|New parasites and predators follow the introduction of two fish species to a subarctic lake: implications for food-web structure and functioning.|
|Jump to Full Text|
|PMID: 23053223 Owner: NLM Status: Publisher|
|Introduced species can alter the topology of food webs. For instance, an introduction can aid the arrival of free-living consumers using the new species as a resource, while new parasites may also arrive with the introduced species. Food-web responses to species additions can thus be far more complex than anticipated. In a subarctic pelagic food web with free-living and parasitic species, two fish species (arctic charr Salvelinus alpinus and three-spined stickleback Gasterosteus aculeatus) have known histories as deliberate introductions. The effects of these introductions on the food web were explored by comparing the current pelagic web with a heuristic reconstruction of the pre-introduction web. Extinctions caused by these introductions could not be evaluated by this approach. The introduced fish species have become important hubs in the trophic network, interacting with numerous parasites, predators and prey. In particular, five parasite species and four predatory bird species depend on the two introduced species as obligate trophic resources in the pelagic web and could therefore not have been present in the pre-introduction network. The presence of the two introduced fish species and the arrival of their associated parasites and predators increased biodiversity, mean trophic level, linkage density, and nestedness; altering both the network structure and functioning of the pelagic web. Parasites, in particular trophically transmitted species, had a prominent role in the network alterations that followed the introductions.|
|Per-Arne Amundsen; Kevin D Lafferty; Rune Knudsen; Raul Primicerio; Roar Kristoffersen; Anders Klemetsen; Armand M Kuris|
Related Documents :
|21674223 - Intake and potential health risk of butyltin compounds from seafood consumption in korea.
23647143 - Combustion of hydrotreated vegetable oil and jatropha methyl ester in a heavy duty engi...
8854823 - Eel (anguilla anguilla) and brown trout (salmo trutta) target species to assess the bio...
|Type: JOURNAL ARTICLE Date: 2012-9-28|
|Title: Oecologia Volume: - ISSN: 1432-1939 ISO Abbreviation: Oecologia Publication Date: 2012 Sep|
|Created Date: 2012-10-11 Completed Date: - Revised Date: -|
Medline Journal Info:
|Nlm Unique ID: 0150372 Medline TA: Oecologia Country: -|
|Languages: ENG Pagination: - Citation Subset: -|
|Department of Arctic and Marine Biology, Faculty of Biosciences, Fisheries and Economics, University of Tromsø, 9037, Tromso, Norway, firstname.lastname@example.org.|
|APA/MLA Format Download EndNote Download BibTex|
Journal ID (nlm-ta): Oecologia
Journal ID (iso-abbrev): Oecologia
Publisher: Springer-Verlag, Berlin/Heidelberg
© The Author(s) 2012
Received Day: 12 Month: 10 Year: 2011
Accepted Day: 31 Month: 8 Year: 2012
Electronic publication date: Day: 28 Month: 9 Year: 2012
pmc-release publication date: Day: 28 Month: 9 Year: 2012
Print publication date: Month: 4 Year: 2013
Volume: 171 Issue: 4
First Page: 993 Last Page: 1002
PubMed Id: 23053223
Publisher Id: 2461
|New parasites and predators follow the introduction of two fish species to a subarctic lake: implications for food-web structure and functioning|
Address: +47-77-644539 +47-77-646020 email@example.com
|Kevin D. LaffertyAff2|
|Armand M. KurisAff3|
Department of Arctic and Marine Biology, Faculty of Biosciences, Fisheries and Economics, University of Tromsø, 9037 Tromso, Norway
U.S. Geological Survey, Western Ecological Research Center, c/o Marine Science Institute, UC Santa Barbara, Santa Barbara, CA 93106 USA
Department of Ecology, Evolution and Marine Biology, and Marine Science Institute, University of California, Santa Barbara, CA 93106 USA
|Communicated by footnote: Communicated by Craig Osenberg.
