Advertisement
Browse Subject Areas
?

Click through the PLOS taxonomy to find articles in your field.

For more information about PLOS Subject Areas, click here.

  • Loading metrics

Open Access

Peer-reviewed

Research Article

Assessing the Utility of Hydrogen, Carbon and Nitrogen Stable Isotopes in Estimating Consumer Allochthony in Two Shallow Eutrophic Lakes

  • Jari Syväranta ,

    jarsyv@bios.au.dk

    Affiliations Department of Fish Biology and Ecology, Leibniz-Institute of Freshwater Biology and Inland Fisheries, Berlin, Germany, Lake Ecology Section, Department of Bioscience, Aarhus University, Silkeborg, Denmark

    ⨯
  • Kristin Scharnweber,

    Affiliations Department of Fish Biology and Ecology, Leibniz-Institute of Freshwater Biology and Inland Fisheries, Berlin, Germany, Evolutionary Biology Centre, Department of Ecology and Genetics; Limnology, Uppsala University, Uppsala, Sweden

    ⨯
  • Mario Brauns,

    Affiliations Department of Fish Biology and Ecology, Leibniz-Institute of Freshwater Biology and Inland Fisheries, Berlin, Germany, Department of River Ecology, Helmholtz Centre for Environmental Research -UFZ, Magdeburg, Germany

    ⨯
  • Sabine Hilt,

    Affiliation Department of Ecosystem Research, Leibniz-Institute of Freshwater Biology and Inland Fisheries, Berlin, Germany

    ⨯
  • Thomas Mehner

    Affiliation Department of Fish Biology and Ecology, Leibniz-Institute of Freshwater Biology and Inland Fisheries, Berlin, Germany

    ⨯

Abstract

Hydrogen stable isotopes (δ2H) have recently been used to complement δ13C and δ15N in food web studies due to their potentially greater power to separate sources of organic matter in aquatic food webs. However, uncertainties remain regarding the use of δ2H, since little is known about the potential variation in the amount of exchangeable hydrogen (Hex) among common sample materials or the patterns of δ2H when entire food webs are considered. We assessed differences in Hex among the typical sample materials in freshwater studies and used δ2H, δ13C and δ15N to compare their effectiveness in tracing allochthonous matter in food webs of two small temperate lakes. Our results showed higher average amounts of Hex in animal tissues (27% in fish and macroinvertebrates, 19% in zooplankton) compared to most plant material (15% in terrestrial plants and 8% in seston/periphyton), with the exception of aquatic vascular plants (23%, referred to as macrophytes). The amount of Hex correlated strongly with sample lipid content (inferred from C:N ratios) in fish and zooplankton samples. Overall, the three isotopes provided good separation of sources (seston, periphyton, macrophytes and allochthonous organic matter), particularly the δ2H followed by δ13C. Aquatic macrophytes revealed unexpectedly high δ2H values, having more elevated δ2H values than terrestrial organic matter with direct implications for estimating consumer allochthony. Organic matter from macrophytes significantly contributed to the food webs in both lakes highlighting the need to include macrophytes as a potential source when using stable isotopes to estimate trophic structures and contributions from allochthonous sources.

Citation: Syväranta J, Scharnweber K, Brauns M, Hilt S, Mehner T (2016) Assessing the Utility of Hydrogen, Carbon and Nitrogen Stable Isotopes in Estimating Consumer Allochthony in Two Shallow Eutrophic Lakes. PLoS ONE 11(5): e0155562. https://doi.org/10.1371/journal.pone.0155562

Editor: Rafael Vazquez-Duhalt, Center for Nanosciences and Nanotechnology, MEXICO

Received: October 16, 2015; Accepted: April 29, 2016; Published: May 11, 2016

Copyright: © 2016 Syväranta et al. This is an open access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are credited.

Data Availability: All relevant data are within the paper and its Supporting Information files.

Funding: This study was financed by the TERRALAC-project of the Wissenschaftsgemeinschaft Leibniz (WGL) to SH and TM. JS was supported by the IGB Fellowship program in Freshwater Science and by the Marie Skłodowska-Curie actions fellowship (660655) under the EU Horizon 2020 funding programme.

Competing interests: The authors have declared that no competing interests exist.

Introduction

Stable isotope analysis (SIA) is now routinely used to study food webs and energy flow within aquatic ecosystems. Carbon isotope ratios (δ13C) are often used as tracers of sources of energy fueling the food webs, while nitrogen isotope ratios (δ15N) are mainly used to quantify trophic levels of organisms and sources of inorganic nitrogen [1]. SIA studies have provided invaluable information on the contributions of allochthonous resources [2–6] and methane-derived carbon to animal consumers in freshwater food webs [7–10], both features that would be difficult or often impossible to study using more conventional methods, such as gut content analyses. However, many studies are faced with substantial difficulties in separating potential sources with sufficient precision due to their overlapping δ13C and δ15N values and/or too many sources to be separated with only two isotopes. In some cases, enrichment studies, using for example 13C-bicarbonate [4, 11–12] or C4 plant material such as cane sugar or maize (Zea mays) [13–15], are a useful way to alter the naturally occurring isotope ratios within the sources to enhance separation. Unfortunately, these methods are not always applicable due to high costs and effort, and alternative measures are needed.

Following recent advances in methodological issues [16–17], stable hydrogen isotopes (δ2H or δD) have now become well established tracers, for example in studies of animal migrations, particularly in terrestrial systems [18–19]. Doucett et al. [20] proposed δ2H as a potential alternative to δ13C in tracing allochthonous organic matter contributions in aquatic food webs by showing that the δ2H provided a greater separation between terrestrial and aquatic production in arid lotic systems. This stems from the fact that δ2H values in terrestrial plants are considerably elevated due to additional discrimination during the transpiration [21], which is not observed in aquatic plants. Differences in δ2H values between terrestrial and aquatic production can exceed 100‰, particularly in arid environments [20], but substantial separation is also possible in more mesic environments [22–23]. Therefore, δ2H values are currently widely employed in many aquatic food web studies, but particularly in tracing allochthonous contributions in freshwater ecosystems [23–27].

