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28 June 2011 Overview: the links that bind aquatic ecosystems
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Abstract

Aquatic research historically has focused on separate aquatic ecosystems (i.e., freshwater, estuarine, and marine). We argue that this separation into subdisciplines is artificial and may even be counterproductive. Instead, scientists should consider the physical linkages between different aquatic ecosystems and the many similarities in properties and processes among those ecosystems (conceptual linkages). The 4 papers in this J-NABS BRIDGES cluster demonstrate the value of integrating information from different aquatic ecosystems. For example, the papers illustrate that transformation and transportation of nutrients and energy physically and conceptually link all aquatic ecosystems and are facilitated by the characteristics of the medium that defines them all—water. To promote the exchange of information within aquatic science, more interecosystem studies should be published in journals and books so that scientists will see parallels and linkages among freshwater, estuarine, and marine systems. Over the longer term, such studies would benefit from the funding and teaching of aquatic science as an integrated whole.

Freshwater, estuarine, and marine ecosystems are linked by the medium that defines them all—water. Historically, the different subdisciplines of aquatic science have developed independently. This separation has been reinforced by obvious differences in organisms, chemical composition, and the size of the aquatic ecosystem studied (Dobson and Frid 1998). Broader integration of research from different aquatic ecosystems has been limited despite the enormous growth of knowledge over the last 50 y. Aquatic scientists are aware of the connections or linkages between aquatic ecosystems, and cross- or interecosystem studies have been published in journals (e.g., Hecky and Kilham 1988, Amon and Benner 1996, Elser et al. 2007) and books (e.g., Maser and Sedell 1994, Wotton 1994, Dobson and Frid 1998). However, the presence of such linkages is not reflected more generally in published aquatic research, which remains largely separated by subdiscipline.

The titles and contents of many aquatic journals (e.g., Freshwater Biology, Marine Ecology Progress Series, River Research and Applications) suggest lack of integration within aquatic science. For example, Lamberti et al. (2010) found that >75% of articles published in J-NABS were concerned exclusively with fresh waters. Furthermore, an evaluation of 50 of the most-cited and of the most recently published J-NABS papers indicated that ≤7%, on average, of the citations in those articles were to marine or estuarine journals or to journals more broadly aquatic in their subject matter (Table 1). The freshwater benthos is the publication niche for J-NABS, so a predominance of freshwater studies is not surprising. Furthermore, a freshwater focus is appropriate for some research topics, such as stream restoration, to which the contribution of marine and estuarine research is likely to be limited. However, the predominance of freshwater citations suggests little consideration of research from estuaries, marine coasts, and oceans or that researchers in these ecosystems do not consider J-NABS as a publication outlet for their work. The lack of integration in journals reflects the current separation and arguably reinforces the continued separation of research in freshwater and marine ecosystems.

Table 1

Summary of citations given in J-NABS publications, either in the 50 most-cited (1988–2002) or 50 most recently published (2009–2010). Citations were categorized according to the aquatic ecosystem or combination of ecosystems that were studied.

i0887-3593-30-3-751-t01.tif

Our central argument is that aquatic science would benefit from better integration of knowledge from all types of water bodies. Given the technological advances that facilitate the acquisition, analysis, and sharing of information, more integration of research from aquatic subdisciplines seems a reasonable expectation. Such interecosystem studies also require a more holistic view of aquatic science in which different water bodies are studied comparatively to reflect similarities in properties and processes among those ecosystems (conceptual linkages) and, as broadly as practical, to reflect physical linkages among aquatic ecosystems. Such interecosystem studies reveal important similarities and differences and allow the establishment of general frameworks from which further hypotheses are generated.

Interecosystem studies that have been published provide important insights into many different aspects of aquatic ecosystems. A summary of these studies (Table 2) shows that their authors considered a variety of aquatic organisms (e.g., viruses, bacteria, algae, fish), processes (e.g., denitrification, respiration), physicochemical factors (e.g., ultraviolet light, nutrient availability), and materials (e.g., particulate organic matter, dissolved organic matter). The studies were focused generally on ecosystem structure (e.g., species composition) over function (e.g., respiration) and usually on lower (e.g., viruses, bacteria, algae) rather than higher trophic levels (e.g., invertebrates, fish). The few studies of ecosystem function addressed nutrient cycling (e.g., nutrient limitation) rather than energy flow (e.g., C sources). Most interecosystem studies were focused exclusively on the pelagic habitat (60%), and fewer considered the benthic (16%) or both the pelagic and benthic (24%) habitats. Most studies compared freshwater and marine ecosystems (64%), whereas the remainder of the studies (36%) also included estuarine ecosystems in their comparisons. Published information, either as literature surveys or, most recently, in meta-analyses was used in ∼½ of the studies, whereas new data were generated from experimental manipulations or field sampling, often complemented by literature surveys, in the other ½. Not surprisingly, the explicitly cross-ecosystem journal Limnology and Oceanography has published the most interecosystem studies (34% of articles considered), whereas the other journals, including J-NABS, have published far fewer (<8%).

