|Invasive mussels alter the littoral food web of a large lake: stable isotopes reveal drastic shifts in sources and flow of energy.|
|Jump to Full Text|
|PMID: 23284673 Owner: NLM Status: MEDLINE|
|We investigated how establishment of invasive dreissenid mussels impacted the structure and energy sources of the littoral benthic food web of a large temperate lake. We combined information about pre- and postdreissenid abundance, biomass, and secondary production of the littoral benthos with results of carbon and nitrogen stable isotope analysis of archival (predreissenid) and recent (postdreissenid) samples of all common benthic taxa. This approach enabled us to determine the importance of benthic and sestonic carbon to the littoral food web before, and more than a decade after dreissenid establishment. Long term dreissenid presence was associated with a 32-fold increase in abundance, 6-fold increase in biomass, and 14-fold increase in secondary production of the littoral benthos. Dreissenids comprised a large portion of the post-invasion benthos, making up 13, 38, and 56% of total abundance, biomass, and secondary production, respectively. The predreissenid food web was supported primarily by benthic primary production, while sestonic material was relatively more important to the postdreissenid food web. The absolute importance of both sestonic material and benthic primary production to the littoral benthos increased considerably following dreissenid establishment. Our results show drastic alterations to food web structure and suggest that dreissenid mussels redirect energy and material from the water column to the littoral benthos both through biodeposition of sestonic material as well as stimulation of benthic primary production.|
|Ted Ozersky; David O Evans; David R Barton|
Related Documents :
|24672503 - Exploring the factor structure of the food cravings questionnaire-trait in cuban adults.
23053223 - New parasites and predators follow the introduction of two fish species to a subarctic ...
12530783 - Stakeholder attitudes toward the risks and benefits of agricultural biotechnology in de...
|Type: Journal Article; Research Support, Non-U.S. Gov't Date: 2012-12-17|
|Title: PloS one Volume: 7 ISSN: 1932-6203 ISO Abbreviation: PLoS ONE Publication Date: 2012|
|Created Date: 2013-01-03 Completed Date: 2013-06-17 Revised Date: 2013-07-11|
Medline Journal Info:
|Nlm Unique ID: 101285081 Medline TA: PLoS One Country: United States|
|Languages: eng Pagination: e51249 Citation Subset: IM|
|Ontario Ministry of Natural Resources, Trent University, Peterborough, Ontario, Canada. firstname.lastname@example.org|
|APA/MLA Format Download EndNote Download BibTex|
Aquatic Organisms / metabolism*
Bivalvia / metabolism*
Isotopes / chemistry, metabolism
Journal ID (nlm-ta): PLoS One
Journal ID (iso-abbrev): PLoS ONE
Journal ID (publisher-id): plos
Journal ID (pmc): plosone
Publisher: Public Library of Science, San Francisco, USA
Copyright: 2012 Ozersky et al
Received Day: 4 Month: 1 Year: 2012
Accepted Day: 2 Month: 11 Year: 2012
collection publication date: Year: 2012
Electronic publication date: Day: 17 Month: 12 Year: 2012
Volume: 7 Issue: 12
E-location ID: e51249
PubMed Id: 23284673
Publisher Id: PONE-D-12-00457
|Invasive Mussels Alter the Littoral Food Web of a Large Lake: Stable Isotopes Reveal Drastic Shifts in Sources and Flow of Energy Alternate Title:Invasive Mussels Alter Food Web Structure|
|David O. Evans1|
|David R. Barton2|
|Luís A. Nunes Amaraledit1||
1Ontario Ministry of Natural Resources, Trent University, Peterborough, Ontario, Canada
2Department of Biology, University of Waterloo, Waterloo, Ontario, Canada
|Northwestern University, United States of America
|Correspondence: * E-mail: email@example.com
[conflict] Competing Interests: The authors have declared that no competing interests exist.
Contributed by footnote: Conceived and designed the experiments: TO DOE. Performed the experiments: TO DOE DRB. Analyzed the data: TO DOE DRB. Contributed reagents/materials/analysis tools: DOE DRB. Wrote the paper: TO DOE DRB.
¤Current address: Department of Biological Sciences, Wellesley College, Wellesley, Massachusetts, United States of America
The establishment of invasive organisms is a threat facing aquatic ecosystems world wide –. Among the most significant–but often most difficult to quantify–ecological impacts of species invasions are alterations to food web structure and energy flow patterns . Stable isotope analysis (SIA) of carbon and nitrogen in constituents of the food web offers a way to untangle the complex effects of species invasions and other perturbations on the trophic structure of ecosystems. Carbon isotope ratios are generally conserved between food sources and consumers, so 13C/12C ratios can be used to determine the contribution of different energy sources to consumer diets –. Nitrogen isotopic composition changes predictably with movement up the food web, allowing the determination of consumer trophic level if the nitrogen isotopic composition of basal resources in known , . Together, C and N stable isotopes have been used to characterize the effects of invasive organisms on the flow of energy through ecosystems , , food web length , and resource partitioning .
Few aquatic invaders have received as much attention from ecologists as the zebra and quagga mussels (Dreissena polymorpha and D. rostriformis bugensis, respectively). Yet, despite decades of study, the effects of dreissenids on energy flow and food web structure are not fully understood. Dreissenids are increasingly seen as habitat-couplers, redirecting nutrients, energy, and production from the water column to the littoral benthic region of lakes –. Dreissenids are filter-feeders that graze on seston and release undigested and unwanted particles as feces and pseudofeces (material collectively known as biodeposits) on the lake bottom, thereby increasing the flux of sestonic material to the benthos , . By clearing the water column and excreting dissolved nutrients at the substrate-water interface dreissenids also increase light penetration and nutrient availability in the nearshore, stimulating primary production of benthic algae , . Thus, dreissenids can compete with other filter-feeders for seston while increasing resource availability for littoral detritivores, grazers, and predators. Studies of the effect of dreissenids on benthic communities indeed show declines in the abundance of native filter feeders, and increased abundance of detritivores, some grazers, and benthic predators following dreissenid establishment , , .
In addition to evidence from studies of community structure, SIA approaches have shed some light on the way dreissenid establishment affects food webs. Because seston is often depleted in 13C relative to benthic algae , , carbon isotope ratios can be used to determine how dreissenids affect the importance and availability of these two energy sources to food webs. SIA of carbon has been used to show that dreissenids can compete with native filter feeders for seston , , and that redirected sestonic material in the form of dreissenid biodeposits can contribute significantly to the diet and production of detritivores such as amphipods and chironomids , . However, there have been no comprehensive examinations of how dreissenid establishment affects the absolute importance of benthic primary production to food webs, or the relative balance between sestonic and benthic energy sources.