However, the use of δ2H has several caveats that can reduce its robustness in food web studies. Over 20% of the H bound in organic sample material can be freely exchangeable with H in ambient water vapor [16]. While the issue of exchangeable H (Hex) in analytical procedures can now efficiently be controlled for, there is still substantial lack of knowledge about differences in the amount of Hex among sample materials. The amount of Hex in some tissues, like keratin, is rather well known and consistent [17] but less is known about the fraction in many other tissues, even though these are continuously used in δ2H studies. This uncertainty in the amount of Hex potentially has serious implications for sample treatment, standardization and results interpretation [28]. Consumers also acquire part of their tissue H from dietary/environmental water, as shown in several controlled experiments [29–33], which complicates inferences of the origin of organic matter supporting consumers. Particular uncertainties remain on the influence of environmental water when whole food webs and multiple trophic levels are considered, as the influence of environmental H may multiply at higher trophic levels. In fact, studies using δ2H on an entire food web scale are still very rare. Furthermore, there is considerable debate on whether and to what extent discrimination in δ2H values occurs during trophic transfers [18, 22, 30–31]. Discrimination likely results from the increased intake of environmental water but can potentially be masked by the substantial influence of lipids on tissue δ2H values. Lipids are highly depleted in 2H [34–35] and may have δ2H values as much as 100‰ lower compared to other body tissues [18, 32], having a substantial influence on bulk tissue δ2H values in lipid-rich tissues or animals [22, 27, 32]. Also, lipids contain very little or no Hex [16, 36] potentially complicating sample preparation procedures among samples with variable lipid contents.

Another potential concern arises from recent evidence of surprisingly elevated δ2H values in aquatic macrophytes [37–38]. The significance of macrophytes (aquatic vascular plants) as an energy source for aquatic consumers has long been debated [39–41], and strong evidence exists for their dietary role especially for benthic consumers [41–44]. Reported δ2H values of macrophytes have been considerably higher than those in algal (phytoplankton or attached algae) production in the same system, approaching the δ2H values analyzed from terrestrial plants. Such overlapping δ2H values between autochthonous macrophytes and allochthonous terrestrial primary producers might severely undermine the robustness of using H isotopes to trace the contributions of allochthonous matter in aquatic food webs, particularly in systems with potentially significant contribution of macrophyte-derived organic matter to consumers.

Here we first compared the amounts of Hex among all our sample materials to assess whether the commonly used keratin standards are suitable for analyzes of δ2H of typical aquatic organisms. We then elucidated entire food web structures using stable isotopes of hydrogen, carbon and nitrogen and assessed their suitability in tracing the contributions from allochthonous organic matter in food webs of two small temperate lakes. We estimated allochthonous contributions to consumers using isotope mixing models and employed either δ13C and δ15N values or δ13C, δ15N and δ2H values to assess the added value of δ2H in temperate lowland lakes. In addition, we evaluated the importance of macrophytes in estimating allochthonous organic matter contributions by running mixing models with and without macrophytes as one potential source.

Materials and Methods

Samples were collected from two eutrophic, shallow lakes located in North-Eastern Germany during summer 2010. Kleiner Gollinsee (hereafter referred to as Gollinsee) has an area of 3.3 ha, mean depth of 1.7 m, total phosphorus (TP) concentration of 42 μg l-1 and dissolved organic carbon (DOC) concentration of 12.3 mg l-1. Gollinsee is turbid (light attenuation: 1.2 ± 0.1 m-1) and dominated by phytoplankton whereas Schulzensee (3.9 ha, 2.3 m, TP 34 μg l-1 and DOC 11.3 mg l-1, respectively) has higher water clarity (light attenuation: 0.7 ± 0.1 m-1) and approximately 22% of the lake area is colonized by submerged macrophytes (Ceratophyllum submersum) [45]. Both lakes are surrounded by alder trees (Alnus glutinosa) and reed stands (Phragmites australis), the latter contributing significantly to the C influx of both lakes [44]. Floating-leaved macrophytes (Nymphaea alba and Nuphar lutea) are growing in both lakes and cover 3% of the lake area in Gollinsee and 12% in Schulzensee [46]. Roach (Rutilus rutilus) was the dominant fish species in both lakes accounting for almost two-thirds of fish biomass, while sunbleak (Leucaspius delineatus) was highly abundant only in the turbid lake after a partial winterkill [47].

Aquatic plant samples (phytoplankton/seston, attached algae and macrophytes, n = 13) and terrestrial plant material (n = 6) were collected in June 2010 to analyze H, C and N stable isotope values in potential sources of organic matter to the lake food webs. Seston was collected by hauling a small mesh size (30 μm) net slowly behind the boat, picking out all larger zooplankton and detritus, diluting the cleaned sample into larger volume of water followed by further separation by sedimentation and drying in an oven. Periphyton was collected by scraping samples from floating and submerged macrophytes and from artificial polypropylene slides submersed into the lake. Periphyton samples were then picked clean from all visible animal and detritus particles, and dried in an oven. Aquatic macrophyte samples (C. submersum, N. alba and reed) were collected by dissecting fresh leaves from the plants which were then wiped clean and cut into smaller pieces, and dried in an oven. Samples from allochthonous organic matter (allo-om) were taken from birch (Betula pendula) and alder trees and included fresh and conditioned leaves from the lake littoral (detritus). Fresh and conditioned samples were analyzed separately but did not differ in their isotope values; hence they were all pooled to represent allo-om.

Zooplankton samples (n = 19) were collected three times (April, June and September 2010) during summer with several vertical hauls using zooplankton nets (mesh sizes 100 and 55μm) and replicate samples were collected during each sampling period from different sites. Samples were then brought to the laboratory and left overnight in clean tap water to allow gut evacuation. The next day these samples were identified, sorted and dried in an oven for later preparation for SIA. All zooplankton isotope values reported here represent samples of Cladocera comprising almost entirely of Daphniidae and Bosminidae. Benthic macroinvertebrate samples (n = 33) were collected in spring and summer with sweep-nets from depths of 0.5 − 1.0 m, identified visually to either family or genus level, sorted and placed into plastic jars with clean tap water for gut evacuation overnight.

Samples (n = 72) of fish, mainly roach, rudd (Scardinius erythrophthalmus), sunbleak, perch (Perca fluviatilis) and pike (Esox lucius) were collected throughout the summer with Nordic multi-mesh gillnets. In addition, young-of-the-year (YOY) cyprinid fish juveniles were collected with electrofishing in May. Fish were killed after capture and frozen for transport to the laboratory. Fishing was conducted by persons holding the official license for professional fishermen in Germany and hence followed the ethical standards and no further permits were needed. Access to and permission to fish in Schulzensee was provided by the Förderverein Feldberg-Uckermärkische Seen e.V. and by the Stiftung Pro Artenvielfalt in Gollinsee. Length and weight were measured and a small muscle sample was dissected from each individual fish. The muscle samples were then dried in an oven for later processing for SIA. In addition to all solid samples, four replicates of approximately 2 ml of lake water were sampled in June ~0.5 m below the lake surface from both lakes, and stored in 2 ml glass vials with air tight caps for later δ2H analysis of water.