Table 2

Summary of interecosystem publications. Ecosystem (Ecosys) abbreviations: E  =  estuarine, F  =  freshwater, M  =  marine; habitat abbreviations: P  =  pelagic, B  =  benthic; method abbreviations: E  =  experimental, LS  =  literature survey, MA  =  meta-analysis, S  =  sampling; conclusion (Con) abbreviations: D  =  differences, S  =  similarities. DOM  =  dissolved organic matter, POM  =  particulate organic matter.

i0887-3593-30-3-751-t02.tif

Interecosystem studies published to date highlight several important features of aquatic ecosystems. First, similarities among aquatic ecosystems (40%) are almost as evident as differences (46%); the remaining 14% found both similarities and differences in the same study. Similarities include the effects of light (Sommaruga et al. 1997, Bancroft et al. 2007) and nutrient limitation (e.g., Guildford and Hecky 2000, Elser et al. 2007) on aquatic organisms. Second, differences that exist between aquatic ecosystems appear to reflect the local environmental context, such as water movement and sediment composition (e.g., Mermillod-Blondin and Rosenberg 2006), nutrient concentrations (e.g., Guildford and Hecky 2000, Elser et al. 2007), and C sources (e.g., Baines and Pace 1991, Amon and Benner 1996), rather than just the more obvious differences among ecosystems in organisms, salinity, or size (e.g., Seitzinger et al. 1991). Third, many areas of aquatic science have not been considered from an interecosystem perspective. Examples of where an interecosystem comparison would be worthwhile include invertebrate functional groupings, allochthonous vs autochthonous inputs, and a comparison of structural and functional metrics.

The papers in this BRIDGES cluster demonstrate the benefits of a broader integration of research from different aquatic ecosystems. Collectively, Mermillod-Blondin (2011), Petticrew et al. (2011), and Wotton (2011) describe how diverse aquatic organisms (e.g., microorganisms, oligochaetes, polychaetes, insects, gastropods, and fish) and their products (e.g., tubes, burrows, feces, mucus, silk, chitin, carcasses, and dissolved organic matter) influence the nutrient and energy fluxes within and between aquatic ecosystems. Articles in this BRIDGES cluster also demonstrate that ecological similarities among disparate aquatic ecosystems are equal to and can be larger than the differences, as others have argued (e.g., Dobson and Frid 1998). For example, Mermillod-Blondin (2011) makes a compelling case for considering the role of water flow in both freshwater and marine ecosystems (cf. Legendre and Demers 1984). Wotton (2011) stresses the importance of exudates to aquatic biota and their role in the dynamics of organic matter in all water bodies. Articles in this BRIDGES cluster also illustrate how aquatic ecosystems, in general, are replete with physical and conceptual linkages, all underpinned by the presence of water. Highlighted physical linkages include the movement of organic matter within, and between different water bodies (Petticrew et al. 2011, Wotton 2011) and conceptual linkages include the role of environmental context (Mermillod-Blondin 2011, Petticrew et al. 2011). Water facilitates linkages among aquatic systems by virtue of its physical and chemical characteristics, such as high specific-heat capacity, the nonlinear relationship between its density and temperature, high viscosity, and capacity to dissolve more substances than any other liquid (Dobson and Frid 1998). These characteristics and the aquatic organisms that have evolved in response to them influence the capacity of aquatic ecosystems to transport and transform nutrients and energy.

Water provides an exceptional transportation system because it is a universal solvent and has high viscosity. As a universal solvent, water dissolves many substances and holds them in solution wherever they are carried. The high viscosity of water facilitates passive and active movement of aquatic organisms and their products (Mermillod-Blondin 2011, Petticrew et al. 2011, Wotton 2011). Thus, water is an effective delivery system of dissolved and particulate matter via currents that organisms generate and currents that already exist. One consequence is that suspension feeders are present in all aquatic ecosystems (Wotton 1994, Dobson and Frid 1998). Movements of organisms and their products, in turn, constitute important linkages within and between aquatic ecosystems. Examples include benthic–pelagic coupling (e.g., Blumenshine et al. 1997), upstream–downstream (e.g., Mulholland et al. 1995) and surface–subsurface connections (e.g., Valett et al. 1997), and movements between aquatic ecosystems (e.g., Chaloner et al. 2004). Mermillod-Blondin (2011) and Wotton (2011) provide examples of how organisms facilitate benthic–pelagic linkages, which have been neglected by some branches of aquatic research (Lamberti et al. 2010) and certainly have yet to be compared among ecosystems.