The littoral zone can dominate production processes and the transfer of energy to higher trophic levels in lakes , , making it important we understand how perturbations affect the food web structure and energy dynamics of littoral ecosystems. To investigate the effect of dreissenids on the littoral food web of a large lake we compared the abundance, biomass, and production of hard substrate-inhabiting littoral benthos collected prior to, and more than a decade following dreissenid establishment in Lake Simcoe, Ontario. We performed SIA of all common members of the pre- and postdreissenid benthos and used isotope mixing models to estimate the importance of sestonic material and benthic primary production to the pre- and postdreissenid littoral benthic communities. Our objectives, by combining information about the biomass, production, and energy sources of different faunal groups, were to i) determine whether dreissenid establishment has had an impact on food web structure of the littoral benthos and, ii) quantify the impact of dreissenid establishment on the relative and absolute importance of sestonic and benthic energy sources to sustaining the littoral benthic food web.
No specific permits were required for the described field studies. All field studies were carried out on public property and did not involve protected or endangered species.
Lake Simcoe is a large (722 km2), oligo-mesotrophic lake in southern Ontario, Canada (Fig. 1). The extensive littoral zone of Lake Simcoe is dominated by rocky substrates to depths of about 8 m, while soft substrates prevail at greater depths. Dreissenid mussels were first observed in the benthos of Lake Simcoe in the fall of 1994, but did not become widespread and abundant until 1996 .
Quantitative benthic samples were collected in 1993 (predreissenid period) and in 2007–2008 (postdreissenid period), using an airlift sampler  operated by SCUBA divers. Fours sites (Fig. 1), selected to include mainland and island littoral habitats in different parts of the lake, were sampled in 1993 using a 0.25 m2 quadrat. The same locations were sampled again in 2007 for crayfish using a 0.25 m2 quadrat and in 2008 for other macroinvertebrates using a 0.0625 m2 quadrat. Three to four replicate samples were collected from 2-m depths at each site in the pre- and postdreissenid periods. Sampling in all years was carried out in late August and early to mid September.
Crayfish were stored frozen until identification, measurement, and tissue removal for SIA (see below). Quantitative samples of smaller macroinvertebrates were fixed in 10% buffered formalin and then transferred to 90% ethanol prior to enumeration and identification. Preserved airlift samples collected in 1993 from three of the four sites were counted to the order level shortly after collection and then returned to the original sample jars. Samples collected in 2008 were counted to the taxonomic level of family or lower for most groups in order to provide finer resolution for food web reconstruction. To maintain consistency of taxonomic resolution, we resorted the samples collected in 1993, then enumerated and identified invertebrates to the same taxonomic level as samples collected in 2008. Fewer animals were found in most samples during this re-sorting, which we attribute to losses caused by the original handling and processing. To estimate 1993 abundances at a taxonomic level that would allow intercomparison with the postdreissenid benthic community, we assumed that the original counts at the order level were correct and proportionally adjusted the counts for lower taxonomic levels. For example, there were 88 amphipods in the original count of replicate A from Blackbird Point. The recount found 44 Gammarus spp. and 12 Hyalella azteca, or a total 56 amphipods. We assumed that both Gammarus spp. and H. azteca suffered similar loss rates, adjusting the numbers to 69 Gammarus spp. and 19 H. azteca. We believe the assumption of equal loss across lower level taxonomic groups is reasonable given that loss rates were not significantly different across orders (Kruskal-Wallis one-way analysis of variance, p>0.05).
Dry biomass of most organisms was estimated from site-specific, length-dry weight relationships (Text S1) and observed, period-specific size-frequency distributions. In cases where we did not have sufficient material to construct site-specific length-dry weight relationships, published relationships were used (references in Text S1). Annual production of benthic invertebrates was estimated using the empirical model of Morin and Bourassa , which uses mean areal biomass, mean individual biomass, and mean annual water temperature to estimate taxon-specific secondary production. We report the abundance, biomass and production only for taxa that were relatively abundant (>5% of total abundance) in either the pre- or postdreissenid period, or that were deemed to contribute greatly to biomass and production because of their large individual size (e.g., crayfish). For a complete listing of invertebrate taxa at these sites see .
Seston for SIA was collected along the south-eastern shoreline of the lake from 8 sites of ∼1 m depth in July and August of 2008. Two 500 ml PET jars were submerged to a depth of ∼0.5 m, filled with lake water and placed on ice. In the lab seston samples were filtered onto precombusted quartz fibre filters, dried at 60°C for 24 hours and stored in a dessicator until preparation for isotope analysis. Periphyton scrapes were collected by a snorkeller from rocks at ∼1–1.5 m depth at McRae Point in September of 2008 (Fig. 1). A 60 ml syringe with an 18-gauge needle was used by a snorkeller to collect biodeposits and detritus from beneath mussel colonies. We observed mussels expelling fresh biodeposits during our sampling and gently collected this material using a syringe fitted with a 10 cm length of 2-mm Ø Tygon® tubing. In the lab biodeposit samples were filtered onto precombusted quartz fibre filters, dried at 60°C for 24 hours and stored in a glass dessicator until SIA. Samples collected from the surface and from beneath mussel colonies had similar stable isotope values, so these data were combined and are reported together.
Most small macroinvertebrates used for SIA were collected in September of 1993 and 2008 from shallow depths (∼1 m) at McRae Point using D-nets with 500-µm nitex mesh and kick and sweep sampling. Macroinvertebrates were separated into general taxonomic groups, allowed to empty their guts for 24 hours in refrigerated containers with lake water, and stored frozen in de-ionized water until analysis. We did not have sufficient frozen material from McRae Point to cover all taxonomic groups, so frozen samples from the predreissenid period were supplemented with formalin-preserved invertebrates collected at McRae Point and adjacent Black Point at 2 m depth in the fall of 1993. SIA results of formalin-preserved samples were corrected for the effect of long-term formalin preservation, which was shown to result in a 2‰ depletion to δ13C values and no significant change to δ15N values of aquatic invertebrate tissues .
