effects on sediment dynamics when they occur in high densities; ranging from the sediment-stabilizing bivalve reefs constructed by filter-feeding blue mussels (Mytilus edulis) and oysters (Ostrea edulis, Crassostrea gigas), and bank-forming cockles (Cerastoderma edule), to sandy fields dominated by the bioturbating, sediment-destabilizing lugworm (Arenicola marina). Like seagrasses, at high densities reef-building species decrease sediment erosion and facilitate finer particles to settle by slowing down water flow close to the bottom (Gutierrez and others 2003). This typically increases the organic content of the sediment surrounding intertidal mussel or oyster reefs. The recruitment of blue mussels and cockles on intertidal flats in the Wadden Sea correlates with relatively increased silt content of the sediment (Piersma and others 2001). This suggests that the engineering effect of bivalve reefs will promote their own recruitment and that there may be significant positive feedbacks between bivalves and sediment stability. Deposit feeding bioturbators (commonly polychaete worms or crustaceans) destabilize the sediment by digging or burrowing activities (Rhoads 1974). At high local densities, bioturbators may therefore disturb or preclude the sediment stabilizing feedbacks that increase the settling of finer particles, caused both by seagrass and mussel beds, and which promote the recruitment of many bivalves (Rhoads and Young 1970; Piersma and others 2001). Accordingly, there is evidence of mutually negative interactions between seagrass and bioturbating polychaete worms (Philippart 1994; Hughes and others 2000) and crustaceans (Siebert and Branch 2006). For off-shore systems, positive feedbacks between sediment conditions and the biological community have been suggested to cause distinct alternative communities dominated by either sediment-stabilizing brittle stars or bioturbating crustaceans at similar environmental conditions (van Nes and others 2007).
Throughout Europe, reef-building species declined dramatically over the last century through human exploitation of all sorts of bivalves, but especially oysters and mussel abundances have been severely affected (Lotze and Reise 2005; Lotze and others 2006; Airoldi and Beck 2007). In addition to direct removal of bivalves, resuspension of the sediment connected to trawling and dredging destabilize sediment conditions and human activities may therefore also have indirect negative effects on bivalve recruitment. In the Wadden Sea, poor recruitment after a documented large-scale shellfish dredging event hindered reestablishment of blue mussels and cockles for almost a decade (Piersma and others 2001, and see reoccurring patterns documented by van Gils and others 2009). The poor recruitment coincided with changed sediment characteristics, where low sediment stability after the perturbation hindered sedimentation of finer silts and finer organic material which is associated with spatfall. Here, we propose that increased sediment disturbance by human exploitation of soft-sediment resources may disrupt sediment-stabilizing feedbacks, and thereby promote a shift from dominance of sediment-stabilizing filter feeders to dominance of sediment destabilizing bioturbating species (Figure 1B).
We have no historic estimates of the overall distribution of intertidal bivalve beds in the western Wadden Sea. However, fragmented blue mussel information suggests that the presence of blue mussel beds were at least as high before 1930 as in the 1970s, when they covered an total area of 1155 ha (Figure 2C; Dankers and others 2003). Starting in the 1980s, there was a strong increase of deposit/mixed feeding polychaetes that continued through the 1990s (at monitoring site Balgzand, Figure 2C; Essink 2005). Philippart and others (2007) showed that benthic secondary production increased significantly at this site comparing 1970–1980 with 1980–2000, due to a strong increase of deposit feeding macrozoobenthos. In the 1980s, fishing on intertidal resources also accelerated dramatically as demonstrated by a five and three times increase in the catch of cockles and mussels, respectively, compared with the decade before (Figure 2D, Dijkema 1997; Dankers and others 2003; Kesteloo and others 2004). In 1989–1990 the intertidal beds were completely removed in the western Dutch Wadden Sea and they did not recover (Beukema and Cadee 1996). Accordingly, the biomass of both blue mussels and cockles are low in the intertidal monitoring programs since the 1990s (Philippart and others 2007), whereas polychaetes have increased four times the biomass registered in the 1970s. In 2009, the intertidal area covered by mussel beds was 157 ha, 13% of the area covered in the 1970s (Figure 2C). The shift from a high cover of sediment stabilizing bivalve beds to a high density of sediment-destabilizing lugworms is supported by a relative increase in worm eating bird species compared to bivalve feeding bird species in the Wadden Sea during this period (van Roomen and others 2005).