The physicochemical characteristics of water and the actions of organisms also facilitate the transformation of material. Examples include the generation of flocs, or ‘snow’, from dissolved organic matter resulting from chemical, physical, and biological processes (Wotton 2011). Consumers also transform organic material by compacting egested material into fecal pellets that sink to form biodeposits (Mermillod-Blondin 2011) or are carried away by currents (Wotton 2011). In addition, aquatic organisms create biogenic structures from organic and inorganic material and act as ecosystem engineers (e.g., Mermillod-Blondin and Rosenberg 2006). Such transformations can have profound effects on the pelagic and benthic environment (Mermillod-Blondin 2011, Petticrew et al. 2011, Wotton 2011). Producers and consumers release compounds directly into the surrounding water (Petticrew et al. 2011, Wotton 2011) where these exudates are transformed or metabolized, often rapidly, by other organisms (e.g., Baines and Pace 1991, Amon and Benner 1996, Malinsky-Rushansky and Legrand 1996). Such transformations are facilitated by interfaces that are abundant in all aquatic ecosystems (Naiman et al. 1988), especially those between sediments and overlying water (Mermillod-Blondin 2011, Petticrew et al. 2011, Wotton 2011). Organisms and resources are brought together at these interfaces for important biogeochemical transformations.

Some aquatic organisms can facilitate both the transport and transformation of material among systems. Pacific salmon (Oncorhynchus spp.) provide one such example (Petticrew et al. 2011). Salmon transport nutrients and energy as they migrate from the ocean via estuaries to fresh waters where they spawn and die. The marine-derived nutrients they deliver as carcasses, gametes, and excretory products are an important ecosystem resource subsidy (Polis et al. 2004) that increases growth and abundance of freshwater producers and consumers (e.g., Chaloner and Wipfli 2002, Chaloner et al. 2004). Salmon spawners also act as ecosystem engineers (Wright and Jones 2006) by constructing redds or nests, which transform sediment size and topography and alter biofilm and invertebrate abundance (e.g., Moore et al. 2004). A considerable amount research has accumulated about the ecology of Pacific salmon (see Quinn 2005), but a comprehensive interecosystem study of their ecological role has yet to be done.

Interecosystem studies suggest that information must be integrated at contrasting spatial and temporal scales. For example, microorganisms use exudates and particles aggregate and fragment at smaller scales (i.e., µm–m, s–d), whereas water currents move particles over large distances and at larger time scales (i.e., km–103 km, days to 10 y) (Wotton 2011). Similarly, the construction of biogenic structures by invertebrates (Mermillod-Blondin 2011) occurs over small spatial and temporal scales but may modify substratum characteristics that persist over larger scales. Last, disturbance associated with salmon spawning redds occurs at smaller spatial scales and persists for limited time (Petticrew et al. 2011), whereas salmon migrations take place over larger scales. Also, the nutrient-enrichment effects of salmon carcasses occur downstream, in adjacent riparian and hyporheic habitats, and as carryover effects beyond the salmon run and into the subsequent year. The role of organisms in the transformation and transportation of organic material should be compared among aquatic ecosystems. For example, the extent to which egestion, excretion, construction, and bioturbation influence the quality and quantity of material present should be determined by using functional groupings (Mermillod-Blondin 2011). The significance of such activities may be indicated by the abundance or diet of organisms. Last, the role of environmental context in the similarities, differences, and linkages among aquatic ecosystems should be considered (Mermillod-Blondin 2011, Petticrew et al. 2011, Wotton 2011).

Several broader recommendations to encourage a more holistic, integrated approach to aquatic research are evident from this BRIDGES cluster. Recommendations have been made for interdisciplinary research (Committee on Inland Aquatic Ecosystems 1996, National Academies 2004, Lamberti et al. 2010), but we make recommendations specifically for interecosystem studies in aquatic science. Such recommendations extend beyond academic institutions to professional societies, publishers, and funding agencies involved in aquatic research.

Academic institutions should encourage interecosystem research in the aquatic sciences. Organizations exist to assist with such endeavors. These organizations include the National Center for Ecological Analysis and Synthesis (NCEAS;  www.nceas.ucsb.edu/; Andelman et al. 2004), and the John Wesley Powell Center for Analysis and Synthesis (US Geological Survey; powellcenter.usgs.gov/). Such efforts are part of a larger interdisciplinary movement to facilitate the synthesis of data (Parr and Cummings 2005). NCEAS encourages use of existing data to address major issues in ecology and, in so doing, encourages application of science to management and policy issues. NCEAS argues that it can influence how science is conducted and facilitate understanding by fostering the collaborations and data sharing that enables the synthesis and analysis of scientific information, a view that is in line with our central argument. Specific interecosystem studies have benefited from the NCEAS (Shurin et al. 2002, Elser et al. 2007), and these studies have had a significant effect (Table 2). Still, the usefulness of such an approach depends, in part, upon the research questions being asked.