Our samples from 2008 were supplemented with specimens of common but less abundant invertebrates collected by kick and sweep sampling at McRae Point and Black Point in September of 2009. Where sufficient numbers of samples of the same taxa were available for a statistical comparison of isotope values of frozen material from 2008 versus 2009, and frozen versus formalin-preserved (and preservation effect-corrected) material from 1993 no significant differences in 13C values were found, and only small (<1‰) differences in 15N values were seen in the case of postdreissenid Gammarus sp. and chironomids (two-sample independent t-tests at α = 0.05); we therefore combined the data. Crayfish for SIA were collected from depths of 2, 4, and 6 m at two sites adjacent to McRae Point (Strawberry Island and Grape Island, Fig. 1). A comparison of the results showed no statistically significant difference in crayfish isotopic composition with depth or between sites (one-way ANOVAs, p>0.05), so crayfish from all depths were pooled for analysis.
Samples of periphyton, crayfish dorsal abdominal muscle, and other invertebrates were prepared for SIA by drying for 24–48 hours at 60°C. Animals other than crayfish were either ground whole or after removal of shells in the case of gastropods and bivalves. When necessary to achieve a minimum sample weight of 0.25 mg, individuals within taxa were combined into a single isotope sample. Biodeposit samples and seston samples were analysed on quartz filters. Seston and biodeposit samples were split into two portions, one of which was acidified by fumigation in a glass dessicator with concentrated hydrochloric acid to remove carbonates . Periphyton samples were acidified in glass vials by slowly adding 10% HCl until visible bubbling stopped, and were then redried, ground and weighed. Samples were analyzed on a Delta Plus continuous flow mass spectrometer (Thermo Finnigan, Germany) coupled to Carlo Erba elemental analyzer (CHNS-O EA1108, Italy) at the University of Waterloo Environmental Isotope Laboratory. Replicate samples had a standard deviation of 0.21‰ for 13C and 0.28‰ for 15N.
A two-source, single-isotope (13C) linear mixing model (IsoError ) was used to estimate the relative importance of sestonic material and benthic primary production to taxa in the pre- and postdreissenid periods. No primary producers were available from the 1993 collections. Consequently snails, which are considered to be periphyton grazers , were used as the benthic end-member and filter-feeding hydropsychid caddisflies  as the sestonic end-member for the predreissenid mixing model. For the postdreissenid period we examined the effect of using two combinations of end-members on food web reconstruction. In our first approach we used seston and periphyton as the sestonic and benthic end-members (seston-periphyton model). In our second approach we used primary consumers as end-members, reasoning that since primary consumers were used as end-members for the predreissenid period, a postdreissenid mixing model based on primary consumers would enable a more direct comparison between periods. We used dreissenids as the sestonic end-member and psephenid beetle larvae (water pennies) as the benthic end-member because dreissenids appear to rely almost exclusively on seston, while psephenids are known to be grazers of periphyton ,  and were the closest to periphyton in 13C values among postdreissenid consumers (dreissenid-psephenid model).We decided not to use snails as the benthic end member in our postdreissenid reconstruction because snails were no longer the most enriched member of the fauna (Fig. 2), suggesting that they incorporated more sestonic material than snails in the predreissenid period. The percent contribution of sestonic and benthic material for each taxon obtained from the mixing models together with taxon-specific biomass and production estimates were used to determine the relative and absolute contribution of benthic and sestonic resources to the nearshore food web in the pre- and postdreissenid periods.
We did not perform SIA on sphaeriid clams, assuming 100% reliance on pelagic carbon. While the literature partially supports this assumption (e.g., ,  and references therein), overestimation of the contribution of sestonic material to sphaeriids should not greatly affect overall conclusions because sphaeriids comprised only a small fraction of pre- (0.09 and 1.11%) and postdreissenid (0.02 and 0.13%) biomass and production, respectively. We also did not perform SIA on the crayfish Orconectes virilis, but results from other locations in Lake Simcoe show that O. virilis has similar δ13C and δ15N values to O. rusticus and O. propinquus (DO Evans, unpublished data). We assigned the isotopic value of O. virilis based on the average isotopic values of 5 randomly selected O. rusticus and 5 O. propinquus from our dataset. Only one sample of the amphipod Crangonyx sp. from 1993 was analysed; the average standard deviation of δ13C values of two other amphipods (Gammarus spp. and H. azteca) was used to approximate the standard deviation of δ13C values of Crangonyx sp. for use in our mixing model.
Abundance, biomass, and estimated production (EP) of the nearshore benthos were much higher in 2007–2008 than in 1993, the year immediately preceding dreissenid establishment in Lake Simcoe. The abundances of most individual taxa as well as total invertebrate abundance were significantly greater in the postdreissenid period (Table 1; Wilcoxon rank-sum tests at α = 0.05). Total invertebrate abundance increased almost 33-fold from an average of 795.2 (±126.2 SE) to 25,807.0 (±1885.3 SE) individuals m−2, total biomass increased approximately 6-fold from 10.7 to 60.3 g dry wt m−2, and total EP increased 14-fold from 6.4 to 90.9 g dry wt m−2 year−1 (Table 1). Dreissenids contributed to much of the increases in biomass and EP of the benthos, constituting 37.7% of the total biomass and 55.8% of total EP in the postdreissenid period (Table 1). Two recent invaders, the crayfish O. rusticus and the amphipod Echinogammarus ischnus, together comprised 33% of non-dreissenid biomass and 19.7% of non-dreissenid EP in 2007–2008 (Table 1).
The composition of the benthic community shifted considerably after dreissenid establishment. The predreissenid community was numerically dominated by chironomids and amphipods, while crayfish, snails, mayflies, oligochaetes and amphipods accounted for the bulk of biomass and EP (Table 1). Much of the enhanced postdreissenid abundance was due to large increases in the abundances of amphipods, isopods, chironomids, oligochaetes, and the introduction of dreissenids. Crayfish (33.9 g m−2) and dreissenids (22.7 g m−2) dominated the postdreissenid biomass, with amphipods, oligochaetes, and isopods also contributing considerably to total biomass. Dreissenids accounted for more than half of EP in the postdreissenid period, followed by small crustaceans, i.e. amphipods and isopods (19.2%), crayfish (14.6%), flatworms (4.6%), and chironomids and other Insecta (4.2%) (Table 1).
Snails were the most enriched in 13C among the predreissenid benthic taxa (−21.4±0.5 SD ‰), and filter-feeding hydropsychid caddisflies the most depleted (−27.9±0.7 SD ‰). Chironomids were the most depleted group in 15N (3.2±1.2 SD ‰), and large lumbriculid oligochaetes the most enriched (14.0±0.85 SD ‰) (Fig. 2A, Table 2).