All solid isotope samples were dried in an oven at 60°C and ground into homogenous powder using a mortar and pestle. A small subsample (0.6 mg) was then weighed into a tin cup for the analysis of δ13C and δ15N at the University of Jyväskylä, Finland, using a FlashEA 1112 elemental analyzer coupled to a Thermo Finnigan DELTAplus Advantage mass spectrometer (Thermo Electron Corporation, Waltham, MA, U.S.A.) following standard protocols and analytical precision better than 0.2‰ for both δ13C and δ15N. Two subsamples (0.4 mg) of each solid sample were also accurately weighed into silver cups for δ2H analyses. The two different sample sets for δ2H analysis were used to assess the amount of Hex in different tissues types. Since significant part of the tissue H can be exchangeable [16], Hex needs to be taken into account when analyzing δ2H from organic materials. Therefore one sample set was equilibrated in Colorado Plateau Stable Isotope Laboratory (CPSIL) ambient lab air with δ2H value -91 ± 8‰ (monthly average for given analysis month) and the other set under water vapor with a δ2H value +354 ± 1.3‰ following Wassenaar & Hobson [17]. The fraction of Hex was then calculated from f(Hex) = (δ2Hsample1—δ2Hsample2) / (δ2Hwater1—δ2Hwater2), where sample1 and sample2 are the δ2H values for the same sample after equilibration in water vapor with two different δ2H values and water1 and water2 are the δ2H values of the water vapor [16, 36, 48–49].

All hydrogen isotope analyses from organic sample material were performed at CPSIL. Samples of organic materials were pyrolized to H2 and the isotope ratio was measured on the H2 gas [20]. Organic matter samples for δ2H were analyzed with a Thermo-Finnigan TC/EA and DeltaPLUS-XL (Thermo Electron Corporation, Bremen, Germany) using keratin, CBS (Caribou hoof) and KHS (Kudo horn) as normalization standards [16–17], and several secondary standards (Moose hair, Baleen BWB-II, Chitin TCI, Colorado River algae and IAEA-085). Hydrogen isotopes from water samples were analyzed by Laser Water Isotope Analyzer V2 (Los Gatos Research, Inc., Mountain View, CA, USA) at UC Davis Stable Isotope Facility. All values are reported in per mil notation (‰) and are in relation to the international standard of Vienna Standard Mean Oceanic Water (δ2HVSMOW). Analytical precision for δ2H of solid samples was < 3‰ and for water < 1‰.

We used R 2.15.2 [50] and Bayesian mixing models in the SIAR (Stable Isotope Analysis in R) package [51] to calculate the proportion of different carbon sources to consumer tissues. We calculated allochthonous organic matter contributions using both a two-isotope (CN, δ13C and δ15N) and a three-isotope model (HCN, δ2H, δ13C and δ15N) with periphyton, seston, allo-om and macrophytes as sources for primary consumers, and a HCN model with and without aquatic macrophytes as one potential source, to compare the results and the impact of using more isotopes and sources. While we were primarily interested in assessing the utility of hydrogen isotopes to trace the flow of allochthonous organic matter in aquatic food webs [20], we did not simply divide the potential energy sources into autochthonous and allochthonous origins but rather wanted to use all three isotopes to illustrate the structure of the entire food web in these lakes. For these models, we assumed no trophic discrimination for δ2H, but conservative 0.5 ± 0.2‰ for δ13C and 3.0 ± 0.5‰ discrimination for δ15N [52]. However, the H in environmental (or dietary) water directly influences consumer δ2H [18, 30], which needs to be accounted for in the model. We corrected for the dietary water using a model ωcompound = 1—(1—ω)t from Solomon et al. [30], where ωcompound is the total H contribution from dietary water to consumer tissue δ2H at trophic level t, and ω is the proportion of tissue H derived from environmental water (see Wilkinson et al. [28] for a recent review on the potential effects of selecting suitable ω). We used ω = 0.173 from Solomon et al. [30] for all consumers and estimated trophic level t for each fish individual from a linear relationship between primary consumer (all invertebrates were assigned t = 2) δ13C and δ15N values in littoral and pelagic habitats following a model outlined in Karlsson and Byström [53]. The model first estimates the fraction of littoral carbon in a consumer (LFcons) from pelagic and littoral isotope baselines (here means of zooplankton/bivalves in pelagic and gastropods/isopods in littoral) from: LFcons = [δ13Ccons—δ13Cpel−(δ15Ncons—δ15Npel) × TS] ÷ (1—TS × BS) / (δ13Clit—δ13Cpel), where TS is the slope of trophic discrimination for δ13C and δ15N (same values as for SIAR above) and BS is the slope of the linear relationship between the pelagic (pel) and littoral (lit) baselines. The trophic position of a consumer (t) can then be calculated from: t = 2 + ([δ15Ncons—δ15Npel—(δ13Clit—δ13Cpel) × BS × LFcons] / ΔN), where ΔN is the discrimination factor for δ15N. Fish were assumed to acquire allo-om indirectly through their prey and therefore mixing models of fish used invertebrates (for non-piscivorous fish) and invertebrates and prey fish (for piscivorous fish, i.e. large perch and pike) as prey sources. The estimates of allo-om contribution were then calculated using ratio calculation from each individual prey source [54, 55].

Differences in the amount of Hex among sample types, and differences in mean allochthonous source contributions using either CN, HCN or no-macrophyte models, were examined using paired t-tests, after testing for normality of paired differences. In cases where the assumptions for normality and homoscedasticity were violated, we used a non-parametric Kruskal-Wallis test with pairwise comparisons. Multivariate analysis of variance (MANOVA) with effect size (partial η2) was used to assess how well the isotopes separated sources in these lakes and overall which isotope had the greatest separating power (strongest effect). Since lipids have less or negligible amount of Hex compared to other tissues (e.g. [16, 36]), we used sample tissue C:N ratios as a proxy for lipid content [56–57] and examined the correlations between C:N ratio and the fraction of Hex with Pearson’s correlation. All statistical tests were done using IBM SPSS Statistics 20.0 (IBM Company, Armonk, NY, U.S.A.)

Results

Fish and macroinvertebrates had consistently more Hex in their tissues compared to zooplankton (F5,141 = 37.7, p < 0.001), while the amount in plant material was highly variable between aquatic and terrestrial plants (Table 1). Aquatic vascular plants (macrophytes) had significantly (p < 0.05, Table 1) more Hex compared to both terrestrial plant material and seston/periphyton. There was a strong negative correlation (Pearson’s r = -0.67, p < 0.001, n = 72) between the amount of Hex and the C:N ratio of fish muscle tissue (Fig 1), indicating that tissues with higher lipid content (C:N ratio) have less Hex. Zooplankton had a similar negative correlation between C:N and Hex, but due to lower sample size this correlation was not significant (r = -0.42, p = 0.07, n = 19). In contrast, both benthic macroinvertebrates and plants showed no correlation between C:N and the amount of Hex (Fig 1).

thumbnail
Download:
Table 1. Fraction of Hex in different sample types.

https://doi.org/10.1371/journal.pone.0155562.t001

thumbnail
Download:
Fig 1. Correlation of Hex and lipid content in sample tissues.