The scientific community should encourage research questions that embrace different aquatic ecosystems. Such questions should include the role of scale because many phenomena can exist over different spatial and temporal scales. For example, use of dissolved organic matter takes place at exceptionally small scales, whereas movement of nutrients and energy can occur at much larger spatial and temporal scales. Such questions also should extend beyond the identities and feeding strategies of organisms, whether consumers or predators, to consider them as transporters and transformers of nutrients and energy (i.e., organisms are important not just because of what they eat, but what they excrete, egest, and build). Arguably, studies involving functional feeding groups (Cummins 1974) and stoichiometry (Elser et al. 2000) have encouraged the perspective reflected in the content of this cluster of BRIDGES papers. Generation of new data, or integration of existing information, could further facilitate such comparative studies in aquatic science.

Data generation and integration needed for interecosystem studies are realistic goals given the availability and reduced cost of techniques for producing (e.g., compound separation and characterization) and analyzing (e.g., Geographical Information Systems) such data, especially at larger and smaller scales. Powerful database tools (e.g., Web of Science™) allow relevant literature to be found and analyzed more easily. Such analyses require new modeling and statistical approaches (Hobbs and Hilborn 2006), including meta-analysis tools that enable analysis of data from several independent studies as one data set (Gurevitch et al. 2001). Meta-analysis already has provided important insights in ecology and especially interecosystem research (Hillebrand 2002, 2009, Piña-Ochoa and Álvarez-Cobelas 2006, Bancroft et al. 2007, Elser et al. 2007). Such tools will only be used to generate new data if aquatic scientists are trained in their use and application.

Broader-based programs are needed to train aquatic scientists. The compelling argument made by Wetzel (1996) for broader training in limnology is appropriate for aquatic science in general. However, underlying philosophies differ among subdisciplines of aquatic science. Dobson and Frid (1998) remarked that scientists in different aquatic subdisciplines often use different terms for the same thing and the same terms for different things. For example, collector-gatherers (freshwater biology; Cummins 1974) and deposit feeders (marine biology; Dobson and Frid 1998) have the same feeding method. In contrast, littoral zone refers to the ‘illuminated shallows’ in freshwater biology and to the intertidal in marine biology (Dobson and Frid 1998). Broader training of aquatic biologists and the publication of interecosystem studies and books with a broader aquatic perspective (Maser and Sedell 1994, Wotton 1994, Dobson and Frid 1998) would help reconcile these contrasts in philosophies and terminology.

Journal editors, especially those of journals with broad scope (e.g., J-NABS) should encourage publication of interecosystem aquatic research, a call already made by others (e.g., Lamberti et al. 2010). Individuals with research experience in several ecosystems could be included on editorial boards, and special issues concerned with such research could be created. Many journals publish special issues (e.g., Danovaro et al. 2008) or have developed sections (e.g., J-NABS BRIDGES) in which the existence and importance of interecosystem research can be highlighted. However, peer review of such manuscripts will require recruitment of referees with broad experience and knowledge of aquatic science.

Many important physical and conceptual linkages among aquatic ecosystems exist because water defines them all. We think integration of research across aquatic ecosystems is important, realistic, and has much potential. However, many gaps exist in our knowledge, and the success of the kind of holistic research needed to fill those gaps depends upon the involvement and support of the entire community of aquatic scientists.

BRIDGES is a recurring feature of J-NABS intended to provide a forum for the interchange of ideas and information relevant to J-NABS readers, but beyond the usual scope of a scientific paper. Articles in this series will bridge from aquatic ecology to other disciplines, e.g., political science, economics, education, chemistry, or other biological sciences. Papers may be complementary or take alternative viewpoints. Authors with ideas for topics should contact Associate Editors Ashley Moerke and Allison Roy.

Ashley Moerke, amoerke@lssu.edu

Allison Roy, roy@kutztown.edu

Co-editors

Acknowledgments

We thank Ashley Moerke and Allison Roy, Co-editors of BRIDGES, for their support while this manuscript was being written. David Janetski, Janine Rüegg, Allison Roy, and 2 anonymous referees provided valuable feedback that improved the manuscript. DTC was supported by the Great Lakes Fishery Trust (Project 2007.857). DTC dedicates this paper to John P. Caouette, a friend and research collaborator, who died tragically in October 2010. A statistician by training, John was holistic in his approach to science and always sought a genuine dialogue with those outside his area of expertise.