Postdreissenid δ13C values of all benthic taxa were bracketed by seston (−26.9±1.45 SD ‰) and periphyton (−11.5±0.7 SD ‰). Dreissenid biodeposits were found to be more enriched in δ13C than seston (−22.6±0.8 SD ‰), suggesting the possibility of inclusion of periphyton or macrophyte detritus in our biodeposit samples, preferential rejection by dreissenids of this 13C enriched fraction from their filtered intake, or enrichment during metabolic processing by mussels or bacteria. The most 13C enriched members of the post-dreissenid fauna were psephenid beetle larvae (−15.8±1.6 SD ‰ δ13C), and dreissenid mussels were the most depleted (−25.8±0.4 SD ‰ δ13C). Psephenid beetles (5.7±0.3 SD ‰ δ15N) and flatworms (11.6±0.5 SD ‰ δ15N) were the most depleted and enriched faunal groups in 15N, respectively (Table 2).
The nine groups that were sampled in both the pre- and postdreissenid periods, and had sufficient replicates for a statistical comparison (Gammarus spp., Hyalella azteca, O. propinquus, Physa sp., Chironomidae, Heptageniidae, Hydropsychidae, Elmidae and Oligochaeta) were consistently and significantly more enriched in 13C in the postdreissenid period (two-sample independent t-tests at α = 0.05) by an average of 4.47 (±0.66 SE) ‰ δ13C (Table 2). Most of those groups also showed a significant, albeit smaller, enrichment in 15N (average 1.34 ‰ ±1.01 SE).
Members of the predreissenid littoral food web displayed a range of reliance on benthic and sestonic resources (Table 3). Filter-feeding hydropsychids and oligochaete worms were the most sestonic-reliant groups, and snails and chironomids the most benthic-reliant. Crayfish, which dominated the biomass and production of the predreissenid benthos were estimated to utilize 67% (±3.1 SE) benthic resources. The average, taxon-specific contribution of sestonic carbon across all taxa was 48.6%. The choice of end-members had an effect on estimates of the importance of benthic and sestonic energy sources to different taxa in the postdreissenid period. The seston-periphyton model showed a greater importance of sestonic material for most groups relative to the dreissenid-psephenid model (Table 3). The average, taxon-specific contribution of sestonic carbon across all taxa was 55.3% in the seston-periphyton model and 41.9% in the dreissenid-psephenid model (Table 3).
The biomass (69.7%) and secondary production (70.6%) of the predreissenid littoral food web were supported mainly by benthic primary production (Table 4, Fig. 3), due to the domination of biomass and production by mostly benthic-reliant crayfish and snails. Most (98.5%) of the sestonic carbon in the predreissenid benthos was also contained in crayfish. Amphipods, sphaeriid clams, heptageniid mayflies, elmid beetle larvae, and worms also contributed to storage and turnover of sestonic carbon prior to dreissenid establishment (Table 3, Table 4).
Contributions of sestonic material and benthic primary production to the food web shifted following dreissenid establishment. Estimates based on the seston-periphyton and dreissenid-psephenid mixing models were in agreement and revealed that, overall, sestonic material contributed more strongly than benthic primary production to the postdreissenid nearshore food web (Table 4, Fig. 3). However, estimates based on seston-periphyton and dreissenid-psephenid models provided somewhat different estimates for the importance of sestonic material versus benthic primary production to the non-dreissenid benthos. The seston-periphyton model showed that benthic and sestonic energy sources were about equally important to the non-dreissenid benthos, whereas the dreissenid-psephenid model suggested benthic primary production is about twice as important in supporting non-dreissenid biomass and secondary production (Table 4, Fig. 3).
The establishment of Dreissena spp. has resulted in dramatic changes to the structure and energy base of the littoral food web in Lake Simcoe. Long-term dreissenid presence led to large increases in the abundance, biomass, and production of littoral macroinvertebrates. We observed changes in both the relative and absolute importance of sestonic and benthic energy sources to the littoral food web, with the relative importance of sestonic material increasing following dreissenid establishment. The results of isotope mixing models and the large increases in biomass and production of the benthos imply that the absolute contribution of both sestonic and benthic material to the food web increased dramatically following dreissenid establishment (Fig. 3). These results provide evidence that dreissenids transfer energy and nutrients from the water column to the littoral benthos of lakes though deposition of sestonic material, as well as through stimulation of benthic primary production.
We found the predreissenid littoral fauna of Lake Simcoe to be typical of exposed rocky substrata in the Great Lakes region  with crayfish and snails dominating biomass and secondary production, and benthic primary production supporting about 70% of biomass and secondary production. The establishment of dreissenids has frequently been associated with increases in the abundance and biomass of littoral benthos, and while the increase in abundance seen in our study is among the largest reported, the qualitative changes to the benthic community generally paralleled those observed elsewhere , , with amphipods, isopods, chironomids, and oligochaetes undergoing large increases in absolute and relative abundance. It is thought that dreissenid enhancement of littoral benthos, especially on rocky substrates, results from a combination of habitat modification and increased food supply , . Shells of living and dead dreissenids increase the availability of habitat  and provide refuge to invertebrates from predation by fish , while the increased flux of sestonic material , and enhanced benthic primary production rates ,  provide greater food resources to benthic consumers. Until now, however, the relative and absolute importance of redirected sestonic material and benthic primary production to dreissenid-invaded food webs have not been well resolved.
Previous studies have shown that dreissenid biodeposits are used as an energy source by some littoral benthic taxa , , and our results demonstrate that redirected sestonic material forms a large portion of the energy budget of the postdreissenid littoral food web in Lake Simcoe. While sestonic carbon contributed most to the biomass and production of dreissenid mussels, it also supported between one third and half of the biomass and production of non-dreissenid benthos. The absolute importance of sestonic material to littoral biomass was about an order of magnitude greater in postdreissenid times, while the contribution of sestonic material to littoral secondary production increased by about 35-fold. Excluding dreissenids, the absolute importance of sestonic material to the biomass and production of the littoral benthos increased by between 3–5, and 7–11 fold, respectively, suggesting that dreissenid biodeposits are an important energy source to the nearshore. The notion that dreissenid biodeposits form the main source of sestonic carbon to the littoral food web is supported by the fact that water clarity increased and planktonic algal biovolumes in Lake Simcoe either decreased or remained unchanged since dreissenid establishment , , making it highly unlikely that natural sedimentation rates of sestonic material increased appreciably in postdreissenid times.
The absolute importance of benthic primary production to the benthos also increased considerably since predreissenid times. While increases in crayfish biomass accounted for much of the increase in the absolute importance of benthic carbon, all other benthic taxa (with the exception of snails) contributed to the increased utilization of benthic primary production in the postdreissenid food web. The absolute importance of benthic primary production to supporting littoral biomass approximately tripled, while its importance to supporting secondary production increased 4–6 fold. This result is consistent with observed increases in benthic primary production following dreissenid establishment ,  and demonstrates that dreissenid-mediated increases in benthic primary production are translated into increased secondary production. Thus, while we saw moderate changes to the relative importance of benthic and sestonic primary production to non-dreissenid benthos, our results clearly demonstrate that the absolute importance of both increased substantially (Fig. 3).