Food webs depict ecological communities via networks of trophic relationships, and the structure and complexity of these networks influence community dynamics and stability (Bascompte et al. 2003; Dunne et al. 2005; Allesina and Pascual 2008). Beyond their importance in addressing general ecological questions, food-web analyses of species additions and deletions can also shed light on the impact of invasions and extinctions (Dunne et al. 2002; Srinivasan et al. 2007; Petchey et al. 2008). In particular, species introductions, in addition to increasing species richness, can alter food-web topology because a new species can act as a consumer or resource for existing species, or might be the critical resource needed for other consumers to invade the web. Introduced or invading species are furthermore likely to have hitchhiking parasites (Prenter et al. 2004; MacLeod et al. 2010), and parasites may also be affected by additions or extirpations of their hosts (Hechinger and Lafferty 2005), which can both affect food-web structure and functioning.
Most free-living species have several parasite species (Poulin and Morand 2004; Hudson et al. 2006). Although not often incorporated into food webs (Marcogliese and Cone 1997; Byers 2009), these infectious agents may affect network structure (Lafferty et al. 2006, 2008; Hernandez and Sukhedo 2008; Amundsen et al. 2009). Parasites are also likely to increase food-web complexity (Hudson et al. 2006) and alter ecosystem stability (Dobson et al. 2006; Wood et al. 2007). Inclusion of parasites in food webs can therefore change the way we view communities and ecosystem dynamics (Marcogliese and Cone 1997; Lafferty et al. 2008; Byers 2009; Poulin 2010), also including the consequences of introduced species (Torchin et al. 2003, 2005; Prenter et al. 2004; Thieltges et al. 2009). For instance, the replacement of a native snail by an introduced species (Torchin et al. 2005) had no effect on food-web topology unless one considered parasites (Lafferty and Kuris 2009); the introduced snail had a single parasite species and its replacement of the native species resulted in the extirpation of more than a dozen native parasite species. Alternatively, if introduced species do not extirpate native hosts, the diversity of parasites in a system could increase. For example, Torchin et al. (2003) estimated that, for every introduced free-living species, two parasite species on average are also introduced. As a result, an increase in the diversity of free-living species may also increase the diversity of parasitic species (Hechinger and Lafferty 2005).
Pelagic systems (both lacustrine and marine) have been used as model food webs (e.g. Havens 1997; Matveev 2003; Jonsson et al. 2005). Here, we evaluate how the introduction of two fish species altered the pelagic food web of a subarctic lake. Although the lake is a coupled benthic–pelagic system, our results pertain only to the pelagia. Two abundant fish species have a known history of deliberate introductions to Lake Takvatn, northern Norway (Jørgensen and Klemetsen 1995; Amundsen et al. 2007). Because they were introduced from nearby, some of their parasites and predators could have accompanied or followed them. Unfortunately, there were no observations of the food web before the introductions. Therefore, we used a conservative heuristic reconstruction of the pre-introduction web (the results were not sensitive to alternative reconstructions; see Online Resource). This retrospective analysis constitutes a practical implementation of the species addition/deletion approach that has been used to explore network impacts of invasions and extinctions (Srinivasan et al. 2007; Petchey et al. 2008). The analysis suggests that the fish introductions have led to new trophic links related to the arrival of parasites and predatory birds in the pelagic network. Hence, we hypothesised that the fish introductions affected the topology of the pelagic web, leading to distinct alterations of important food-web characteristics, including changes in the distribution of body sizes of species in the system. We further hypothesised that parasites have an important role for the structural and dynamic implications of these species additions.
The study lake, Takvatn (69°07′N, 19°05′E), is a subarctic, oligotrophic and dimictic lake situated 214 m above sea level in northern Norway with an area of 14.2 km2 and a maximum depth of ca 80 m. Mountains and a landscape dominated by birch (Betula pubescens) with scattered pine trees (Pinussylvestris) and patches of farmland surround the watershed. The climate is subarctic with an average air temperature in July of 13.2 °C. Midnight sun is present from late May until late July, whereas the polar night lasts from late November to late January. The ice-free season extends from June to November, with summer stratification from mid-July to the end of August. The maximum epilimnetic temperature is approximately 14 °C, and the thermocline occurs at 10–14 m depth. Secchi depth ranges between 14 and 17 m, and total phosphorus concentration does not exceed 5 μg l−1. The pH is neutral to slightly alkaline.
Detailed information related to phytoplankton, zooplankton, fish, birds and parasites and their trophic interactions are available from long-term ecological studies in Takvatn over the last three decades (e.g. Primicerio 2000; Amundsen et al. 2007, 2009; Persson et al. 2007). These data were used to develop a comprehensive topological food web for the pelagia of the lake (hereafter called the post-introduction food web; see Amundsen et al. 2009 for details).