Literature Cited

1.

R. M. W. Amon and R. Benner . 1996. Bacterial utilization of different size classes of dissolved organic matter. Limnology and Oceanography 41:41–51. Google Scholar

2.

S. J. Andelman, C. M. Bowles, M. R. Willig, and R. B. Waide . 2004. Understanding environmental complexity through a distributed knowledge network. BioScience 54:240–246. Google Scholar

3.

S. B. Baines and M. L. Pace . 1991. The production of dissolved organic matter by phytoplankton and its importance to bacteria: patterns across marine and freshwater systems. Limnology and Oceanography 36:1078–1090. Google Scholar

4.

S. B. Baines, M. L. Pace, and D. M. Karl . 1994. Why does the relationship between sinking flux and planktonic primary production differ between lakes and oceans? Limnology and Oceanography 39:213–226. Google Scholar

5.

B. A. Bancroft, N. J. Baker, and A. R. Blaustein . 2007. Effects of UVB radiation on marine and freshwater organisms: a synthesis through meta-analysis. Ecology Letters 10:332–345. Google Scholar

6.

T. Bell and J. Kalff . 2001. The contribution of picophytoplankton in marine and freshwater systems of different trophic status and depth. Limnology and Oceanography 46:1243–1248. Google Scholar

7.

D. F. Bird and J. Kalff . 1984. Empirical relationships between bacterial abundance and chlorophyll concentration in fresh and marine waters. Canadian Journal of Fisheries and Aquatic Sciences 41:1015–1023. Google Scholar

8.

S. C. Blumenshine, Y. Vadeboncoeur, D. M. Lodge, K. L. Cottingham, and S. E. Knight . 1997. Benthic–pelagic links: responses of benthos to water-column nutrient enrichment. Journal of the North American Benthological Society 16:466–479. Google Scholar

9.

D. T. Chaloner, G. A. Lamberti, R. W. Merritt, N. L. Mitchell, P. H. Ostrom, and M. S. Wipfli . 2004. Variation in responses to spawning Pacific salmon among three south-eastern Alaska streams. Freshwater Biology 49:587–599. Google Scholar

10.

D. T. Chaloner and M. S. Wipfli . 2002. Influence of decomposing Pacific salmon carcasses on macroinvertebrate growth and standing stock in southeastern Alaska streams. Journal of the North American Benthological Society 21:430–442. Google Scholar

11.

Committee on Inland Aquatic Ecosystems (Editor) 1996. Freshwater ecosystems: revitalizing educational programs in limnology. National Academy Press. Washington, DC. Google Scholar

12.

K. W. Cummins 1974. Structure and function of stream ecosystems. BioScience 24:631–641. Google Scholar

13.

R. Danovaro, C. Corinaldesi, M. Filippini, U. R. Fischer, M. O. Gessner, S. Jacquet, M. Magagnini, and B. Velimirov . 2008. Viriobenthos in freshwater and marine sediments: a review. Freshwater Biology 53:1186–1213. Google Scholar

14.

P. A. del Giorgio, J. J. Cole, and A. Cimbleris . 1997. Respiration rates in bacteria exceed phytoplankton production in unproductive aquatic systems. Nature 385:148–151. Google Scholar

15.

P. A. del Giorgio and R. L. France . 1996. Ecosystem-specific patterns in the relationship between zooplankton and POM or microplankton δ13C. Limnology and Oceanography 41:359–365. Google Scholar

16.

P. A. del Giorgio and G. Scarborough . 1995. Increase in the proportion of metabolically active bacteria along gradients of enrichment in freshwater and marine plankton: implications for estimates of bacterial growth and production rates. Journal of Plankton Research 17:1905–1924. Google Scholar

17.

W. R. DeMott 1988. Discrimination between algae and artificial particles by freshwater and marine copepods. Limnology and Oceanography 33:397–408. Google Scholar

18.

M. Dobson and C. Frid . 1998. Ecology of aquatic systems. Addison Wesley Longman. Harlow, UK. Google Scholar

19.

J. J. Elser, M. E. S. Bracken, E. E. Cleland, D. S. Gruner, W. S. Harpole, H. Hillebrand, J. T. Ngai, E. W. Seabloom, J. B. Shurin, and J. E. Smith . 2007. Global analysis of nitrogen and phosphorus limitation of primary producers in freshwater, marine and terrestrial ecosystems. Ecology Letters 10:1135–1142. Google Scholar

20.

J. J. Elser and R. P. Hassett . 1994. A stoichiometric analysis of the zooplankton-phytoplankton interaction in marine and freshwater ecosystems. Nature 370:211–213. Google Scholar

21.

