Increasing species richness of the macrozoobenthic fauna on tidal flats of the Wadden Sea by local range expansion and invasion of exotic species
© The Author(s) 2010
Received: 26 April 2010
Accepted: 29 June 2010
Published: 18 July 2010
A 40-y series of consistently collected samples (15 fixed sampling sites, constant sampled area of 15 × 0.95 m2, annual sampling only in late-winter/early-spring seasons, and consistent sieving and sorting procedures; restriction to 50 easily recognizable species) of macrozoobenthos on Balgzand, a tidal flat area in the westernmost part of the Wadden Sea (The Netherlands), revealed significantly increasing trends of species richness. Total numbers of species annually encountered increased from ~28 to ~38. Mean species density (number of species found per sampling site) increased from ~13 to ~18 per 0.95 m2. During the 40 years of the 1970–2009 period of observation, 4 exotic species invaded the area: (in order of first appearance) Ensis directus, Marenzelleria viridis, Crassostrea gigas, and Hemigrapsus takanoi. Another 5 species recently moved to Balgzand from nearby (subtidal) locations. Together, these 9 new species on the tidal flats explained by far most of the increase in total species numbers, but accounted for only one-third of the observed increase in species density (as a consequence of the restricted distribution of most of them). Species density increased particularly by a substantial number of species that showed increasing trends in the numbers of tidal flat sites they occupied. Most of these wider-spreading species were found to suffer from cold winters. During the 40-y period of observation, winter temperatures rose by about 2°C and cold winters became less frequent. The mean number of cold-sensitive species found per site significantly increased by almost 2 per 0.95 m2. Among the other species (not sensitive to low winter temperatures), 6 showed a rising and 2 a declining trend in number of occupied sites, resulting in a net long-term increase in species density amounting to another gain of 1.6 per 0.95 m2. Half of the 50 studied species did not show such long-term trend, nor were invaders. Thus, each of 3 groups (local or alien invaders/winter-sensitive species/other increasing species) contributed to a roughly similar extent to the overall increase in species density.
Though there is widespread and right concern on global-wide declining biodiversity, reports of increasing species richness in specific areas have been reported as well. Such increases in species numbers in local areas can arise from introductions of invaders from distant locations (exceeding numbers of extinctions) or from changes in environmental conditions (when these changes promote more species than they do harm). Both types of causes can be directly influenced by man: invasions by increased shipping (Reise et al. 1999) and changes in habitat diversity and suitability by management (protection/restoration) and disturbance. A special class of changing environmental conditions affecting species richness is the ongoing climate change by which some species are locally promoted and others put at a disadvantage.
For invertebrates in the marine environment, few homogeneous data series of sufficient length appear to be available to reliably judge long-term trends in species richness and relate possible trends to underlying causes. There are several reports on successful introductions of exotic species leading to increases in species numbers, as displacement of autochthonous species appears to be a rare phenomenon (Reise et al. 1999; Wolff 2000). A warming climate generally results in poleward shifts of distribution areas, southern species increasing in abundance and northern species declining in the northern hemisphere (Sagarin et al. 1999). As species richness generally declines with increasing latitude, species gains tend to exceed species losses in areas at higher latitudes (Hawkins et al. 2009).
This study is based on a 40-y series of consistently collected quantitative data on macrozoobenthos in a vast area in the Dutch Wadden Sea. The Wadden Sea is an estuarine area of geologically young age and was seriously human-altered for the last centuries (Lotze et al. 2005). Such areas appear to be particularly vulnerable for exotic invaders (Wolff 1999). The Wadden Sea is characterized by vast tidal mud and sand flats, which are inhabited by a fauna with high biomass and low species diversity (Beukema 1976; Beukema and Cadée 1997). Part of the species suffer from severe winters (Beukema 1979; 1990) and may profit from the warming climate (Beukema 1992). Data series reviewed by Van der Graaf et al. (2009) point to increasing species numbers in various parts of the Wadden Sea for recent decades. However, for methodological reasons, these trends should be considered with caution. Avoiding these methodological problems by a restriction to a delimited group of conspicuous species, we analyze changes in total species numbers as well as in species density (number of species per unit area) and relate these changes to some possible underlying processes, such as invader introductions, climate change and human disturbance.