The established food web is a source web, including only trophic relationships among species that arise from phytoplankton as the basal energy source. To best represent the available data, the food web was constrained to species using the open-water limnetic zone as their feeding habitat during the ice-free season of the lake (see also Havens 1997 for an extensive treatise of pelagic food webs). This is the period when the food web is most diverse, but it also means that our results do not apply to the winter food web (which, for instance, does not include birds). Winter dynamics are different in that there is lower diversity, productivity, and metabolism. With respect to parasites, only taxa completing their life cycle by using pelagic-dwelling species as their hosts have been included as members of the pelagic network.
Originally, brown trout Salmo trutta was the only fish species present in Takvatn, but after overexploitation of the trout population, arctic charr Salvelinus alpinus were deliberately introduced from the nearby lake Fjellfrøsvatn in 1930 (Amundsen et al. 2007). Takvatn and Fjellfrøsvatn are located 6 km apart in different tributaries of the same watershed. Three-spined stickleback Gasterosteus aculeatus were introduced to Takvatn in 1950 from Sagelvvatn, another nearby lake located 13 km away in a different watershed (Jørgensen and Klemetsen 1995). This was a deliberate introduction to improve forage for brown trout and arctic charr by adding a prey fish species. No direct connections exist between the three lake systems, and the aquatic communities of these postglacial lakes have been isolated for several thousand years. To our knowledge, both introductions included adults which were not inspected for the presence of parasites. Based on the knowledge of the established food web and the known history of the introductions of arctic charr and three-spined stickleback, we heuristically reconstructed the pelagic food web in Takvatn prior to the introduction of the fishes (hereafter called the pre-introduction food web). First, we removed arctic charr and three-spined stickleback and their associated links from the list of nodes in the current pelagic web. Thereafter, we omitted from the food web (1) parasite species that require arctic charr and/or three-spined stickleback to complete their life cycle, and (2) predator species that had no pelagic prey other than arctic charr and/or three-spined stickleback.
Our heuristic reconstruction of the pre-introduction network follows a conservative approach, only omitting species that rely upon arctic charr and/or three-spined stickleback as obligate nutritional resources and thus evidently could not have been present in the pelagic web prior to the arrival of these introduced species. Lacking from our reconstructed web are any species driven extinct by the introduced fishes. Top–down predation effects may have occurred following the fish introductions with potential consequences for the species composition at lower trophic levels. Arctic charr and three-spined stickleback are efficient zooplankton predators (e.g. Langeland and Nøst 1995), and their arrival may thus have negatively influenced predation-vulnerable species, resulting in changes in the composition of the zooplankton community. Similarly, the phytoplankton composition of the pre-introduction web may also have differed from the post-introduction web due to subsequent trophic cascade effects. Although no information is available to corroborate extinctions, we did consider plausible alternative webs where the fish introductions led to, e.g., the extinction of a large-bodied cladoceran as well as other potential scenarios for changes in the zooplankton and phytoplankton assemblages (see Online Resource). These alternative scenarios revealed only minor differences in important food-web parameters relative to the outcome of our conservative approach and no consequences for the overall conclusions were identified (Online Resource, Table A1), supporting our heuristic reconstruction and analyses. Any recent fish extinctions can also be ruled out because brown trout, arctic charr, and three-spined sticklebacks are the only possible fish species for Takvatn due to distributional restrictions from the postglacial period. Nonetheless, our approach can only investigate how the fish introductions appear to have facilitated the colonisation of new consumers to the system, and cannot evaluate potential extinctions associated with these introductions. Extinctions associated with these introductions are possible and could alter our interpretations.