Our choice of mixing model end-members affected estimates of the relative and absolute importance of littoral and sestonic production to the postdreissenid food web. The relative merits of the two postdreissenid mixing models we used are open to debate. On the one hand mixing models based on primary consumers are recommended because consumers average the signatures of primary producers which can vary considerably over time , and offer a “time-integrated” picture of the food web. On the other hand, the use of primary consumers requires assumptions about their diets. Snails are recommended as the benthic-littoral end-member in mixing models because they are assumed to feed almost exclusively on periphyton. Feeding experiments, however, show that snails often feed opportunistically (e.g., ), and our stable isotope results suggest that sestonic material may have comprised a considerable portion (30 to 48%) of snail diets in the postdreissenid period. The relatively high reliance of snails on sestonic material in the postdreissenid period raises the question whether snails are an appropriate benthic end-member for our reconstruction of the predreissenid food web. We believe that because sestonic material was less readily available to snails in the predreissenid period their reliance on benthic algae would have been higher than in postdreissenid times. There is still a possibility that by using snails we are overestimating the importance of benthic material to the predreissenid food web, but this is unlikely to affect the main conclusion of our study that the absolute importance of both sestonic material and benthic primary production to the littoral food web increased following dreissenid establishment.
An unexpected finding of our study was the consistent enrichment in 13C and 15N of benthic organisms in the postdreissenid period, regardless of whether the organisms were filter-feeders, detritivores, or grazers. Our mixing models show that the relative importance of isotopically-heavy benthic primary production to most taxa did not increase significantly following dreissenid establishment (Table 2), suggesting that benthic and sestonic primary producers became more enriched in 15N and 13C following dreissenid invasion. While we cannot confirm that such a shift in isotopic values of primary producers occurred, it would be consistent with increased rates of sestonic and benthic primary production often seen in dreissenid invaded systems . As primary production rates increase fractionation against heavier isotopes can decrease drastically, leading to more enriched δ13C and δ15N values of benthic and sestonic primary producers –, which is consistent with the isotopic enrichment seen in our study. The possibility that changes in primary production rates associated with dreissenid establishment and other ecological perturbations can lead to shifts in isotopic values of primary producers deserves further investigation, and may need to be considered in studies using isotopic approaches and archival samples to examine the effects of perturbations on food webs. Long-term background enrichment in 15N values  associated with increasing human development of the watershed  offers another possible explanation for the enrichment of 15N values in postdreissenid benthos, although the levels of 15N enrichment seen in sediment cores since dreissenid establishment in the lake  are unlikely to account for the full magnitude of enrichment seen in our benthos samples.
Several caveats should be mentioned. Firstly, empirical models of invertebrate production offer only general approximations of actual production rates , so our secondary production results should be recognized as estimates rather than direct measurements. Secondly, we assumed that dreissenid establishment was the only major change that impacted the ecology of Lake Simcoe between 1993 and 2008. There is evidence that phosphorus loading into the lake has declined by 20–30% from the mid 1990’s to the late 2000’s , , but it is unlikely that this relatively modest reduction could account for the observed changes to the food web, and we believe that dreissenid invasion offers the most parsimonious explanation for our results. Finally, our observations apply to the rocky nearshore of a relatively clear lake with an extensive littoral zone. We predict that in deeper portions of lakes, more turbid lakes, or lakes with a steeper morphometry, dreissenid enhancement of the benthic food web might be driven to a greater extent by redirection of sestonic material, and to a lesser extent by stimulation of littoral production than in our study system.
This is the first study to combine SIA with biomass and production estimates to describe how dreissenids affect food web structure and energy sources in lakes. Our findings are consistent with the hypothesis that dreissenids redirect energy and material from the water column to the littoral areas of lakes , . By providing increased habitat availability dreissenids create a physical “matrix” for enhancements in the abundance, biomass, and production of the littoral benthos. By changing the rates and sources of energy supply to the benthos, dreissenids modify the energy base and structure of the littoral food web. Biodeposition of sestonic material by dreissenid mussels creates a direct energy link from the water column to the littoral benthos and increases the amount of energy available to detritivores and other members of the benthic community. Increased water clarity and dreissenid remineralization of sestonic-derived nutrients in the nearshore creates an indirect energy link to the nearshore by stimulating benthic littoral primary production. The redirection of production from the sestonic realm to the nearshore by dreissenids has major implications for aquatic ecosystems and may explain some of the changes in the distribution, energy sources, and production of nearshore and offshore fish communities , , nutrient cycling patterns , , and transfer of contaminants through food webs ,  seen following dreissenid establishment.
Length-dry weight relationships used to estimate invertebrate biomass, methods used to construct length-dry weight relationships, and references for those relationships obtained from the literature.
Click here for additional data file (pone.0051249.s001.doc)
We wish to acknowledge the help rendered in the lab and in the field by Yvonne Allen, Victoria Kopf, Audie Skinner, Katrina Wisniewski, Stacey Zwiers (Ontario Ministry of Natural Resources), David Depew, Eric Dunford, Joel Harrison, Jennifer Hood, Adam Houben, Simona Lenard, Sairah Malkin, Bill Mark, Jessica Pang, and Lee Pinnel (University of Waterloo). Thoughtful comments from Robert Hecky and an anonymous reviewer helped in improving this manuscript.