Since around 1970, data on macrozoobenthos have been collected twice annually at 15 permanent (marked) sampling stations (“sites”) located on Balgzand, a 50-km2 tidal flat area in the westernmost part of the Wadden Sea. For this study, we used only data collected in late-winter/early-spring, mostly in March, when numbers are at an annual minimum. Most (12) sites were 1-km long transects where 50 bottom samples of nearly 2 dm2 each were taken at distance intervals of 20 m, together 0.95 m2 per site. The 3 other sites were squares of 900 m2 where 9 samples of close to 0.1 m2 each were taken at randomly chosen places. The sites covered the entire intertidal range and nearly the full range of sediment types on Balgzand (Beukema and Cadée 1997). There was little change in these abiotic conditions during the 40-y period of observation. Hard substrates such as dikes were not sampled, but animals attached to shells of mussels or oysters were included. The samples were sieved (1-mm square meshes) in the field and sorted alive in the laboratory. All living animals were picked out, sorted to species level as much as possible, and counted. Further details on the sampling area, the sampling stations, and the methods can be found in Beukema and Cadée (1997).
Temperature data were taken from Van Aken (2008). We used monthly means of surface water temperatures in the nearby Marsdiep tidal channel and averaged for each winter the means of December, January and February to obtain a mean winter water temperature.
Sources of error
Summary of contributions by various groups of species to long-term (1970–2009) changes in macrozoobenthic species richness on Balgzand, expressed in (changes of) mean number of species per site (n, per 0.95 m2)
+~1.5 (Fig. 4b)
See Fig. 5
+~0.2 (Fig. 4b)
Crep, Gly, Lep, Ech, Oph a
+~1.8 (Fig. 4a)
See Fig. 2
+~2.0 (Fig. 4c)
Lit, Ner spp., Ete, Uro, Gam, Balb
−~0.4 (Fig. 4c)
Mag, Scolel c
No trend, common
~0 (Fig. 4d)
No trend, rare
~0 (Fig. 4d)
Total (see Fig. 1b)
In fact, many more than these 50 macrozoobenthic species are present on Wadden Sea tidal flats, and some tens of them were regularly or occasionally found in our samples. Some hundreds of benthic invertebrate species have been reported from the tidal plus subtidal parts of the international Wadden Sea, most of them small-sized (Wolff and Dankers 1981; Petersen et al. 1996). By reducing a full list to 50 selected items, we are convinced that we anticipated a possible positive bias in the species-richness trend due to a growing skill in recognizing species.
Long-term trends in species numbers and temperature
In accordance with the recent trend of rising temperatures, which is particularly strong in Dutch coastal waters and occurs in all seasons (Van Aken 2008, 2010), annual mean water temperatures rose by a mean rate of ~0.05°C year−1 during the 1970–2009 period of observation (Fig. 1a). Annual means increased from about 10 to almost 12°C (correlation with year number r = 0.63, n = 39, P < 0.0001); fluctuations in winter (Dec–Jan–Feb periods) temperatures were stronger and more irregular (open points in Fig. 1a), but nevertheless winter water temperatures showed a significantly positive correlation with year number (r = 0.36, n = 39, P < 0.05), again at a mean rate of increase of ~0.05°C year−1. Among the 40 winters of the period of observation, 8 were particularly cold (mean winter water temperature <3°C): 1970, 1979, 1982, 1985, 1986, 1987, 1996 and 1997 (see open points of Fig. 1a, c). Such severe winters appear to occur less frequently during the last than the first half of the 1970–2009 period.
In early 1991, the species numbers were particularly low (crosses in Fig. 1c). In that year, not any mussel bed was present on Balgzand as a consequence of heavy fishing in the summer of 1990 (Beukema 1993; Beukema and Cadée 1996). In 1991, the number of species was not only reduced by the absence of the one species Mytilus edulis but also by the absence of species that use mussel shells as a hard substrate such as barnacles and periwinkles.