Relationship between the fraction of exchangeable H (Hex) (0−1) and the C:N ratios (as proxy for lipid content) in sample materials. Values for Pearson’s correlation coefficients and p-values are given in each corresponding panel.

https://doi.org/10.1371/journal.pone.0155562.g001

Carbon stable isotope values in Gollinsee and Schulzensee food webs varied roughly by 10‰ with lowest δ13C values (-33 to -35‰) observed in pelagic seston and highest (-24 to -25‰) in aquatic macrophytes in both lakes (Fig 2). The δ15N values similarly varied by almost 10‰ from producers to consumers with slightly higher values in pelagic consumers (zooplankton, planktivorous fish) than in more littoral consumers (benthic macroinvertebrates, benthivorous fish), a pattern often observed in eutrophic lakes (e.g. [58]). The mean isotope values of sources (i.e. seston, periphyton, allo-om and macrophytes) were similar between the two lakes (MANOVA; p = 0.438) but differed from each other particularly in δ13C and δ2H values. In fact, the mean δ2H values were clearly distinct and separated (Fig 3), except between seston and periphyton, and δ2H clearly had the highest effect size (F3,11 = 41.5; p < 0.001; partial η2 = 0.93). Mean δ13C values also provided a reasonable separation, particularly among seston, allo-om and macrophytes (F3,11 = 19.9; p < 0.001; partial η2 = 0.84), but could not separate periphyton from allo-om or macrophytes. Only periphyton was separated by its mean δ15N values from other sources (F3,11 = 6.1; p = 0.011; partial η2 = 0.62) and overall the values were strongly overlapping. In general, seston and periphyton had the lowest and nearly identical mean (± SD) δ2H values at -161 ± 0.1‰ to -174 ± 3.6‰ with very little variation around the mean values. Allo-om had mean δ2H values ~30‰ elevated to seston/periphyton at -143 ± 11‰ in Gollinsee and -137 ± 2‰ in Schulzensee, while the most elevated mean δ2H values were observed in aquatic macrophytes (-107 ± 18‰ in Gollinsee and -100 ± 16‰ in Schulzensee). δ2H values were not significantly different among submerged (C. submersum), floating-leaved (N. alba) and emerged (reed) macrophytes.

thumbnail
Download:
Fig 2. Isotope biplots of δ13C and δ15N values of the food webs in Gollinsee (upper panel) and Schulzensee (lower panel).

The figures illustrate sufficient separation but considerable overlap in δ13C and δ15N values among the sources in both lakes.

https://doi.org/10.1371/journal.pone.0155562.g002

thumbnail
Download:
Fig 3. Isotope biplots of δ2H and δ13C values of the food webs in Gollinsee and Schulzensee.

H and C isotopes reveal a distinct separation of sources in both lakes and the typical pattern of low and identical δ2H values in pelagic and littoral algal production, higher δ2H values in terrestrial organic matter but the highest δ2H values in aquatic macrophytes.

https://doi.org/10.1371/journal.pone.0155562.g003

Consumers in both lakes were positioned as expected within the δ13C-δ15N-δ2H space, after accounting for the environmental water on consumer H, which in Gollinsee had a mean δ2H value of -33 ± 0.3‰ and in Schulzensee -28 ± 0.6‰. The more pelagic consumers were clearly aligned towards seston δ13C and δ2H values while the more littoral benthic invertebrates had higher values and some clearly approached the values of aquatic macrophytes (Fig 3). Rudd, a known herbivorous fish [59], differed from other fish by its isotope values, particularly in macrophyte-rich Schulzensee (Figs 2 and 3), having isotope values indicative of its consumption of macrophytes and periphyton, and the highest estimates of allo-om contribution (Table 2).

thumbnail
Download:
Table 2. Mean allo-om contributions to consumers in Gollinsee and Schulzensee.

https://doi.org/10.1371/journal.pone.0155562.t002

Calculating mean allochthonous carbon contributions to different consumers in both food webs using either the CN (δ13C and δ15N) or the HCN (δ13C, δ15N and δ2H) models resulted in small and insignificant differences for the macroinvertebrate consumers (paired t-test; p = 0.85, Fig 4 upper panel). Mean allo-om contributions (± SD) to benthic macroinvertebrates in Gollinsee were 27 ± 5% using CN and 26 ± 7% using HCN and equal in Schulzensee at 28 ± 3% with CN and 28 ± 7% with HCN model (Table 2). Though not statistically significant, there was more difference in mean allo-om contribution between the two models within zooplankton samples; 21% and 14% in Gollinsee and Schulzensee using CN but only 9% and 7% using HCN, respectively (Fig 4, Table 2). Full mixing model results and reliance of invertebrate consumers from other carbon sources are provided in a supplementary S1 Table. Using only C and N isotopes resulted in similarly higher estimates of mean allo-om contribution to fish compared to HCN (t9 = -5.37, p < 0.001). Using C and N, the mean contribution of allo-om was 24 ± 1% and 21 ± 2% to fish biomass in Gollinsee and Schulzensee whereas using HCN, the values decreased to 16 ± 3% and 18 ± 4%, respectively. Including δ2H values in the model also increased the precision of mixing models, particularly at higher trophic levels, by decreasing the variation in observed probability distributions (Table 2).

thumbnail
Download:
Fig 4. A comparison of consumer allochthony values from different models.

Models used either δ13C and δ15N values or δ13C, δ15N and δ2H values (CN and HCN methods, upper panel) or a HCN mixing model with either macrophytes excluded from the model (y-axis, -macrophytes) or macrophytes included (x-axis, +macrophytes) to estimate consumer allochthony. The lines indicate a 1:1 fit. More detailed values with uncertainties are provided in Table 2.

https://doi.org/10.1371/journal.pone.0155562.g004

Comparing the HCN mixing models with and without aquatic macrophytes as one potential source for consumers resulted in more striking differences in allo-om contributions (Fig 4, lower panel, Table 2). While there was little difference in the estimates of allo-om contribution to zooplankton biomass with or without macrophytes, the impacts on macroinvertebrate and thereby fish estimates were significant (t9 = -2.92, p = 0.017 for macroinvertebrates and t9 = -2.20, p = 0.049 for fish). Excluding macrophytes from the model increased the allo-om contribution to benthic macroinvertebrates to 47 ± 24% (from 26 ± 7%) and 52 ± 13% (28 ± 7%) in Gollinsee and Schulzensee. The highest contribution of allo-om was found in detritivorous Asellus aquaticus (Isopoda) in Gollinsee, which approached 80%. For fish, the estimates increased to 29 ± 7% (16 ± 3%) and 25 ± 6% (18 ± 4%), respectively.