J. J. Elser, L. B. Stabler, and R. P. Hassett . 1995. Nutrient limitation of bacterial growth and rates of bacterivory in lakes and oceans: a comparative study. Aquatic Microbial Ecology 9:105–110. Google Scholar

22.

J. J. Elser, R. W. Sterner, E. Gorokhova, W. F. Fagan, T. A. Markow, J. B. Cotner, J. F. Harrison, S. E. Hobbie, G. M. Odell, and L. J. Weider . 2000. Biological stoichiometry from genes to ecosystems. Ecology Letters 3:540–550. Google Scholar

23.

M. Filippini and M. Middelboe . 2007. Viral abundance and genome size distribution in the sediment and water column of marine and freshwater ecosystems. FEMS Microbiology Ecology 60:397–410. Google Scholar

24.

F. O. Glöckner, B. M. Fuchs, and R. Amann . 1999. Bacterioplankton compositions of lakes and oceans: a first comparison based on fluorescence in situ hybridization. Applied and Environmental Microbiology 65:3721–3726. Google Scholar

25.

S. J. Guildford and R. E. Hecky . 2000. Total nitrogen, total phosphorus, and nutrient limitation in lakes and oceans: is there a common relationship? Limnology and Oceanography 45:1213–1223. Google Scholar

26.

J. Gurevitch, P. S. Curtis, and M. H. Jones . 2001. Meta-analysis in ecology. Advances in Ecological Research 32:199–247. Google Scholar

27.

R. P. Hassett, B. Cardinale, L. B. Stabler, and J. J. Elser . 1997. Ecological stoichiometry of N and P in pelagic ecosystems: comparison of lakes and oceans with emphasis on the zooplankton-phytoplankton interaction. Limnology and Oceanography 42:648–662. Google Scholar

28.

K. E. Havens, J. Hauxwell, A. C. Tyler, S. Thomas, K. J. McGlathery, J. Cebrian, I. Valiela, A. D. Steinman, and S. J. Hwang . 2001. Complex interactions between autotrophs in shallow marine and freshwater ecosystems: implications for community responses to nutrient stress. Environmental Pollution 113:95–107. Google Scholar

29.

R. E. Hecky, P. Campbell, and L. L. Hendzel . 1993. The stoichiometry of carbon, nitrogen, and phosphorus in particulate matter of lakes and oceans. Limnology and Oceanography 38:709–724. Google Scholar

30.

R. E. Hecky and P. Kilham . 1988. Nutrient limitation of phytoplankton in freshwater and marine environments: a review of recent evidence on the effects of enrichment. Limnology and Oceanography 33:796–822. Google Scholar

31.

H. Hillebrand 2002. Top-down versus bottom-up control of autotrophic biomass: a meta-analysis on experiments with periphyton. Journal of the North American Benthological Society 21:349–369. Google Scholar

32.

H. Hillebrand 2009. Meta-analysis of grazer control of periphyton biomass across aquatic ecosystems. Journal of Phycology 45:798–806. Google Scholar

33.

H. Hillebrand, D. S. Gruner, E. T. Borer, M. E. S. Bracken, E. E. Cleland, J. J. Elser, W. S. Harpole, J. T. Ngai, E. W. Seabloom, J. B. Shurin, and J. E. Smith . 2007. Consumer versus resource control of producer diversity depends on ecosystem type and producer community structure. Proceedings of the National Academy of Sciences of the United States of America 104:10904–10909. Google Scholar

34.

N. T. Hobbs and R. Hilborn . 2006. Alternatives to statistical hypothesis testing in ecology: a guide to self teaching. Ecological Applications 16:5–19. Google Scholar

35.

P. Kilham and R. E. Hecky . 1988. Comparative ecology of marine and freshwater phytoplankton. Limnology and Oceanography 33:776–795. Google Scholar

36.

G. A. Lamberti, D. T. Chaloner, and A. E. Hershey . 2010. Linkages among aquatic ecosystems. Journal of North American Benthological Society 29:245–263. Google Scholar

37.

L. Legendre and S. Demers . 1984. Towards dynamic biological oceanography and limnology. Canadian Journal of Fisheries and Aquatic Sciences 41:2–19. Google Scholar

38.

N. Z. Malinsky-Rushansky and C. Legrand . 1996. Excretion of dissolved organic carbon by phytoplankton of different sizes and subsequent bacterial uptake. Marine Ecology Progress Series 132:249–255. Google Scholar

39.

R. Maranger and D. F. Bird . 1995. Viral abundance in aquatic systems: a comparison between marine and fresh waters. Marine Ecology Progress Series 121:217–226. Google Scholar

40.

C. Maser and J. Sedell . 1994. From the forest to the sea: the ecology of wood in streams, rivers, estuaries, and oceans. St Lucie Press. Delray Beach, Florida. Google Scholar

41.