Effects of winter temperatures
Several zoobenthic species living on Wadden Sea tidal flats are sensitive to low winter temperatures, i.e. they show significantly reduced survival rates in severe winters (Beukema 1979). Some of these species completely or almost completely disappear from the intertidal after the coldest winters, either at all intertidal zones (Beukema 1990) or only at the sampling sites at high intertidal levels (Beukema 1985). Beukema (1990) listed 11 of such winter-sensitive species of benthic animals on Balgzand. They are all included in the present 50-species list, and 10 of them showed a significantly positive relationship between winter temperature and number of sites subsequently occupied: the bivalves Cerastoderma edule (Fig. 2d), Abra tenuis (Fig. 2b), Tellina tenuis (Fig. 2b) and Mysella bidentata (Fig. 2c), the polychaete worms Lanice conchilega (Fig. 2a) and its commensal Malmgreniella lunulata (Fig. 2a) and Nephtys hombergii (Fig. 2c), the group of Nemerteans (Fig. 2d), and the crustaceans Crangon crangon (Fig. 2e) and Carcinus maenas (Fig. 2f). The 11th species (Bylgides sarsi) that was reported to show reduced survival in cold winters did not show a significant relationship as shown in Fig. 2, nor did it show a long-term trend in numbers of site occupied.
As to be expected from the substantial share of winter-sensitive species among the macrozoobenthic fauna on Balgzand, the total numbers of species found were higher after mild than after cold winters, for both 14.25- and 0.95-m2 sampling areas (solid and open points of Fig. 3a). To allow for the interaction between year number and winter temperatures, the species numbers were de-trended, i.e. they were augmented by 0.21 (number per 14.25 m2) or 0.13 (number per 0.95 m2) for each year before 1990 and reduced by the same amount for each year after 1990 (correction values taken from Fig. 1b). The thus year-influence-corrected species numbers were still significantly positively correlated with preceding-winter water temperatures (Fig. 3b), increasing by ~1.1 (14.25 m2) and ~0.6 (0.95 m2) species per 1°C temperature rise.
At least 6 frequently observed species were completely absent after the coldest winters (zero points in Fig. 2 at the lowest temperatures) and some of them needed a few years after a severe winter to recover and thus remained absent for another 1 or 2 year (most of the zero points in Fig. 2 at winter temperatures of >4°C). Some other species (e.g. N. hombergii and C. edule, Fig. 2c, d) occurred at reduced numbers of sites after the coldest winters, but were never completely absent. Complete absence affects the total species number per 14.25 m2 as well as the mean number per 0.95 m2, whereas absence at part of the sampling sites only reduces the mean species number per 0.95 m2.
After most of the mild winters, all of the above 10 winter-sensitive species were present at one or more sites. In these years, the group contributed a number of 10 to the total (per 14.25 m2) species number (solid squares in Fig. 1c). After cold winters, only about half of these species were present at one or more sites, resulting in a contribution of ~5 winter-sensitive species to total species numbers (open squares for 1970, 1979, 1982, 1985, 1986, 1987, 1996 and 1997 in Fig. 1c). Whenever a severe winter had occurred at least 3 years ago (as in the 1974–1978, 1991–1995, and 2000–2009 periods), the contributions of winter-sensitive species were 10 or close to 10 species (solid squares of Fig. 1c). Likewise, but less pronounced, mean contributions of winter-sensitive species per 0.95 m2 were higher after mild than after cold winters (solid and open circles in Fig. 1c) and were particularly high in years long after a severe winter.
Apart from the above 4 invasive species that recently arrived in Europe, 5 more species (that were already present in the North Sea area for at least decades) were only recently observed on the Balgzand tidal flats: Crepidula fornicata, Glycera alba, Lepidochitona cinerea, Echinocardium cordatum and Ophiura ophiura. This small group of newcomers on the Balgzand tidal flats was observed in small numbers (mostly only 1 specimen) at few sites (mostly only 1 site), thus contributing little to species numbers per 0.95 m2 (open points in Fig. 4b).