Discussion

This study underlines key issues that require more attention when using stable isotopes of hydrogen with carbon and nitrogen to study the structure and energy flow in freshwater ecosystems. Specifically, studies combining δ2H with δ13C and δ15N to trace allochthonous contributions in lake food webs need to be more aware of the possible δ2H values in different sources of organic matter in lakes and therefore carefully consider the choice of end-members (sources) in their mixing models. Most previous studies have not analyzed or reported δ2H of macrophytes, but instead used phytoplankton and/or attached algae as sole representatives for δ2H of autochthonous production [20, 23, 25–27, 60–61], assuming either insignificant contributions from aquatic macrophytes (or no presence of macrophytes) or equal δ2H values for all autochthonous production. Many of these studies assessed the allochthony of zooplankton to which macrophyte-derived organic matter might not significantly contribute independent of their presence in the lake, as shown in this study. However, terrestrial particulate organic matter (POM) has been shown to substantially support zooplankton [6] in more oligotrophic systems and therefore POM from macrophytes could be a significant source for zooplankton in these systems, assuming direct consumption of POM (but see Brett et al. [62]).

Our results show that i) macrophytes are an important dietary source for many aquatic consumers and, together with similar findings from previous studies [37–38], also ii) indicate that δ2H of higher aquatic plants can vary substantially from that of algae, with important implications for estimating allochthonous matter contributions derived from stable isotope mixing models. Further, the experimental equilibration of samples done here under two distinct δ2H of water vapor revealed differences in the amount of Hex in our sample materials which call for further examination.

Hex in sample materials

While there was practically no difference between the mean Hex in fish and benthic macroinvertebrates, both had significantly more Hex than the zooplankton samples. Similarly, the amount of Hex was low, but more variable, in all our seston and terrestrial plant samples. It is important to understand the potential implications of varying amount of Hex in sample materials, particularly when choosing suitable standards for analyses of δ2H from organic materials. As the exchangeable part of H in sample tissues is freely exchangeable with the H in water vapor, the standard materials should ideally have similar amounts of Hex as the samples. The δ2H values in air can fluctuate seasonally and differ markedly from those in the samples and therefore both differences in Hex and variation in δ2H of air will introduce bias into the final analysis results.

At present, keratin standards (such as powdered hair, horn, hoof, and whale baleen) are primarily used and available for reliable δ2H analyses. While keratin in feathers for example can theoretically have as much as 40% Hex [18], experimental studies have shown that these materials typically contain less than 20% Hex [16–17, 36] and biological materials generally contain between 10–30% [36]. Our fish muscle and macroinvertebrate samples contained on average 27% Hex which is somewhat higher than expected, but within the typical ranges. It is possible that the δ2H value used in our calculations (laboratory air moisture -91 ± 8‰, taken from the seasonal average values for precipitation at Flagstaff, Arizona, for the analysis time), is not entirely accurate. But even assuming a more negative value for the same area, such as -110‰ reported in Doucett et al. [20], would reduce the average %Hex value by only 1% unit for both fish and macroinvertebrates. Zooplankton as well as terrestrial and aquatic plants had on average 15–23% Hex fitting relatively well with the ~20% Hex of keratin standards, while seston/periphyton samples had much less Hex, on average just 8%. However, even though the differences in %-values may seem rather high, the impact on the final δ2H values may not be as dramatic when considering the expected differences among organic matter sources in fresh water systems, and other uncertainties associated with the mean δ2H values (Table 3). A difference <10‰ would probably not have a significant impact in systems with sufficient differences among the source δ2H values but needs to be considered when sources are less well separated and the Hex between the sample and the standard are more considerable (but see discussion in Wilkinson et al. [28]). Based on results presented here, the commonly used standard materials seem appropriate for aquatic consumer tissues but care must be taken when selecting standard materials for producer samples (such as those used here as sources).

thumbnail
Download:
Table 3. Potential influence of changing δ2H in air moisture on δ2H values in a sample with variable Hex.

https://doi.org/10.1371/journal.pone.0155562.t003

Of greater importance is unquestionably the sample lipid content [22, 32]. Lipids are known to be extremely (-100‰) depleted in 2H [34–35] and therefore could strongly influence the observed bulk sample δ2H values [32], being analogous to bulk sample lipid content and δ13C values [54]. Also, lipids contain very little Hex [16, 36]; hence samples with high lipid content may have much less Hex [16, 22, 48] with subsequent implications beyond the immediate effect on δ2H values of bulk samples. Using the bulk sample C:N ratio as a proxy for lipid content [56–57], the amount of Hex correlated strongly with fish muscle tissue and a weak relationship was also evident between zooplankton C:N ratios and Hex, indicating that the samples with higher lipid content had less Hex. Fish and zooplankton can both accumulate appreciable amounts of lipids in their body tissues and our results here demonstrate that in addition to the direct impacts on sample δ2H values, this will influence the amount of Hex in sample materials. However, the C:N ratio does not seem to correlate as strongly with the lipid content in benthic macroinvertebrates or in plant material, likely due to variable amounts of chitin in whole body invertebrate samples [56] and plasticity in nitrogen uptake and allocation in plants [63], which is likely the reason for no correlation between the amount of Hex and these sample materials here. It is strongly recommended that future food web studies using δ2H values either extract lipids from their samples (see further recommendations in Soto et al. [32] and Wilkinson et al. [28]) or work towards developing suitable δ2H normalization models similar to δ13C based on sample lipid content.

δ2H in primary producers

As expected, the δ2H values of water from both studied lakes were similar and fit well into the global isoscapes of δ2H in precipitation for North-Eastern Germany [64] and the observed values in precipitation for summer months in this region (www.waterisotopes.org). These values were therefore considered to represent δ2H in lake water for the entire summer. The δ2H values in pelagic phytoplankton (or seston) and attached algae/periphyton were ~130‰ more negative than the surrounding water, a value very similar to those found in many other studies [20, 23, 26, 38]. However, terrestrial vegetation (alder and birch leaves) had δ2H values only ~30‰ elevated from those of algae creating far less separation between δ2H values of allochthonous organic matter and algae than reported for example from more arid environments [20], or even from boreal humic lakes of northern Sweden [23]. Rather surprisingly, the macrophytes in our lakes had even higher δ2H values than terrestrial vegetation, being roughly another 30‰ enriched in 2H and we observed no differences in δ2H values among submerged, floating-leaved and emerged macrophytes. While surprising, a few other studies have also reported unexpectedly high δ2H values for macrophytes [37–38]. Photosynthesis is assumed to involve a discrimination in δ2H, making plants 160–170‰ more negative in their δ2H values than the environmental water [38, and references therein] and terrestrial plants with an additional transpiration process are expected to be considerably elevated in their final δ2H values compared to aquatic plants. At present it is difficult to explain the observed δ2H patterns in aquatic vegetation (but see discussion in [38]), but the distinct δ2H values of macrophytes in our lakes helped to verify their importance for lake consumers. The δ13C values often overlap among benthic algae, macrophytes and terrestrial sources, while the δ15N can be highly variable in aquatic systems [56, 65] due to the many potential sources of inorganic N [66], making these less efficient in separating multiple sources for mixing models.