M. L. Mei and R. Danovaro . 2004. Virus production and life strategies in aquatic sediments. Limnology and Oceanography 49:459–470. Google Scholar

42.

F. Mermillod-Blondin 2011. The functional significance of bioturbation and biodeposition on biogeochemical processes at the water–sediment interface in freshwater and marine ecosystems. Journal of the North American Benthological Society 30:770–778. Google Scholar

43.

F. Mermillod-Blondin and R. Rosenberg . 2006. Ecosystem engineering: the impact of bioturbation on biogeochemical processes in marine and freshwater benthic habitats. Aquatic Sciences 68:434–442. Google Scholar

44.

B. A. Methé, W. D. Hiorns, and J. P. Zehr . 1998. Contrasts between marine and freshwater bacterial community composition: analyses of communities in Lake George and six other Adirondack lakes. Limnology and Oceanography 43:368–374. Google Scholar

45.

J. W. Moore, D. E. Schindler, and M. D. Scheuerell . 2004. Disturbance of freshwater habitats by anadromous salmon in Alaska. Oecologia (Berlin) 139:298–308. Google Scholar

46.

P. J. Mulholland, E. R. Marzolf, S. P. Hendricks, R. V. Wilkerson, and A. K. Baybayan . 1995. Longitudinal patterns of nutrient cycling and periphyton characteristics in streams: a test of upstream–downstream linkage. Journal of the North American Benthological Society 14:357–370. Google Scholar

47.

R. A. Myers, G. Mertz, and J. Bridson . 1997. Spatial scales of interannual recruitment variations of marine, anadromous, and freshwater fish. Canadian Journal of Fisheries and Aquatic Sciences 54:1400–1407. Google Scholar

48.

R. J. Naiman, H. Decamps, J. Pastor, and C. A. Johnston . 1988. The potential importance of boundaries of fluvial ecosystems. Journal of the North American Benthological Society 7:289–306. Google Scholar

49.

National Academies 2004. Facilitating interdisciplinary research. National Academy Press. Washington, DC. Google Scholar

50.

H. W. Paerl 1974. Bacterial uptake of dissolved organic matter in relation to detrital aggregation in marine and freshwater ecosystems. Limnology and Oceanography 19:966–972. Google Scholar

51.

H. W. Paerl 1975. Microbial attachment to particles in marine and freshwater ecosystems. Microbial Ecology 2:73–83. Google Scholar

52.

C. S. Parr and M. P. Cummings . 2005. Data sharing in ecology and evolution. Trends in Ecology and Evolution 20:362–363. Google Scholar

53.

E. L. Petticrew, J. F. Rex, and S. J. Albers . 2011. Bidirectional delivery of organic matter between freshwater and marine systems: an example from Pacific salmon streams. Journal of the North American Benthological Society 30:779–786. Google Scholar

54.

E. Piña-Ochoa and M. Álvarez-Cobelas . 2006. Denitrification in aquatic environments: a cross-system analysis. Biogeochemistry 81:111–130. Google Scholar

55.

2004. G. A. Polis, M. E. Power, and G. Huxel . Food webs at the landscape level. University of Chicago Press. Chicago, Illinois. Google Scholar

56.

P. B. Price and T. Sowers . 2004. Temperature dependence of metabolic rates for microbial growth, maintenance, and survival. Proceedings of the National Academy of Sciences of the United States of America 101:4631–4636. Google Scholar

57.

T. P. Quinn 2005. The behavior and ecology of Pacific salmon and trout. University of Washington Press. Seattle, Washington. Google Scholar

58.

W. S. Reeburgh and D. T. Heggie . 1977. Microbial methane consumption reactions and their effect on methane distributions in freshwater and marine environments. Limnology and Oceanography 22:1–9. Google Scholar

59.

D. J. Repeta, T. M. Quan, L. I. Aluwihare, and A. M. Accardi . 2002. Chemical characterization of high molecular weight dissolved organic matter in fresh and marine waters. Geochimica et Cosmochimica Acta 66:955–962. Google Scholar

60.

B. C. Sander and J. Kalff . 1993. Factors controlling bacterial production in marine and freshwater sediments. Microbial Ecology 26:79–99. Google Scholar

61.

R. W. Sanders, D. A. Caron, and U. G. Berninger . 1992. Relationships between bacteria and heterotrophic nanoplankton in marine and fresh waters: an inter-ecosystem comparison. Marine Ecology Progress Series 86:1–14. Google Scholar

62.

M. Schallenberg and J. Kalff . 1993. The ecology of sediment bacteria in lakes and comparisons with other aquatic ecosystems. Ecology 74:919–934. Google Scholar

63.