|1.||Vitousek PM,, Mooney HA,, Lubchenko J,, Melillo JM, (Year: 1997) Human domination of Earth’s ecosystems. Science277: 494–499|
|2.||Global Invasive Species Database (http://www.issg.org/database). Accessed on December 05, 2011.|
|3.||Strayer DL, (Year: 2010) Alien species in fresh waters: ecological effects, interactions with other stressors, and prospects for the future. Freshwat Biol55 (Suppl. 1)152–174|
|4.||Peterson BJ,, Fry B, (Year: 1987) Stable isotopes in ecosystem studies. Annu Rev Ecol Syst18: 293–320|
|5.||Hecky RE,, Hesslein RH, (Year: 1995) Contributions of benthic algae to lake food webs as revealed by stable isotope analysis. J N Am Benthol Soc14: 631–653|
|6.||Post DM, (Year: 2002) Using stable isotopes to estimate trophic position: models, methods, and assumptions. Ecology83: 703–718|
|7.||Minagawa M,, Wada E, (Year: 1984) Stepwise enrichment of 15N along food chains: Further evidence and the relation between δ15N and animal age. Geochim Cosmochim Acta48: 1135–1140|
|8.||Vander Zanden MJ,, Casselman JM,, Rasmussen JB, (Year: 1999) Stable isotope evidence for the food web consequences of species invasions in lakes. Nature401: 464–467|
|9.||Nilsson E,, Solomon CT,, Wilson KA,, Willis TV,, Larget B,, et al. (Year: 2011) Effects of an invasive crayfish on trophic relationships in north-temperate lake food webs. Freshwater Biol57: 10–23|
|10.||Gorokhova E,, Hansson S,, Höglander H,, Andersen CM, (Year: 2005) Stable isotopes show food web changes after invasion by the predatory cladoceran Cercopagis pengoi in a Baltic Sea bay. Oecologia143: 251–25915688211|
|11.||Limén H,, van Overdijk CDA,, MacIsaac HJ, (Year: 2005) Food partitioning between the amphipods Echinogammarus ischnus, Gammarus fasciatus, and Hyalella azteca as revealed by stable isotopes. J Great Lakes Res31: 97–104|
|12.||Mills EL,, Casselman JM,, Dermott R,, J. Fitzsimons JD,, Gal G,, et al. (Year: 2003) Lake Ontario: food web dynamics in a changing ecosystem (1970–2000). Can J Fish Aquat Sci60: 471–490|
|13.||Hecky RE,, Smith REH,, Barton DR,, Guildford SJ,, Taylor WD,, et al. (Year: 2004) The nearshore phosphorus shunt: a consequence of ecosystem engineering by dreissenids in the Laurentian Great Lakes. Can J Fish Aquat Sci61: 1285–1293|
|14.||Higgins SN,, Vander Zanden MJ, (Year: 2010) What a difference a species makes: a meta-analysis of dreissenid mussel impacts on freshwater ecosystems. Ecol Monogr80: 179–196|
|15.||Izvekova EI,, Lvova-Katchanova AA, (Year: 1972) Sedimentation of suspended matter by Dreissena polymorpha Pallas and its subsequent utilization by Chironomidae larvae. Pol Arch Hydrobiol19: 203–210|
|16.||Gergs R,, Rinke K,, Rothhaupt KO, (Year: 2009) Zebra mussels mediate benthic-pelagic coupling by biodeposition and changing detrital stoichiometry. Freshwat Biol54: 1379–1391|
|17.||Malkin SY,, Guildford SJ,, Hecky RE, (Year: 2008) Modelling the growth of Cladophora in a Laurentian Great Lake in response to changes due to the exotic invader Dreissena and lake warming. Limol Oceanogr53: 1111–1124|
|18.||Ward JM,, Ricciardi A, (Year: 2007) Impacts of Dreissena invasions on benthic macroinvertebrate communities: a meta-analysis. Divers Distrib13: 155–165|
|19.||Ozersky T,, Barton DR,, Evans DO, (Year: 2011) Fourteen years of dreissenid presence in the rocky littoral zone of a large lake: effects on macroinvertebrate abundance and diversity. J N Am Benthol Soc30: 913–922|
|20.||France RL, (Year: 1995) Carbon-13 enrichment in benthic compared to planktonic algae: foodweb implications. Mar Ecol Prog Ser124: 307–312|
|21.||Mitchell MJ,, Mills EL,, Idrisi N,, Michener R, (Year: 1996) Stable isotopes of nitrogen and carbon in an aquatic food web recently invaded by Dreissena polymorpha (Pallas). Can J Fish Aquat Sci53: 1445–1450|
|22.||Garton DW,, Payne CD,, Montoya JP, (Year: 2005) Flexible diet and trophic position of dreissenid mussels as inferred from stable isotopes of carbon and nitrogen. Can J Fish Aquat Sci62: 1119–1129|
|23.||Gergs R,, Grey J,, Rothhaupt KO, (Year: 2011) Temporal variation in zebra mussel (Dreissena polymorpha) density structure the benthic food web and community composition on hard substrates in Lake Constance, Germany. Biol Invasions13: 2727–2738|
|24.||Vadeboncoeur Y,, Vander Zanden M J,, Lodge DM, (Year: 2002) Putting the lake back together: reintegrating benthic pathways into lake food web models. BioScience52: 44–54|
|25.||Evans DO, Skinner AJ, Allen R, McMurtry MJ (2011) Invasion of zebra mussel, Dreissena polymorpha, in Lake Simcoe. J Great Lakes Res (Suppl. 3): 36–45.|
|26.||Barton DR,, Hynes HBN, (Year: 1978) Wave-zone macrobenthos of the exposed Canadian shores of the St. Lawrence Great Lakes. J Great Lakes Res4: 27–45|
|27.||Morin A,, Bourassa N, (Year: 1992) Modèles emperiques de la production annuelle et do rapport P/B d’invertébrés benthiques d’eau courante. Can J Fish Aquat Sci49: 532–539|
|28.||Rennie MD,, Ozersky T,, Evans DO, (Year: 2012) Effects of formalin preservation on invertebrate isotopic values over decadal time scales. Can J Zool90: 1320–1327|
|29.||Lorrain A,, Savoye N,, Chauvaud L,, Paulet Y,, Naulet N, (Year: 2003) Decarbonation and preservation method for the analysis of organic C and N contents and stable isotope ratios of low-carbonated suspended particulate material. Anal Chim Acta491: 125–133|
|30.||Phillips DL,, Gregg JW, (Year: 2001) Uncertainty in source partitioning using stable isotopes. Oecologia127: 171–179|
|31.||Merritt RW, Cummins KW (1996) An introduction to the aquatic insects on North America, 3rd ed. Dubuque: Kendall-Hunt Publishing Company. 862 p.|
|32.||Murvosh CM, (Year: 1971) Ecology of the water penny beetle Psephenus herricki (DeKay). Ecol Monogr41: 79–96|
|33.||Hershey A,, Beaty S,, Fortino K,, Kelly S,, Keyse M,, et al. (Year: 2006) Stable isotope signatures of benthic invertebrates in arctic lakes indicate limited coupling to pelagic production. Limnol Oceanogr51: 177–188|