Blue mussel beds indirectly increase local PP (Asmus and Asmus 1991; Baird and others 2007). To estimate changes in the contribution of blue mussel beds to benthic PP in the intertidal, we related the changes in area of mussel beds in the western Dutch Wadden Sea to production data from the Sylt-Romö area in the north-eastern part of the Wadden Sea. The Sylt-Romö production data were collected during a 20 year period, compartmentalized into different habitat types and made available in Baird and others (2007). In the Sylt-Romö system, blue mussels are by far the most productive (1460 gC m−2 y−1) followed by dense Zostera noltii beds (intertidal seagrass: 368 gC m−2 y−1). These two habitats are 6 and 1.5 times more productive compared to other benthic habitats (muddy and sandy flats and shoals: mean = 228, SE = 5; Arenicola-flats: 237 gC m−2 y−1). The strong increase in PP on mussel beds depends on perennial macroalgae which attach to the mussels, such as Fucus spp. The pelagic domain is by far the least productive (90 gC m−2 y−1). According to these data, the documented decrease of blue mussels in the 1990s in the western Wadden Sea can be estimated as a loss in PP of 24 gC m−2 y−1 averaged over the whole intertidal area (from a contribution of 28.0 to 3.8 gC m−2 y−1).
Mussel beds also promote local pelagic production by remineralizing nutrients. Experiments from tidal pools show that the presence of mussels increases local PP up to eight times (Pfister 2007). Flume measurements over blue mussel beds in the field indicate that the potential pelagic production from release of nutrients significantly exceeds the reduction in phytoplankton by feeding (Asmus and Asmus 1991). For intertidal blue mussel beds in the northern Wadden Sea, 1 m2 of mussel bed sustains a pelagic production of 3.55 gC per day in summer through nutrient release (corrected for phytoplankton uptake; Asmus and Asmus 1991). This indicates that the dramatic declines in bivalve reefs in the 1990s have decreased the production potential of the Wadden Sea significantly.
Internal Versus External Regulation
The historic synthesis suggests that three major human impact events have contributed to changed drivers of ecosystem functioning in the Wadden Sea over the last century. This includes the dramatic loss of seagrass from dredging and disease in the 1930s, the major increase in production from eutrophication in the 1980s and the removal of all intertidal mussel beds and most of the high density cockle-beds in the 1990s. As shown, seagrass meadows and mussel banks provide conspicuous and large-scale internal regulation of ecosystem services, mainly by: (1) generating a heterogeneous landscape, both by their physical structures and by accumulating sediment (Gutierrez and others 2003; van der Heide and others 2007); (2) contributing much higher benthic primary and secondary production than other habitats on shallow soft-bottoms (Asmus and Asmus 2000; Baird and others 2007); and (3) promoting PP by improving the light climate (seagrass) and remineralization of nutrients (mussels) (Asmus and Asmus 1991; van der Heide and others 2007). Thus, a soft-sediment system dominated by sediment stabilizing ecosystem engineers is a system with a high degree of internal stimulation both of habitat heterogeneity and PP.
However, trophic dynamics of coastal systems are not only determined by local processes but also by the food web dynamics in deeper off-shore systems, and vice versa (Estes and others 1998; Jackson and others 2001; Ljunggren and others in press.). Globally, as well as for the Wadden Sea, off-shore food-webs have undergone massive changes over the last decades due to overexploitation of the main fish stocks (Wolff 2005; Worm and others 2006). Changes in off-shore food web configuration can cascade to coastal food-webs by changes in predation pressures (Jackson and others 2001) or as food-depletion caused by massive increases in migrating off-shore mesopredators (Ljunggren and others in press). Other dominating changes in external influences are an increased nutrient and organic matter load caused by a general eutrophication of major rivers (Vitousek and others 1997), and a predicted increase in storm frequency and wave intensity by climate change (Harley and others 2006). Intertidal mussel beds and oyster reefs may be severely eroded by extreme weather events, such as severe storms and accumulations of drift ice (Armonies and others 2001; pers. obs.). At the same time, changes in coastal ecosystem functioning in most soft-sediment systems by large scale loss of seagrasses, mangroves and/or reefs building species (Valiela and others 2001; Duarte 2002; Lotze and others 2006; Orth and others 2006) have probably lead to decreased nursery functions for the main off-shore crustacean and fish populations, thereby limiting the exchange of juveniles in many areas. Here we propose that by negative effects on sediment stabilizing ecosystem engineers through trawling and dredging, together with increased external inputs of nutrient resources, human disturbances change shallow soft-bottom communities from mainly internally regulated systems to systems dominated by external forcing (Figure 1C).