Among the remaining 31 species (50-10-4-5), 6 showed a statistically significant upward and 2 a significant downward trend in the numbers of sites where they were encountered in the successive years of the 1970–2009 period of observation. Together, the 6 species with a positive trend (Littorina littorea, Nereis spp. (mostly Alitta succinea, but also including some A. virens and Eunereis longissima), Eteone spp., Urothoe poseidonis, Gammarus locusta, and the group of Balanoids) showed an increase in mean numbers of species per site from ~0.7 to ~2.7 species per 0.95 m2 (Fig. 4c). The 2 species with a negative trend (Magelona johnstoni, Scolelepis foliosa) showed a decline from ~0.7 to ~0.3 species per 0.95 m2 (Fig. 4c). Thus, the net contribution to species density of the 8 species with a significant trend amounted to a positive value of 2.0–0.4 = 1.6 species per 0.95 m2. The remaining 23 species did not contribute (neither positively nor negatively) to species density (Fig. 4d).
A long period of consistent sampling of the macrozoobenthic fauna on the Balgzand tidal flats revealed a gradual increase in species richness. Expressed as total number of species encountered, the increase amounted to about 35% (~28 to ~38) over the entire 40-y period of observation. Expressed as a mean number per sampling site, the increase was of a similar magnitude (~13 to ~18 per 0.95 m2). As a measure of species richness, we consider the latter estimate of species density superior to total species number, because the total number found in any year strongly depends on finds of just one individual of a rare species. Each of such finds would add about 3% to total species number, but only about 0.5% to the number per site (1/15 = 0.07, being 0.5% of 14.2, the long-term mean number of species per 0.95 m2).
The above numbers refer to a limited group of 50 species, all easily identifiable and relatively conspicuous. This limitation was thought imperative to exclude a possibly serious influence of growing experience of the observers in sorting samples and/or recognizing rare or similar-looking species, which would lead to undeservedly increasing estimates of numbers of species found during the long period of observation.
We identified various groups of species to contribute to the increasing trend in species richness. The 10 winter-sensitive species (mentioned in Fig. 2) contributed together ~1.8 species per 0.95 m2 to the increase in species density (Fig. 4a), in accordance with the increasing trend of winter temperatures and the declining frequency of occurrence of cold winters (Fig. 1a). The species belonging to this group hardly affected the total species numbers, because they were all present at one or more sites both at the start and at the end of the 40-y period. The appearance of 9 invaders, either of exotic or local origin, explained almost completely the long-term increase in total species number (amounting to 10 species). The contribution to the long-term increase in species density of exotic and local newcomers amounted to 1.5 and 0.2 species per 0.95 m2, respectively (Fig. 4b). A substantial share of the observed increase in species density was contributed by species that showed a long-term positive or negative trend in the numbers of sites occupied, but without an apparent coupling to a known change in environmental conditions. This contribution amounted to +2.0 and −0.4 (net +1.6) species per 0.95 m2 (Fig. 4c). Taken together, the above-mentioned groups contributed 1.8 + 1.7 + 1.6 = 5.1 species per 0.95 m2, and this is close to the observed overall increase in species density of 5.2 species per 0.95 m2 (Table 1). Note that not just a few species accounted for the long-term changes in species density, but that more than half (27/50) of the studied species were in some way involved in the explanation of this increase. On the other hand, the one 9-species group of newcomers (including 4 truly exotic species and 5 showing only local range extension) could almost completely explain the observed increase in total species number.
The observed increases in macrozoobenthic species richness may not be limited to the westernmost part of the Wadden Sea. A recent survey of the macrozoobenthos of the Wadden Sea (Van der Graaf et al. 2009) indicates increasing trends of species numbers at all 3 sites (Balgzand, Groninger Wad, Norderney) that were continuously sampled ever since the 1970s. However, as the authors rightly remark, part of these increases in species numbers will have been caused by methodological reasons (viz. the above-discussed improved species identification). In the north Frisian Wadden Sea near the island of Sylt, Reise et al. (1989) report increases in numbers of infauna species, particularly in polychaetes, between the 1930s and 1980s, resulting in enhanced numbers of species per 0.2 m2 (compare Figure 8b of Lotze 2005). Van der Graaf et al. (2009) could not confirm a suggested “polychaete take-over”. In the central western North Sea, a 33-y data series by Frid et al. (2009) revealed a significant increase in numbers of genera found per 0.5 m2 from ~100 in the 1970s to ~120 in the 1990s and early 2000s.