|34.||Kořínková T, (Year: 2011) Food utilisation in fingernail and pill clams. Malacologica Bohemoslovaca10: 1–4|
|35.||Stewart TW,, Miner JG,, Lowe RL, (Year: 1998) Quantifying mechanisms for zebra mussel effects on benthic macroinvertebrates: organic matter production and shell generated habitat. J N Am Benthol Soc17: 81–94|
|36.||Silver Botts P,, Patterson BA,, Schloesser DW, (Year: 1996) Zebra mussel effects on benthic invertebrates: physical or biotic?J N Am Benthol Soc15: 179–184|
|37.||Beekey MA,, DJ McCabe,, JE Marsden, (Year: 2004) Zebra mussels affect benthic predator foraging success and habitat choice on soft sediments. Oecologia141: 164–17015278426|
|38.||Mayer CM,, Keats RA,, Rudstam LG,, Mills EL, (Year: 2002) Scale-dependent effects of zebra mussels on benthic invertebrates in a large eutrophic lake. J N Am Benthol Soc21: 616–633|
|39.||Eimers MC,, Winter JG,, Scheider WA,, Watmough SA,, Nicholls KH, (Year: 2005) Recent changes and patterns in the water chemistry of Lake Simcoe. J Great Lakes Res31: 322–332|
|40.||Winter JG, Young JD, Landre A, Stainsby E, Jarjanazi H (2011) Changes in phytoplankton community composition of Lake Simcoe from 1980 to 2007 and relationships with multiple stressors. J Great Lakes Res (Suppl. 3): 63–71.|
|41.||Lombardo P,, Cooke D, (Year: 2002) Consumption and preference of selected food types by two freshwater gastropod species. Arch Hydrobiol155: 667–685|
|42.||Laws E,, Popp BN,, Bidigare RR,, Kennicutt MC,, Macko SA, (Year: 1995) Dependence of phytoplankton carbon isotopic composition on growth rate and [CO2]aq: Theoretical considerations and experimental results. Geochim Cosmochim Acta59: 1131–1138|
|43.||MacLeod NA,, Barton DR, (Year: 1998) Effects of light intensity, water velocity, and species composition on carbon and nitrogen stable isotope ratios in periphyton. Can J Fish Aquat Sci55: 1919–1925|
|44.||Hill WR,, Fanta SE,, Roberts BJ, (Year: 2008) 13C dynamics in benthic algae: effects of light, phosphorus and biomass development. Limnol Oceanogr53: 1217–1226|
|45.||Hiriart-Baer VP,, Milne JE,, Marvin CH, (Year: 2011) Temporal trends in phosphorus and lacustrine productivity in Lake simcoe inferred from lake sediment. J Great Lakes Res37: 764–771|
|46.||Evans DO,, Nicholls KH,, Allen YC,, McMurtry MJ, (Year: 1996) Historical land use, phophorus loading and loss of fish habitat in Lake Simcoe, Canada. Can J Fish Aquat Sci53: 194–218|
|47.||Benke AC, (Year: 1993) Concepts and patterns of invertebrate production in running waters. Verh Internat Verein Limnol25: 15–38|
|48.||Young JD, Winter JG, Molot L (2011) A re-evaluation of the empirical relationships connecting dissolved oxygen and phosphorus loading after dreissenid mussel invasion in Lake Simcoe. J Great Lakes Res (Suppl. 3): 7–15.|
|49.||Rennie MD,, Sprules GW,, Johnson TB, (Year: 2009) Resource switching in fish following a major food web disruption. Oecologia159: 789–80219214590|
|50.||Campbell LM,, Thacker R,, Barton D,, Muir DCG,, Greenwood D,, et al. (Year: 2009) Re-engineering the eastern Lake Erie littoral food web: the trophic function of non-indigenous Ponto-Caspian species. J Great Lakes Res37: 224–231|
|51.||Stańczykowska A,, Lewandowski K, (Year: 1993) Effect of filtering activity of Dreissena polymorpha (Pall.) on the nutrient budget of the littoral of Lake Mikołajskie. Hydrobiologia251: 73–79|
|52.||Ozersky T,, Malkin SY,, Barton DR,, Hecky RE, (Year: 2009) Dreissenid phosphorus excretion can sustain C. glomerata growth along a portion of Lake Ontario shoreline. J Great Lakes Res35: 321–328|
|53.||Bruner KA,, Fisher SW,, Landrum PF, (Year: 1994) The role of the zebra mussel, Dreissena polymorpha, in contaminant cycling: II. Zebra mussel contaminant accumulation from algae and suspended particles, and transfer to the benthic invertebrate, Gammarus fasciatus. J Great Lakes Res20: 735–750|
|54.||Morrison HA,, Gobas FAPC,, Lazar R,, Whittle MD,, Haffner DG, (Year: 1998) Projected changes to the trophodynamics of PCBs in the western Lake Erie ecosystem attributed to the presence of zebra mussels (Dreissena polymorpha). Environ Sci Technol32: 3862–3867|
Table 1 Mean abundance (standard error in parentheses), biomass, and annual production of benthic organisms in pre- and postdreissenid periods from 4 shallow (2 m) sites in Lake Simcoe.
|Taxon||Abundancem−2||Biomassmg m−2||Productionmg m−2 yr−1||Abundancem−2||Biomassmg m−2||Productionmg m−2 yr−1|
|Hyalella azteca||117.1 (30.9)||11||92||4414.9 (882.1)*||313||3280|
|Gammarus spp.||11.7 (4.1)||3.7||18||3820.6 (749.2)*||1020||6850|
|Echinogammarus ischnus||not present||not present||not present||2652.6 (691.3)||446||3500|
|Crangonyx sp.||6.2 (2.3)||0.70||4.6||1146.3 (408.6)*||143||1230|
|Caecitodea racovitzai||0.0||0||0||1516.6 (366.2)*||385||2620|
|Orconectes propinquus||17.6 (2.8)||9970||4870||19.0 (4.4)||17930||7710|
|Orconectes rusticus||not present||not present||not present||10.8 (4.8)||11950||4420|
|Orconectes virilis||0.0||0||0||1.5 (0.7)*||4040||1160|
|Physidae||15.9 (6.0)||76||154||51.4 (18.9)||142||427|
|Hydrobiidae||19.7 (6.3)||3.7||22||278.9 (88.6)*||89||553|
|Dreissena spp.||not present||not present||not present||3366.3 (688.3)||22720||50760|
|Sphaeriidae||74.3 (12.7)||14||84||146.3 (45.6)||12||114|
|Chironomidae||296.8 (112.0)||12||124||3709.7 (698.4)*||248||2640|
|Polycentropodidae||17.6 (4.4)||13||45||171.4 (46.8)*||104||519|
|Heptageniidae||46.8 (8.3)||22||104||115.4 (48.1)||42||247|
|Elmidae||45.2 (11.0)||9.2||60||227.7 (135.0)||49||372|
|Oligochaeta||98.1 (43.1)||16||93||3798.9 (653.6)*||565||372|
|Platyhelminthes||2.0 (1.3)||0.60||3.0||358.9 (120.3)*||107||4170|
|All taxa combined||795.2 (126.2)||10670||6370||25807.0 (1885.3)*||60300||90900|
Asterisks appear beside the significantly larger number as determined by Wilcoxon rank-sum test at α = 0.05.