We can also distinguish four phases in the development of the western Wadden Sea (Figure 2). Phase I (1900–1930) is a period of low external nutrient loading with high water transparency, high pelagic production and a high contribution of subtidal seagrass (Zostera marina) to the benthic production. Phase II (1930–1970) is a period with still relatively low nutrient concentrations, decreasing transparency of the water with a parallel decrease in pelagic production, and an almost total loss of subtidal seagrass. Phase III (1970–1990) is a period of very high nutrient loads and a doubling of pelagic production restoring levels to historical estimations. There is a continuing decrease of water transparency and no significant recovery of subtidal seagrass. During this phase shellfish fisheries expand and intensify. Phase IV (1990–2008) is a period of gradually declining nutrient concentrations, water transparency and pelagic production, whereas dramatic decreases in intertidal mussel beds are paralleled by increases in polychaete worms. The distinctly different relations between species groups in the different phases show that the system has not responded linearly to external forcing: there are periods with equally high pelagic production under both low and high nutrient loads (phase I and III), and there are periods with distinctly different compositions of benthic production under similar nutrient loads (phase II and IV, Figure 2). Thus, our results indicate complex dynamics, where the different time periods in the Wadden Sea have different relations between external abiotic conditions and biological production. This contrasts strongly with the traditional management view of coastal ecosystems in which production mainly is driven by linear and reversible responses to resource load, and specifically to recent concerns that it is modern water quality management that is most responsible for decreased production of fisheries resources (Daan and van der Mheen 2004; Philippart and others 2007). Instead, our synthesis indicates that the western Wadden Sea system may have lost much of its internal contribution to production by human disturbances, which makes the modern state highly vulnerable to external nutrient loads.
The lack of recovery of both subtidal seagrasses and intertidal blue mussels after the disturbance events does indeed indicate that human activities have changed the abiotic conditions and/or deleted feedbacks from the biological communities necessary for reestablishment. For seagrass there is compelling evidence that subtidal seagrass recovery at present is impossible because of increased amounts of suspended sediments in the water, limiting light availability (van der Heide and others 2007). The increase of suspended sediments in the water column is partly a consequence of the reduction in subtidal seagrass itself and partly of the changed hydrodynamics due to large-scale coastal protection measures, such as dams, dikes and goynes (van der Heide and others 2007). Based on the trends and processes we have described, we propose that a human-driven regime shift in trophic structures and ecosystem regulation has moved the Wadden Sea from an internally regulated system dominated by sediment stabilizing ecosystem engineers, towards a system driven by external drivers and dominated by sediment destabilizing deposit feeders. If the apparent non-linearity of soft-bottom systems is true, it may be difficult to restore the degraded habitats and production potential of the system without more radical measures than just the reduction of local human impacts, which is the dominating strategy by nature management, conservation organizations and policy makers today. Our synthesis suggests: (1) that we need to adopt an ecosystem-based management perspective that acknowledges the strong and dynamic interdependencies between nature conservation, fisheries, water quality management and coastal defence, and (2) that restoration projects of seagrass meadows and bivalve reefs need to be performed at such scales that we also restore the important feedback mechanisms needed to promote those local abiotic conditions that are favorable for the target species (see also: van der Heide and others 2007; Eriksson and others 2009; Schulte and others 2009).
We thank Serena Donadi, Johan Eklöv and Els van der Zee for stimulating discussions, Dick Visser for artwork, and Heike Lotze, Simon Thrush and an anonymous reviewer for valuable comments on the text.