Though the trends in species richness may usually be upward, species losses have been reported from the Wadden Sea. The main causes of (local or total) species extinction in the Wadden Sea appear to be habitat change or destruction and exploitation (compare Figure 3 of Lotze et al. 2005). Several cases of habitat destruction were caused by fishery (Reise et al. 1989; Piersma et al. 2001), including disturbance of the upper bottom layer and complete removal of oyster and mussel banks. Mussel (and oyster) beds are usually richer in species than their surroundings, as these structures offer locally hard substrates to species that cannot live on the surrounding soft sediments (Buschbaum et al. 2009). The few sampling sites on Balgzand that usually included mussel beds showed higher species densities than other sites. The removal of all mussel beds in 1990 (Beukema and Cadée 1996) resulted in exceptionally low estimates of species richness at the next sampling occasion in early 1991 (see plus and multi points in Fig. 1c, d, 3b), but species richness and mussel numbers had largely recovered already by 1992, due to highly successful reproduction in many species (including mussels) in the summer of 1991.
As in other areas, part of the increasing species richness on Balgzand was due to invaders. In Wadden Sea invertebrates, the numbers of newly introduced species exceeded those of species that became extinct (compare Figure 2 of Lotze et al. 2005). No cases appear to be known of extinction caused by an invasive species in the Wadden Sea (Wolff 2000; Lotze et al. 2005) and examples of invaders reducing abundance of other species appear to be few. An example of such negative interaction may be the local declines of biomass of Nereis spec. and other species simultaneously with the rapid increase in biomass of Marenzelleria viridis after their introduction (Essink et al. 1998; Essink and Dekker 2002). Markert et al. (2010) and Troost (2010) found no indication of a suppression of indigenous species by the recent establishment of reefs of Pacific oysters Crassostrea gigas in the German and Dutch Wadden Sea, respectively.
A substantial part of the observed increase in species density could be attributed to the warming climate: the 10 winter-sensitive species (Fig. 2) became more abundant and were found at an increasing number of sampling sites (Table 1; Fig. 4a). Declines in numbers of occupied sites were observed in a few species, but these declines appeared to be unrelated to temperature change. A few species, notably the bivalve Macoma balthica do suffer from the warming climate and showed declining trends in abundance for recent decades (Beukema et al. 2009). So far, however, this did not result in declining numbers of sites were they were found. Thus, the long-term warming trends resulted in increasing species richness on the Balgzand tidal flats. This conclusion is in accordance with that of Hawkins et al. (2009) for British rocky-shore fauna, that more southern (warm-water) species have been recorded advancing than northern (cold-water) species retreating. A similar conclusion was reached by Sagarin et al. (1999) for the Californian rocky intertidal.
The two processes (invasions and advancement of species, mostly by climate change) that caused the increase in species richness on Balgzand tidal flats are still in progress and may be expected to continue. Immigration of alien species by a.o. transport in ballast water, attachment to ship hulls or to imported organisms (such as oysters) cannot completely be prevented. Brackish estuaries and other coastal areas appear to offer plenty of open niches for newcomers (Wolff 1999; Reise et al. 1999). Further spread of lower-latitude species into a poleward direction (in fact largely a re-colonization process ever since the Ice Ages) will rapidly continue as long as global warming continues. So far, there are no signs of extirpation of species in the study area as a consequence of warming. Warming promoted the distribution of winter-sensitive species that were already present in the area. Occasional cold winters caused an immediate but temporary reduction in species number and species density, but recovery went rapidly. In conclusion, we expect further increases in species numbers and species-density values from all processes underlying the observed increase in species richness.
This study is part of a long-term monitoring program on macrozoobenthos in the Wadden Sea executed by NIOZ and financially supported by the Dutch Ministry of Transport, Public Works and Water Management, Water Service (RWS-Waterdienst).