Table 2 Summary of results of 13C and 15N isotope analysis (standard deviation in brackets) for taxa collected in the pre- (1993) and postdreissenid periods (2007–2009).
|Group||Year of collection||Preservation method||n||Average δ13C||Average δ15N|
|Chironomidae||1993||formalin||7||−21.76 (1.16)||3.17 (1.60)|
|Elmidae||1993||frozen (1), formalin (6)||7||−26.19 (1.30)||5.19 (0.92)|
|Gammarus spp.||1993||frozen (5), formalin (1)||6||−23.96 (1.01)||3.95 (1.01)|
|Heptageniidae||1993||frozen (4), formalin (3)||7||−25.30 (0.40)||5.83 (1.17)|
|Hyalella azteca||1993||formalin||5||−23.36 (0.52)||3.83 (0.41)|
|Hydropsychidae||1993||frozen||5||−27.94 (0.67)||7.92 (1.71)|
|Orconectes propinquus||1993||frozen||18||−23.54 (0.52)||10.54 (0.70)|
|Oligochaeta||1993||frozen||2||−26.63 (0.22)||14.00 (0.85)|
|Snails||1993||frozen||8||−21.37 (0.50)||5.35 (0.38)|
|biodeposits||2008||frozen||6||−22.56 (0.79)||4.15 (0.25)|
|periphyton||2008||frozen||5||−11.49 (0.72)||3.73 (0.29)|
|seston||2008||frozen||8||−26.90 (1.45)||4.90 (0.56)|
|Chironomidae||2008 (4), 2009 (7)||frozen||11||−19.36 (0.48)||8.03 (0.30)|
|Dreissena spp.||2008||frozen||7||−25.84 (0.40)||7.29 (0.25)|
|Echinogammarus ischnus||2008||frozen||6||−18.60 (0.45)||6.05 (0.48)|
|Elmidae||2008||frozen||4||−19.09 (0.61)||6.40 (0.22)|
|Gammarus spp.||2008 (7), 2009 (2)||frozen||9||−19.66 (0.55)||7.09 (0.78)|
|Heptageniidae||2008||frozen||2||−22.17 (0.17)||7.13 (0.13)|
|Hyalella azteca||2009||frozen||5||−19.99 (0.27)||6.59 (0.71)|
|Hydropsychidae||2008||frozen||2||−24.27 (0.25)||10.29 (0.11)|
|Isopoda||2008 (6), 2009 (1)||frozen||7||−19.23 (0.27)||6.54 (0.52)|
|Orconectes propinquus||2007||frozen||17||−18.49 (0.58)||10.29 (0.41)|
|Orconectes rusticus||2007||frozen||18||−18.94 (1.63)||9.68 (0.67)|
|Oligochaeta||2009||frozen||4||−18.39 (1.26)||8.19 (0.63)|
|Platyhelminthes||2008||frozen||4||−20.54 (0.39)||11.55 (0.54)|
|Polycentropodidae||2008||frozen||4||−21.08 (0.72)||9.77 (0.23)|
|Psephenidae||2008||frozen||5||−15.82 (1.57)||5.65 (0.28)|
|Snails||2008||frozen||14||−18.44 (1.04)||7.82 (0.60)|
Number in brackets beside year of collection and preservation method indicates how many of the total number of samples (n) were collected in that year or preserved using that method for taxa for which samples from more than one year or preservation methods were used.
Table 3 Contribution of sestonic carbon (% sestonic) to members of the benthos in the pre- and postdreissenid periods in the shallow littoral zone of Lake Simcoe, as determined by stable isotope analysis and the IsoError isotope mixing model .
|Hyalella azteca||30.3 (4.3)||55.2 (2.2)||41.6 (4.3)|
|Gammarus spp.||39.4 (6.8)||53.0 (2.3)||38.3 (4.7)|
|Echinogammarus ischnus||–||46.1 (2.3)||27.7 (5.6)|
|Crangonyx sp.||63.6 (12.1)||–||–|
|Caecidotea racovitzai||–||50.2 (2.1)||34.0 (4.8)|
|Orconectes propinquus||33.0 (3.1)||45.4 (2.1)||26.6 (5.3)|
|Orconectes rusticus||–||48.3 (3.2)||31.1 (6.2)|
|Snails||0 (3.8)||47.4 (3.0)||29.7 (6.0)|
|Dreissena spp.||–||93.1 (3.3)||100 (2.1)|
|Chironomids||5.9 (7.1)||51.1 (2.2)||35.3 (4.8)|
|Polycentropodidae||–||62.2 (3.2)||52.5 (5.0)|
|Heptageniidae||59.8 (4.0)||69.3 (2.5)||63.4 (3.0)|
|Elmidae||73.4 (8.4)||49.3 (2.8)||32.6 (5.6)|
|Psephenidae||–||28.1 (4.9)||0 (9.9)|
|Hydropsychidae||100 (7.2)||82.9 (3.0)||84.3 (2.4)|
|Oligochaeta||80.1 (4.7)||45.1 (2.6)||26.2 (5.9)|
|Platyhelminthes||–||58.7 (2.5)||47.1 (4.2)|
Standard error is shown in brackets.
Table 4 Amount of sestonic- and benthic-derived biomass and production in different groups of littoral benthos of Lake Simcoe, in pre- and postdreissenid periods, using hydropsychids and snails as the sestonic and benthic end-members for the predreissenid period and two combinations of end-members for the postdreissenid period.
|Group||sestonic-derived biomass mg m−2||benthic-derived biomass mg m−2||sestonic -derived production mg m−2 yr−1||benthic-derived production mg m−2 yr−1|
|predreissenid; end-members: hydropsychids (sestonic)- snails(benthic)|
|postdreissenid; end-members: seston (sestonic)- periphyton (benthic)|
|postdreissenid; end-members: dreissenids (sestonic)- psephenids (benthic)|
Previous Document: Transcriptome analysis suggests that starch synthesis may proceed via multiple metabolic routes in h...
Next Document: The C-terminus of ClpC1 of Mycobacterium tuberculosis is crucial for its oligomerization and functio...