Estimates of allochthonous contributions

The importance of including macrophytes as one potential source of organic matter in the mixing models when estimating allochthonous contributions was highlighted in the comparison of models with and without macrophytes (Fig 4, lower panel). While the difference in the estimates of allochthony for zooplankton was minimal between the two models, including macrophytes considerably reduced allochthony in fish, and particularly in benthic macroinvertebrates. Without macrophytes, allochthony of the isopod A. aquaticus and gastropods was as high as 70–80%, similar to the very high contributions reported in some previous studies [6, 67]. However, allochthony declined to 32–35% when macrophytes were added to the model, confirming the importance of macrophytes as one source of organic matter to consumers. In fact, Brothers et al. [45–46] made a detailed study on C fluxes in these lakes, including C flux from reeds and other macrophytes. Detailed measurements of macrophyte areas, densities and biomass with direct measurements and literature data of C content revealed high C influx from reeds and other macrophytes in both lakes (86% of C influx in Gollinsee i.e. 214 g C m-2 yr-1 and 72% i.e. 119 g C m-2 yr-1 in Schulzensee) [45, 54], indicating high autochthonous production. Therefore the lower estimates of allochthony in this study seem more realistic for these lakes. The importance of this finding is highlighted by the fact that in many studies using H (HC/HCN) isotopes only algae or periphyton are used as autochthonous mixing model end-member (20, 22–25, 61). While primary production in many lakes may indeed be dominated by algae, and macrophyte and reed abundance is low, in other lakes (such as those studied here) macrophytes contribute substantially to primary production [45]. Our calculations illustrate the potential implications of excluding macrophytes in the mixing models when they are present. As the macrophyte δ2H values in both our lakes were considerably elevated compared to other sources of organic matter, even rather small amounts of organic matter derived from macrophytes can significantly bias the estimates, if only algae and terrestrial matter were assumed as sources. Therefore, macrophytes should be included as one source in mixing models for lakes where they are present (including reeds in the littoral).

Estimates of consumer allochthony using either CN or HCN mixing models (Fig 4, upper panel) were more similar than those comparing HCN model with and without macrophytes. In fact, for benthic macroinvertebrates the CN and HCN models resulted in almost equal estimates of allochthony. In contrast, fish and particularly zooplankton allochthony were estimated higher using the traditional CN model but the difference could partly relate to the impacts of lipids on consumer δ2H values. Since lipids have very low δ2H values, even small amounts of storage lipids can have significant impact on the bulk sample δ2H values. We did not remove lipids from our samples but in particular zooplankton is known to accumulate appreciable amounts of lipids, considerably affecting the isotope values analyzed from bulk samples [57]. Therefore, removing lipids would certainly have elevated the δ2H values of zooplankton and would have increased the allochthony in HCN mixing models. In addition, very little is known about the potential discrimination of H isotopes in trophic transfers from prey to consumers. In our mixing models we used the common practice of assuming no real trophic discrimination, but did assume ~17% contribution from environmental water at each trophic level [30]. While our results do not point to any major additional trophic discrimination, these assumptions can influence the outcome particularly at the higher trophic levels [28] and therefore more laboratory work is urgently needed to verify the robustness of these assumptions.

Conclusions

Our results highlight the benefits of combining δ2H values with δ13C and δ15N in food web studies, particularly when multiple resources need to be separated. However, our comparisons of multiple sample materials for differences in Hex revealed significantly higher proportions of Hex in animal tissues compared to plant tissues (excluding macrophytes). In general, however, the results fit to expected ranges relatively well and align with those of most common standard materials (such as keratin). Nonetheless, we concur with previous studies [28, 32–33] urging for greater caution when interpreting δ2H results before more laboratory and field studies on the effects of environmental water, lipids and δ2H patterns in ecosystems are available. Furthermore, the importance of aquatic macrophytes as a dietary source for lake consumers was detected more clearly when using δ2H. Due to the high δ2H values of macrophytes, estimates of allochthony by mixing models were largely dependent on whether macrophytes were included or not. We therefore strongly recommend future studies to include macrophytes as a potential resource when using δ2H with δ13C and δ15N in aquatic food web studies.

Supporting Information

S1 Dataset. Stable HCN isotope data used in this study.

https://doi.org/10.1371/journal.pone.0155562.s001

(XLSX)

S1 Table. Mixing model source contributions to invertebrate consumers in Gollinsee and Schulzensee.

https://doi.org/10.1371/journal.pone.0155562.s002

(PDF)

Acknowledgments

We thank A. Türck, C. Helms, S. Oksanen, A. Vogt, and T. Wanke for their help in the field and laboratory. R. Mauersberger (Förderverein Feldberg-Uckermärkische Seen e.V.) and R. Tischbier (Stiftung Pro Artenvielfalt) kindly provided background information and access to the lakes. Shawn Devlin kindly checked the English of the manuscript.

Author Contributions

Conceived and designed the experiments: JS SH TM. Performed the experiments: JS KS MB SH TM. Analyzed the data: JS KS MB. Contributed reagents/materials/analysis tools: JS TM. Wrote the paper: JS KS MB SH TM.