This article is distributed under the terms of the Creative Commons Attribution Noncommercial License which permits any noncommercial use, distribution, and reproduction in any medium, provided the original author(s) and source are credited.
- Asakura A, Watanabe S (2005) Hemigrapsus takanoi, new species, a sibling species of the common Japanese intertidal crab H. penicillatus (Decapoda: Brachyura: Grapsoidea). J Crust Biol 25:279–292View ArticleGoogle Scholar
- Beukema JJ (1976) Biomass and species richness of the macrobenthic animals living on the tidal flats of the Dutch Wadden Sea. Neth J Sea Res 10:236–261View ArticleGoogle Scholar
- Beukema JJ (1979) Biomass and species richness of the macrobenthic animals living on a tidal flat area in the Dutch Wadden Sea: effects of a severe winter. Neth J Sea Res 13:203–223View ArticleGoogle Scholar
- Beukema JJ (1985) Zoobenthos survival during severe winters on high and low tidal flats in the Dutch Wadden Sea. In: Gray JS, Christiansen ME (eds) Marine biology of polar regions and effects of stress on marine organisms. Wiley, Chichester, pp 351–361Google Scholar
- Beukema JJ (1990) Expected effects of changes in winter temperatures on benthic animals living in soft sediments in coastal North Sea areas. In: Beukema JJ, Wolff WJ, Brouns JJWM (eds) Expected effects of climatic change on marine coastal ecosystems. Kluwer, Dordrecht, pp 83–92Google Scholar
- Beukema JJ (1992) Expected changes in the Wadden Sea benthos in a warmer world: lessons from periods with mild winters. Neth J Sea Res 30:73–79View ArticleGoogle Scholar
- Beukema JJ (1993) Increased mortality in alternative bivalve prey during a period when the tidal flats of the Dutch Wadden Sea were devoid of mussels. Neth J Sea Res 31:395–406View ArticleGoogle Scholar
- Beukema JJ, Cadée GC (1996) Consequences of the sudden removal of nearly all mussels and cockles from the Dutch Wadden Sea. PSZN: Mar Ecol 17:279–289View ArticleGoogle Scholar
- Beukema JJ, Cadée GC (1997) Local differences on macrozoobenthic response to enhanced food supply caused by mild eutrophication in a Wadden Sea area: food is only locally a limiting factor. Limnol Oceanogr 42:1424–1435View ArticleGoogle Scholar
- Beukema JJ, Dekker R (1995) Dynamics and growth of a recent invader into European coastal waters: the American razor clam, Ensis directus. J Mar Biol Ass UK 75:351–362View ArticleGoogle Scholar
- Beukema JJ, Dekker R, Jansen JM (2009) Some like it cold: populations of the tellinid bivalve Macoma balthica (L.) suffer in various ways from a warming climate. Mar Ecol Prog Ser 384:135–145View ArticleGoogle Scholar
- Buschbaum C et al (2009) Mytilid mussels: global habitat engineers in coastal sediments. Helgol Mar Res 63:47–58View ArticleGoogle Scholar
- Essink K (1999) Dispersal and development of Marenzelleria spp. (Polychaeta, Spionidae) populations in NW Europe and The Netherlands. Helgol Meeresunters 52:367–372View ArticleGoogle Scholar
- Essink K, Dekker R (2002) General patterns in invasive ecology tested in the Dutch Wadden Sea: the case of a brackish-marine polychaetous worm. Biol Invasions 4:359–368View ArticleGoogle Scholar
- Essink K, Eppinga J, Dekker R (1998) Long-term changes (1977–1994) in intertidal macozoobenthos of the Dollard (Ems estuary) and effects of introduction of the North American spionid polychaete Marenzelleria cf. wireni. Senckenb Marit 28:211–225View ArticleGoogle Scholar
- Frid CLJ, Garwood PR, Robinson LA (2009) Observing change in a North Sea benthic system: a 33 year time series. J Mar Syst 77:227–236View ArticleGoogle Scholar