S. Seitzinger, J. A. Harrison, J. K. Böhlke, A. F. Bouwman, R. Lowrance, B. Peterson, C. Tobias, and G. Van Drecht . 2006. Denitrification across landscapes and waterscapes: a synthesis. Ecological Applications 16:2064–2090. Google Scholar

64.

S. P. Seitzinger, W. S. Gardner, and A. K. Spratt . 1991. The effect of salinity on ammonium sorption in aquatic sediments: implications for benthic nutrient recycling. Estuaries 14:167–174. Google Scholar

65.

J. B. Shurin, E. T. Borer, E. W. Seabloom, K. Anderson, C. A. Blanchette, B. Broitman, S. D. Cooper, and B. S. Halpern . 2002. A cross-ecosystem comparison of the strength of trophic cascades. Ecology Letters 5:785–791. Google Scholar

66.

M. Simon, H. P. Grossart, B. Schweitzer, and H. Ploug . 2002. Microbial ecology of organic aggregates in aquatic ecosystems. Aquatic Microbial Ecology 28:175–211. Google Scholar

67.

V. H. Smith 2006. Responses of estuarine and coastal marine phytoplankton to nitrogen and phosphorus enrichment. Limnology and Oceanography 51:377–384. Google Scholar

68.

R. Sommaruga, I. Obernosterer, G. J. Herndl, and R. Psenner . 1997. Inhibitory effect of solar radiation on thymidine and leucine incorporation by freshwater and marine bacterioplankton. Applied and Environmental Microbiology 63:4178–4184. Google Scholar

69.

U. Sommer and F. Sommer . 2006. Cladocerans versus copepods: the cause of contrasting top-down controls on freshwater and marine phytoplankton. Oecologia (Berlin) 147:183–194. Google Scholar

70.

R. W. Sterner, T. Andersen, J. J. Elser, D. O. Hessen, J. M. Hood, E. McCauley, and J. Urabe . 2008. Scale-dependent carbon∶nitrogen∶phosphorus seston stoichiometry in marine and freshwaters. Limnology and Oceanography 53:1169–1180. Google Scholar

71.

H. M. Valett, C. N. Dahm, M. E. Campana, J. A. Morrice, M. A. Baker, and C. S. Fellows . 1997. Hydrologic influences on groundwater surface water ecotones: heterogeneity in nutrient composition and retention. Journal of the North American Benthological Society 16:239–247. Google Scholar

72.

M. Ventura 2006. Linking biochemical and elemental composition in freshwater and marine crustacean zooplankton. Marine Ecology Progress Series 327:233–246. Google Scholar

73.

R. J. West and R. J. King . 1996. Marine, brackish, and freshwater fish communities in the vegetated and bare shallows of an Australian coastal river. Estuaries 19:31–41. Google Scholar

74.

R. G. Wetzel 1996. Training of aquatic ecosystem scientists. Pages 218–233 in Committee on Inland Aquatic Ecosystems (editors). Freshwater ecosystems: revitalizing educational programs in limnology. National Academy Press. Washington, DC. Google Scholar

75.

P. A. White, J. Kalff, J. B. Rasmussen, and J. M. Gasol . 1991. The effect of temperature and algal biomass on bacterial production and specific growth rate in freshwater and marine habitats. Microbial Ecology 21:99–118. Google Scholar

76.

1994. R. S. Wotton The biology of particles in aquatic systems. 2nd edition. Lewis Publishers/CRC Press. Boca Raton, Florida. Google Scholar

77.

R. S. Wotton 2011. EPS (Extracellular Polymeric Substances), silk, and chitin: vitally important exudates in aquatic ecosystems. Journal of the North American Benthological Society 30:762–769. Google Scholar

78.

J. P. Wright and C. G. Jones . 2006. The concept of organisms as ecosystem engineers ten years on: progress, limitations, and challenges. BioScience 56:203–209. Google Scholar

Notes

[1] BRIDGES is a recurring feature of J-NABS intended to provide a forum for the interchange of ideas and information relevant to J-NABS readers, but beyond the usual scope of a scientific paper. Articles in this series may integrate science into ecosystem management or bridge aquatic ecology to other disciplines, e.g., political science, economics, education, chemistry, or other biological sciences. Papers may be complementary or take alternative viewpoints. Authors with ideas for topics should contact Associate Editors Ashley Moerke and Allison Roy.

Ashley Moerke, amoerke@lssu.edu

Allison Roy, roy@kutztown.edu

Co-editors

Dominic T. Chaloner and Roger S. Wotton "Overview: the links that bind aquatic ecosystems," Journal of the North American Benthological Society 30(3), 751-761, (28 June 2011). https://doi.org/10.1899/10-125.1
Received: 15 September 2010; Accepted: 1 April 2011; Published: 28 June 2011
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