Topological predator–prey food webs consist of an n × n matrix of n species, with predators as columns and prey as rows (Cohen 1978). Parasites are included by inserting them as columns with their hosts as rows (Lafferty et al. 2006). Binary entries (e.g. 0 or 1) are furthermore inserted in the matrix to indicate consumer-resource links, providing the necessary information to calculate relevant food-web metrics. To explore food-web properties and assess the impact of species additions on food-web structure, we calculated and compared several metrics of the pre- and post-introduction food webs, including species richness (S), number of links (L), linkage density (L/S), connectance (L/S2), and relative nestedness (see below). To help identify the source of any changes, we used the method advocated by Lafferty et al. (2006) to consider quadrants (subwebs) of a matrix organised by grouping free-living species into the first part of the species list and parasite species into the second part of the list. This allowed us to calculate metrics (1) just for free-living species (i.e. the predator–prey web), (2) for parasites and free-living species but excluding predator–parasite and parasite–parasite links, and (3) for parasites and free-living species including predator–parasite and parasite–parasite links (i.e. the total web including parasites). To estimate nestedness, we first calculated matrix temperature (a measure of absolute nestedness) using software described by Rodríguez-Gironés and Santamaría (2006). To allow easier comparison among networks, we then estimated relative nestedness after Bascompte et al. (2003). We also conducted robustness analyses of the before and after webs. Prior to robustness analysis, predator–parasite links were removed, as per Lafferty and Kuris (2009), which also contains details on the analyses. In short, species were removed in a random sequence. At each removal, species lacking resources (or for which any stage has no resources) were also removed. This is a very conservative way to measure interactions among species as it does not account for how consumers affect prey nor consider interaction strengths or species abundances (Dunne et al. 2002). Robustness, here, is the number of removals needed to reduce the number of species by half (Dunne et al. 2002). We took the modal robustness from 500 disassemblies and also recorded the first and third quartiles.
The reconstructed pre-introduction pelagic food web in Takvatn had 39 nodes, consisting of 8 basal species, 23 free-living predators, and 8 parasitic taxa (Fig. 1a). The basal species were all phytoplankton (Ph1–Ph8). The predators distributed themselves over four trophic levels (throughout we consider maximum trophic level). The first and second consumer levels comprised rotifers (Ro1–Ro8) and crustacean zooplankton (Cl1–Cl5 and Co1–Co4), whereas the third level included a single fish species (brown trout, Fi1) and the fourth and top level comprised five bird species (Bi1, Bi2, Bi3, Bi5 and Bi6). The eight parasite taxa present (PA1, PA2, PA3, PA5, PA9, PA11, PA12 and PA13) infected hosts at all trophic levels. 50 % of the parasite species were food transmitted, having hosts at two or more trophic levels.
Comparing the reconstructed pre-introduction web with the current web revealed that the introductions of arctic charr (Fi2) and three-spined stickleback (Fi3) to the lake resulted in significant changes in the structure of the pelagic food web, including increases in the numbers of nodes and links, as well as an increase in food chain lengths and the number of trophic levels (Fig. 1b; Table 1a). More specifically, the introduction of arctic charr facilitated the arrival of three new parasite species [Eubothrium salvelini (PA4), Philonema oncorhynchi (PA7) and Salmincola edwardsii (PA8)], which all rely upon the charr as their obligate host in this system and are not able to complete their life cycle in the sole presence of brown trout. Similarly, the introduction of three-spined stickleback resulted in the arrival of another two parasite species [Schistocephalus solidus (PA6) and Gyrodactylus arcuatus (PA10)] that both have the stickleback as an obligate host in their life cycle. Several of these parasite species also infect many native species in the web during the completion of their life cycles. The fish introductions furthermore opened the possibility for four new bird species [Clangula hyemalis (Bi4), Melanitta nigra (Bi7), Aythya fuligula (Bi8), and Bucephala clangula (Bi9)] to feed in the pelagic zone. These birds prey on stickleback and arctic charr, but are not able to use brown trout or zooplankton as prey and were thus not integrated in the pre-introduction pelagic web. They may have been foraging along the margins of the lake prior to the fish introductions as they can feed on some benthic invertebrates. However, these four bird species are new for the pelagic network as no suitable prey species were present in the pelagic community prior to the introductions of arctic charr and stickleback. In sum, after the introductions of the two fish species, the number of free-living predators in the pelagic food web increased from 23 to 29, and the number of parasitic taxa from 8 to 13. Furthermore, the number of trophic levels increased from 5 to 6 (Fig. 1; Table 1a).