References

  1. 1. Peterson BJ, Fry B. Stable isotopes in ecosystem studies. Ann. Rev. Ecol. Syst. 1987; 18:293–320.
  2. 2. Jones RI, Grey J, Sleep D, Quarmby C. An assessment, using stable isotopes, of the importance of allochthonous organic carbon sources to the pelagic food web in Loch Ness. Proc. R. Lond. B. 1998; 265:105–11.
  3. 3. Grey J, Jones RI, Sleep D. Seasonal changes in the importance of the source of organic matter to the diet of zooplankton in Loch Ness, as indicated by stable isotope analysis. Limnol. Oceanogr. 2001; 46:505–13.
  4. 4. Pace ML, Cole JJ, Carpenter SR, Kitchell JF, Hodgson JR, Van de Bogert MC, et al. Whole-lake carbon-13 additions reveal terrestrial support of aquatic food webs. Nature 2004; 427:240–3. pmid:14724637
  5. 5. Carpenter SR, Cole JJ, Pace ML, Van de Bogert MC, Bade DL, Bastviken D, et al. Ecosystem subsidies: Terrestrial support of aquatic food webs from C-13 addition to contrasting lakes. Ecology 2005; 86:2737–50.
  6. 6. Cole JJ, Carpenter SR, Pace ML, Van de Bogert MC, Kitchell JF, Hodgson JR. Differential support of lake food webs by three types of terrestrial organic carbon. Ecol. Lett. 2006; 9: 558–68. pmid:16643301
  7. 7. Grey J, Kelly A, Jones RI. High intraspecific variability in carbon and nitrogen isotope ratios of lake chironomid larvae. Limnol. Oceanogr. 2004; 49:239–44.
  8. 8. Jones RI, Carter CE, Kelly A, Ward S, Kelly DJ, Grey J. Widespread contribution of methane-cycle bacteria to the diets of lake profundal chironomid larvae. Ecology 2008; 89:857–64. pmid:18459348
  9. 9. Ravinet M, Syväranta J, Jones RI, Grey J. A trophic pathway from biogenic methane supports fish biomass in a temperate lake ecosystem. Oikos 2010; 119:409–16.
  10. 10. Jones RI, Grey J. Biogenic methane in freshwater food webs. Freshwater Biol. 2011; 56:213–29.
  11. 11. Taipale S, Kankaala P, Jones RI. Contributions of different organic carbon sources to Daphnia in the pelagic foodweb of a small polyhumic lake: Results from mesocosm (DIC)-C-13-additions. Ecosystems 2007; 10:757–72.
  12. 12. Devlin SP, Saarenheimo J, Syväranta J, Jones RI. Top consumer abundance influences lake methane efflux. Nature Commun. 2015; in press
  13. 13. Kankaala P, Peura S, Nykanen H, Sonninen E, Taipale S, Tiirola M, et al. Impacts of added dissolved organic carbon on boreal freshwater pelagic metabolism and food webs in mesocosm experiments. Fund. Appl. Limnol. 2010; 177:161–76.
  14. 14. Scharnweber K, Vanni MJ, Hilt S, Syväranta J, Mehner T. Boomerang ecosystem fluxes: organic carbon inputs from land to lakes are returned to terrestrial food webs via aquatic insects. Oikos 2014; 123:1439–48.
  15. 15. Scharnweber K, Syväranta J, Hilt S, Brauns M, Vanni MJ, Brothers S, et al. Whole-lake experiments reveal the fate of terrestrial particulate organic carbon in benthic food webs of shallow lakes. Ecology 2014; 95:1496–505. pmid:25039215
  16. 16. Wassenaar LI, Hobson KA. Improved method for determining the stable-Hydrogen isotopic composition (delta-D) of complex organic materials of environmental interest. Environ. Sci. Technol. 2000; 34:2354–60.
  17. 17. Wassenaar LI, Hobson KA. Comparative equilibration and online technique for determination of non-exchangeable hydrogen of keratins for use in animal migration studies. Isot. Environ. Healt. S. 2003; 39:211–17.
  18. 18. Hobson KA. Tracing origins and migration of wildlife using stable isotopes: a review. Oecologia 1999; 120:314–26.
  19. 19. Hobson KA. Using stable isotopes to trace long-distance dispersal in birds and other taxa. Diversity Distrib. 2005; 11:157–64.
  20. 20. Doucett RR, Marks JC, Blinn DW, Caron M, Hungate BA. Measuring terrestrial subsidies to aquatic food webs using stable isotopes of hydrogen. Ecology 2007; 88:1587–92. pmid:17601150
  21. 21. Smith BN, Ziegler H. Isotopic Fractionation of Hydrogen in Plants. Bot. Acta 1990; 103:335–42.
  22. 22. Jardine TD, Kidd KA, Cunjak RA. An evaluation of deuterium as a food source tracer in temperate streams of eastern Canada. J. N. Am. Benthol. Soc. 2009; 28:885–93.
  23. 23. Karlsson J, Berggren M, Ask J, Bystrom P, Jonsson A, Laudon H, et al. Terrestrial organic matter support of lake food webs: Evidence from lake metabolism and stable hydrogen isotopes of consumers. Limnol. Oceanogr. 2012; 57:1042–48.
  24. 24. Babler AL, Pilati A, Vanni MJ. Terrestrial support of detritivorous fish populations decreases with watershed size. Ecosphere 2011; 2:art76.
  25. 25. Cole JJ, Carpenter SR, Kitchell JF, Pace ML, Solomon CT, Weidel BC. Strong evidence for terrestrial support of zooplankton in small lakes based on stable isotopes of carbon, nitrogen, and hydrogen. Proc. Natl. Acad. Sci. U.S.A. 2011; 108:1975–80. pmid:21245299
  26. 26. Solomon CT, Carpenter SR, Clayton MK, Cole JJ, Coloso JJ, Pace ML, et al. Terrestrial, benthic, and pelagic resource use in lakes: results from a three-isotope Bayesian mixing model. Ecology 2011; 92:1115–25. pmid:21661572
  27. 27. Wilkinson GM, Carpenter SR, Cole JJ, Pace ML, Yang C. Terrestrial support of pelagic consumers: patterns and variability revealed by a multilake study. Freshwater Biol. 2013; 58:2037–49.
  28. 28. Wilkinson GM, Cole JJ, Pace ML. Deuterium as a food source tracer: Sensitivity to environmental water, lipid content, and hydrogen exchange. Limnol. Oceanogr. Methods 2015; 13:213–23.
  29. 29. Hobson KA, Atwell L, Wassenaar LI. Influence of drinking water and diet on the stable-hydrogen isotope ratios of animal tissues. Proc. Natl. Acad. Sci. USA 1999; 96:8003–6. pmid:10393937
  30. 30. Solomon CT, Cole JJ, Doucett RR, Pace ML, Preston ND, Smith LE, et al. The influence of environmental water on the hydrogen stable isotope ratio in aquatic consumers. Oecologia 2009; 161:313–324. pmid:19471971
  31. 31. Soto DX, Wassenaar LI, Hobson KA, Catalan J. Effects of size and diet on stable hydrogen isotope values (delta D) in fish: implications for tracing origins of individuals and their food sources. Can. J. Fish. Aquat. Sci. 2011; 68:2011–19.
  32. 32. Soto DX, Wassenaar LI, Hobson KA. Stable hydrogen and oxygen isotopes in aquatic food webs are tracers of diet and provenance. Funct. Ecol. 2013; 27:535–43.
  33. 33. Graham CT, Harrison SSC, Harrod C. Differences in the contributions of dietary water to the hydrogen stable isotope ratios of cultured Atlantic salmon and Arctic charr tissues. Hydrobiologia 2014; 721:45–55.