- Gollasch S (1999) The Asian decapod Hemigrapsus penicillatus (De Haan, 1835) (Grapsidae, Decapoda) introduced in European waters: status quo and future perspective. Helgol Meeresunters 52:359–366View ArticleGoogle Scholar
- Hawkins SJ et al (2009) Consequences of climate-driven biodiversity changes for ecosystems functioning of North European rocky shores. Mar Ecol Prog Ser 396:245–259View ArticleGoogle Scholar
- Lotze HK (2005) Radical changes in the Wadden Sea fauna and flora over the last 2,000 years. Helgol Mar Res 59:71–83View ArticleGoogle Scholar
- Lotze HK et al (2005) Human transformations of the Wadden Sea ecosystem through time: a synthesis. Helgol Mar Res 59:84–95View ArticleGoogle Scholar
- Markert A, Wehrmann A, Kröncke I (2010) Recently established Crassostrea-reefs versus native Mytilus-beds: differences in ecosystem engineering affects the macrofaunal communities (Wadden Sea of Lower Saxony, southern German Bight). Biol Invasions 12:15–32View ArticleGoogle Scholar
- Petersen et al. (1996) Red list of macrofaunal benthic invertebrates of the Wadden Sea. Helgol Meeresunters 50(suppl.):69–76Google Scholar
- Piersma T, Koolhaas A, Dekinga A, Beukema JJ, Dekker R, Essink K (2001) Long-term indirect effects of mechanical cockle-dredging on intertidal bivalve stocks in the Wadden Sea. J Appl Ecol 38:976–990View ArticleGoogle Scholar
- Reise K, Herre E, Sturm M (1989) Historical changes in the benthos of the Wadden Sea around the island of Sylt in the North Sea. Helgol Meeresunters 43:417–433View ArticleGoogle Scholar
- Reise K, Gollasch S, Wolff WJ (1999) Introduced marine species of the North Sea coasts. Helgol Meeresunters 52:219–234View ArticleGoogle Scholar
- Sagarin RD, Barry JP, Gilman SE, Baxter CH (1999) Climate-related change in an intertidal community over short and long time scales. Ecol Monogr 69:465–490View ArticleGoogle Scholar
- Sikorski AV, Bick A (2004) Revision of Marenzelleria Mesnil, 1896 (Spionidae, Polychaeta). Sarsia 89:253–275View ArticleGoogle Scholar
- Troost K (2010) Causes and effects of a highly successful marine invasion: case-study of the introduced Pacific oyster Crassostrea gigas in continental NW European estuaries. J Sea Res (in press)Google Scholar
- Van Aken HM (2008) Variability of the water temperature in the western Wadden Sea on tidal to centennial scales. J Sea Res 60:227–234View ArticleGoogle Scholar
- Van Aken HM (2010) Meteorological forcing of long-term temperature variations of the Dutch coastal waters. J Sea Res 63:143–151View ArticleGoogle Scholar
- Van der Graaf S, De Vlas J, Herlyn M, Voss J, Heyer K, Drent J (2009) Macrozoobenthos. Thematic report no. 10. In: Marencic H, De Vlas J (eds) Quality status report 2009. Wadden Sea Ecosystems No. 25. Common Wadden Sea Secretariat, WilhelmshavenGoogle Scholar
- Von Cosel R (2009) The razor shells of the eastern Atlantic, part 2. Pharidae II: the genus Ensis Schumacher, 1817 (Bivalvia, Solenoidea). Basteria 73:9–56Google Scholar
- Wolff WJ (1999) Exotic invaders of the meso-oligohaline zone of estuaries in the Netherlands: why are there so many? Helgol Meeresunters 52:393–400View ArticleGoogle Scholar
- Wolff WJ (2000) Causes of extirpation in the Wadden Sea, an estuarine area in the Netherlands. Conserv Biol 14:876–885View ArticleGoogle Scholar
- Wolff WJ (2005) Non-indigenous marine and estuarine species in The Netherlands. Zool Meded Leiden 79(1):1–116Google Scholar
- Wolff WJ, Dankers N (1981) Preliminary checklist of the zoobenthos and nekton species of the Wadden Sea. In: Wolff WJ (ed) Ecology of the Wadden Sea Balkema, Rotterdam 1(4):24–60Google Scholar