The species composition and structure at the basal and first and second consumer levels were apparently unchanged from the pre- to the post-introduction pelagic food web, which may be a result of the conservative approach that was used for the reconstruction of the pre-introduction web. Large changes were, in contrast, evident for the higher trophic levels (birds, brown trout, parasites) following the introductions of charr and stickleback. At the third consumer level, the introduced three-spined stickleback became the principal consumer of zooplankton (Fig. 1). The introduced arctic charr were positioned at the fourth consumer level, preying on stickleback as well as zooplankton. The brown trout prey on the introduced stickleback and arctic charr, and have thus advanced two trophic levels up to the fifth consumer level (Fig. 1). This level also included six species of piscivorous birds (Bi1–Bi6), which consume both arctic charr and stickleback, whereas three bird species (Bi7–Bi9) that are only able to use sticklebacks as fish prey were located at the fourth trophic level. Both the pre- and post-introduction food webs were “wasp-waisted” (Fig. 1), with high diversity in the low and high trophic levels and an intermediate level represented only by a single species (brown trout or three-spined stickleback, respectively).
The fish introductions increased several aspects of system complexity. The reconstructed pre-introduction pelagic food web had 282 links, while the post-introduction web had 440 (Table 1a). The linkage density increased from 7.23 to 8.80, largely as a result of increased predator–parasite links. Connectance decreased (0.185 vs. 0.176) from the pre- to the post-introduction web (Table 1a). The degrees of a node (i.e. the number of links a species has to other species) increased from the pre-introduction (mean 13.4 ± 0.94 SE) to the post-introduction (mean 16.1 ± 0.99 SE) food-web (Fig. 2). Also, the mean degree of omnivory (i.e. the average number of trophic levels being fed on) increased from 1.58 (±0.17) to 2.05 (±0.16) from the pre- to the post-introduction web. Similarly, the number of natural enemies per consumer (i.e. the vulnerability of the species) showed a considerable increase from the pre- to the post-introduction web, particularly at the third and higher trophic levels (Fig. 3). Both the pre- and post-introduction food webs were nested in comparison to randomised matrices (Monte Carlo re-sampling, P < 0.0001). The relative nestedness increased from 0.16 to 0.25 from the pre- to the post-introduction web. High nestedness indicates that specialists are more likely to have a diet that is a subset of generalists than to have unique diets.
Parasites drove many of the observed changes in the food web as 79 % of the 158 new-established links after the species additions involved parasites. In particular, the importance of predator–parasite links increased after the species introductions (Table 1d), whereas only moderate differences in network metrics were seen between the pre- and post-introduction parasite–host subwebs (Table 1c). For the free-living predator–prey subweb (i.e. without the parasites included), there were also few differences in network metrics between the pre- and post-introduction networks (Table 1b). For instance, both linkage density and nestedness showed insignificant changes from the pre- to the post-introduction situation of the predator–prey subweb, whereas distinct changes were seen for the total web including parasites. A notable exception is connectance, which showed a larger decrease in the predator–prey web (−16 %) relative to the total web (−4 %). For the total web, robustness decreased from 45 % (quartile range 41–47 %) in the pre-introduction to 43 % (39–46 %) in the post-introduction network. In contrast, if parasites were excluded, robustness increased from 46 % (43–48 %) in the pre-introduction to 47 % (4–48 %) in the post-introduction web.
The body sizes of the free-living species in the pelagic food web increased with increasing trophic level, ranging over several orders of magnitude from basal phytoplankton at 10 μm to top predators at >50 cm in body length (Table 2). In general, there was an increase in body length of about one order of magnitude between consecutive trophic levels. However, in the pre-introduction web, the centimetre size class (10−2 m) was missing due to the absence of three-spined stickleback and arctic charr and the fact that native brown trout use tributary streams as nursery areas and only enter the lake at sizes >10 cm (Persson et al. 2007).