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- Airoldi L, Beck MW. 2007. Loss, status and trends for coastal marine habitats of Europe. Oceanogr Mar Biol 45:345–405.Google Scholar
- Daan N, van der Mheen HW. 2004. Outstanding environmental issues in relation to European fisheries. Neth Inst Fish Res RIVO 62:1–21.Google Scholar
- Dankers NMJA, Meijboom A, Cremer JSM, Dijkman EM, Hermes Y, te Marvelde L. 2003. Historische ontwikkeling van droogfallende mosselbanken in de Nederlandse Wadden Zee. Alterra Rep 873:1–114.Google Scholar
- De Jonge VN, Essink K, Boddeke R. 1993. The Dutch Wadden Sea—a changed ecosystem. Hydrobiologia 265:45–71.Google Scholar
- Dijkema KS. 1997. Molluscan fisheries and culture in the Netherlands U.S. Commer., NOAA Tech. Rep. NMFS 129:115–35.Google Scholar
- Duarte CM. 2002. The future of seagrass meadows. Environ Conserv 29:192–206.Google Scholar
- Essink K. 2005. Macrozoobenthos. Wadden Sea Ecosyst 19:184–9.Google Scholar
- Hall SJ. 1994. Physical disturbance of marine benthic communities—life in unconsolidated sediments. Oceanogr Mar Biol 32:132–79.Google Scholar
- Jackson JBC, Kirby MX, Berger WH, Bjorndal KA, Botsford LW, Bourque BJ, Bradbury RH, Cooke R, Erlandson J, Estes JA, Hughes TP, Kidwell S, Lange CB, Lenihan HS, Pandolfi JM, Steneck PCHRS, Tegner MJ, Warner RR. 2001. Historical overfishing and the recent collapse of coastal ecosystems. Science 293:629–38.CrossRefPubMedGoogle Scholar
- Kesteloo JJ, Stralen MR, Breen V, Craeymeersch JA. 2004. Het kokkelbestand in de Nederlandse kustwateren in 2004. Nederlands Instituut voor Visserij onderzoek (RIVO) BV Rapport C052:1–48.Google Scholar
- Ljunggren L, Sandström A, Bergström U, Mattila J, Lappalainen A, Johansson G, Sundblad G, Casini M, Kaljuste O, Eriksson BK. Recruitment failure of coastal predatory fish in the Baltic Sea is related to an offshore system shift. ICES J Mar Sci (in press).Google Scholar
- Peterson CH, Summerson HC, Fegley SR. 1987. Ecological consequences of mechanical harvesting of clams. Fish Bull 85:281–98.Google Scholar
- Reise K. 1985. Tidal flat ecology: an experimental approach to species interactions. Berlin: Springer-Verlag.Google Scholar
- Rhoads DC. 1974. Organism-sediment relation on the muddy sea floor. Oceanogr Mar Biol Annu Rev 12:263–300.Google Scholar
- Rhoads DC, Young DK. 1970. Influence of deposit-feeding organisms on sediment stability and community trophic structure. J Mar Res 28:150.Google Scholar
- Schaffner LC, Dellapenna TM, Hinchey EK, Friedrichs CT, Neubauer MT, Smith ME, Kuehl SA. 2001. Physical energy regimes, seabed dynamics and organism-sediment interactions along an estuarine gradient. In: Aller JY, Woodin SA, Aller RC, Eds. Organism-sediment interactions. Columbia: University of South Carolina Press. Google Scholar
- van Roomen M, van Turnhout C, van Winden E, Koks B, Goedhart P, Leopold M, Smit C. 2005. Trends in benthivorous waterbirds in the Dutch Wadden Sea 1975–2002: large differences between shellfish-eaters and worm-eaters. Limosa 78:21–38.Google Scholar
- Wolff WJ, den Hartog C, Dijkema KS, Admiraal W, Colijn F, van den Hoek C, Joenje W, de Jonge VN, Polderman PJG. 1979. Flora and vegetation of the Wadden Sea. Report of the Wadden Sea Working Group 3:1–206.Google Scholar