  34. 34. Smith B, Epstein S. Biogeochemistry of Stable Isotopes of Hydrogen and Carbon in Salt Marsh Biota. Plant Physiol. 1970; 46:738–42. pmid:16657539
  35. 35. Sessions AL, Burgoyne TW, Schimmelmann A, Hayes JM. Fractionation of hydrogen isotopes in lipid biosynthesis. Org. Geochem. 1999; 30:1193–200.
  36. 36. Chesson LA, Podlesak DW, Cerling TE, Ehleringer JR. Evaluating uncertainty in the calculation of non-exchangeable hydrogen fractions within organic materials. Rapid Commun. Mass Sp. 2009; 23:1275–80.
  37. 37. Cole JJ, Solomon CT. Terrestrial support of zebra mussels and the Hudson River food web: A multi-isotope, Bayesian analysis. Limnol. Oceanogr. 2012; 57:1802–15.
  38. 38. Hondula KL, Pace ML, Cole JJ, Batt RD. Hydrogen isotope discrimination in aquatic primary producers: implications for aquatic food web studies. Aquat. Sci. 2014; 76:217–29.
  39. 39. France RL. Stable isotopic survey of the role of macrophytes in the carbon flow of aquatic foodwebs. Vegetatio 1995; 124:67–72.
  40. 40. Hecky RE, Hesslein RH. Contributions of benthic algae to lake food webs as revealed by stable isotope analysis. J. N. Am. Benthol. Soc. 1995; 14:631–53.
  41. 41. Mendonca R, Kosten S, Lacerot G, Mazzeo N, Roland F, Ometto JP, et al. Bimodality in stable isotope composition facilitates the tracing of carbon transfer from macrophytes to higher trophic levels. Hydrobiologia 2013; 710:205–18.
  42. 42. Newman RM. Herbivory and detritivory on fresh-water macrophytes by invertebrates: a review. J. N. Am. Benthol. Soc. 1991; 10:89–114.
  43. 43. Batt RD, Carpenter SR, Cole JJ, Pace ML, Cline TJ, Johnson RA, et al. Resources supporting the food web of a naturally productive lake. Limnol. Oceanogr. 2012; 57:1443–1452.
  44. 44. de Kluijver A, Ning J, Liu Z, Jeppesen E, Gulati RD, Middelburg JJ. Macrophytes and periphyton carbon subsidies to bacterioplankton and zooplankton in a shallow eutrophic lake in tropical China. Limnol. Oceanogr. 2015; 60:375–85.
  45. 45. Brothers S, Hilt S, Meyer S, Köhler J. Plant community structure determines primary productivity in shallow, eutrophic lakes. Freshwater Biol. 2013; 58:2264–76.
  46. 46. Brothers S, Hilt S, Attermeyer K, Grossart H-P, Kosten S, Mehner T, et al. A regime shift from macrophyte to phytoplankton dominance enhances carbon burial in a shallow, eutrophic lake. Ecosphere 2013; 4:art137.
  47. 47. Hilt S, Wanke T, Brauns M, Brothers A, Gaedke U, Köhler J, et al. Contrasting response of shallow eutrophic lakes to winterkill of fish. Hydrobiologia 2015; 749:31–42.
  48. 48. Schimmelmann A, Lewan MD, Wintsch RP. D/H isotope ratios of kerogen, bitumen, oil, and water in hydrous pyrolysis of source rocks containing kerogen types I, II, IIS, and III. Geochim. Cosmochim. Acta. 1999; 63:3751–66.
  49. 49. Qi H, Coplen TB. Investigation of preparation techniques for delta H-2 analysis of keratin materials and a proposed analytical protocol. Rapid Commun. Mass Sp. 2011; 25:2672–72.
  50. 50. R Development Core Team. R: A language and environment for statistical computing. R foundation for statistical Computing. 2010; Vienna, Austria.
    • 51. Parnell AC, Inger R, Bearhop S, Jackson AL. Source partitioning using stable isotopes: coping with too much variation. PLOS One 2010; 5:e9672. pmid:20300637
    • 52. Syväranta J, Högmander P, Keskinen T, Karjalainen J, Jones RI. Altered energy flow pathways in a lake ecosystem following manipulation of fish community structure. Aquat. Sci. 2011; 73:79–89.
    • 53. Karlsson J, Bystrom P. Littoral energy mobilization dominates energy supply for top consumers in subarctic lakes. Limnol. Oceanogr. 2005; 50:538–43.
    • 54. Mehner T, Attermeyer K, Brauns M, Brothers S, Diekmann J, Gaedke U, et al. Weak response of animal allochthony and production to enhanced supply of terrestrial leaf litter in nutrient-rich lakes. Ecosystems. Forthcoming 2015
    • 55. Brauns M, Gücker B, Wagner C, Garcia X-F, Walz N, Pusch MT. Human lakeshore development alters the structure and trophic basis of littoral food webs. J. Appl. Ecol. 2011; 48:916–25.
    • 56. Kiljunen M, Grey J, Sinisalo T, Harrod C, Immonen H, Jones RI. A revised model for lipid-normalizing δ13C values from aquatic organisms, with implications for isotope mixing models. J. Appl. Ecol. 2006; 43:1213–22.
    • 57. Syväranta J, Rautio M. Zooplankton, lipids and stable isotopes: importance of seasonal, latitudinal, and taxonomic differences. Can. J. Fish. Aquat. Sci. 2010; 67:1721–29.
    • 58. Syväranta J, Hämäläinen H, Jones RI. Within-lake variability in carbon and nitrogen stable isotope signatures. Freshwater Biol. 2006; 51:1090–102.
    • 59. Prejs A, Jackowska H. Lake macrophytes as the food of roach (Rutilus rutilus L.) and rudd (Scardinius erythrophthalmus L.). I. Species composition and dominance relations in the lake food. Ekol. Pol. 1978; 26:429–37.
    • 60. Finlay JC, Doucett RR, McNeely C. Tracing energy flow in stream food webs using stable isotopes of hydrogen. Freshwater Biol. 2010; 55:941–51.
    • 61. Wilkinson GM, Pace ML, Cole JJ. Terrestrial dominance of organic matter in north temperate lakes. Global Biochem. Cy. 2013; 27:43–51.
    • 62. Brett MT, Kainz MJ, Taipale SJ, Seshana H. Phytoplankton, not allochthonous carbon, sustains herbivorous zooplankton production. Proc. Natl. Acad. Sci. USA 2009; 106:21197–201. pmid:19934044
    • 63. Post DM, Layman CA, Arrington DA, Takimoto G, Quattrochi J, Montaña CG. Getting to the fat of the matter: models, methods and assumptions for dealing with lipids in stable isotope analyses. Oecologia 2007; 152:179–89. pmid:17225157
    • 64. Terzer S, Wassenaar LI, Araguas-Araguas LJ, Aggarwal PK. Global isoscapes for delta O-18 and delta H-2 in precipitation: improved prediction using regionalized climatic regression models. Hydrol. Earth Syst. Sc. 2013; 17:4713–28.
    • 65. Peipoch M, Garcia E, Blesa A, Ribot M, Riera JL, Martí E. Contrasts among macrophyte riparian species in their use of stream water nitrate and ammonium: insights from 15N natural abundance. Aquat. Sci. 2014; 76:203–15.
    • 66. Mjelde M, Faafeng BA. Ceratophyllum demersum hampers phytoplankton development in some small Norwegian lakes over a wide range of phosphorus concentrations and geographical latitude. Freshwater Biol. 1997; 37:355–65.
    • 67. Solomon CT, Carpenter SR, Cole JJ, Pace ML. Support of benthic invertebrates by detrital resources and current autochthonous primary production: results from a whole-lake C-13 addition. Freshwater Biol. 2008; 53:42–54.