The introduction of arctic charr and three-spined stickleback altered the Takvatn pelagic food web, increasing species richness beyond the mere addition of the two introduced species by facilitating the establishment of several hitchhiking or independently arriving parasite species and constituting essential food resources for new avian predators. Hence, the introductions of the 2 fish species facilitated the addition of another 9 species to the pelagic community, increasing richness from 39 to 50 species. These species additions also resulted in a large increase in the number of trophic links, and the topology of the food web changed dramatically. The increases in numbers of nodes and links were accompanied by an increase in food-chain lengths and in the total number of trophic levels of the web. Moreover, the complexity of the web increased, clearly manifested by increases in linkage density, degree distribution, vulnerability to natural enemies, omnivory, and nestedness, which potentially also has large consequences for network functioning and stability (e.g. Allesina and Pascual 2008; Lafferty et al. 2008). The connectance changed little in the total pelagic web, but decreased in the predator–prey web. Other important food-web characteristics such as linkage density and nestedness exhibited few changes from the pre- to the post-introduction predator–prey web. Jonsson et al. (2005) similarly found modest effects on the pelagic predator–prey web of Tuesday Lake following a food-web manipulation including both addition and removal of fish species. Parasites were not included in the Tuesday Lake studies, but Jonsson et al. acknowledged their potential importance and also called for an exploration of the role of parasites in food-web manipulations such as species additions (Jonsson et al. 2005). Our study indeed confirms that parasites can have an important role in food-web alterations following species introductions. More specifically, the large differences observed in responses between the predator–prey and the total web were due to the fact that most of the new links were parasite-associated; an observation that underpins the importance of taking parasites into considerations in food-web studies (see also, e.g., Marcogliese 2003, 2005; Lafferty et al. 2008; Beckerman and Petchey 2009; Poulin 2010).
Due to the large modifications in species composition following the introductions of the two fish species to Takvatn, there were also large alterations in functional traits within the food web related to changes in size–structure interactions and foraging efficiencies within the network; impacts that also influence parasite transmission within the system (see also Poulin and Leung 2011). At 10−2 m in length, stickleback and juvenile arctic charr became a new intermediate size class in the pelagia of Takvatn (see Table 2), enhancing the size coherence within the pelagic web and resulting in (1) increased predation on crustacean zooplankton (see below), (2) a two-step advancement in trophic position of brown trout, and (3) the additional invasion of the pelagic web by bird species feeding on stickleback and juvenile charr. Brown trout, the only fish species present in the pre-introduction web, make limited use of zooplankton as prey, and arctic charr and stickleback are known to be far more efficient zooplankton predators (Langeland and Nøst 1995). Hence, the pre-introduction crustacean zooplankton community in Takvatn must have experienced much less predation from brown trout alone than in the subsequent presence of the introduced arctic charr and three-spined stickleback. While it is possible that the introduced fish drove some large zooplankton extinct, it is hard to reconstruct pre-invasion food webs. We found that an inclusion of the most likely extinction (Bythotrephes longimanus) in the reconstructed pre-invasion web did not alter the general findings (see Online Resource). However, whether or not extinctions occurred, we do not wish to understate the importance of fish predation on this system. Increased fish predation on crustacean zooplankton changes the zooplankton community towards more mobile species like copepods and towards smaller species, in particular within the cladocerans (e.g. Gliwicz and Pijanowska 1989). Accordingly, the post-introduction crustacean zooplankton community in Takvatn has been dominated by small-sized cladocerans and copepods (Dahl-Hansen 1995; Primicerio 2000), which have also become important prey of planktivorous arctic charr and three-spined stickleback (Amundsen and Klemetsen 1988; Jørgensen and Klemetsen 1995). Several fish parasites (including Diphyllobothrium spp., Eubothrium spp., S. solidus, P. oncorhynchi, and Proteocephalus sp.) use copepods as intermediate hosts, and predation-induced changes in the zooplankton community have thus likely enhanced the completion of the life cycles of these parasites (Knudsen 1995). Intensified piscivory by birds related to the presence of three-spined stickleback and arctic charr has furthermore increased the transmission rates of several bird parasites that use fish as intermediate hosts (Knudsen et al. 1996). These trophically transmitted parasites are highly connected species that are present at several trophic levels (Amundsen et al. 2009), and they contribute to the complexity of the network, thus highlighting the particular importance of food-transmitted parasites in food webs (see also Lafferty et al. 2006, 2008; Hernandez and Sukhedo 2008; Poulin and Leung 2011).
The introduction of three-spined stickleback has likely increased the transmission rate and abundance of food-transmitted parasites in both piscivorous birds and fish in the system as this small-sized fish is a common prey of these predators (e.g. Whoriskey and Fitzgerald 1985; L’Abée-Lund et al. 1992; Amundsen 1994) and also acts as an intermediate host for several of the present parasite species (Amundsen et al. 2009). This is true for the two Diphyllobothrium species that are transmitted as plerocercoid larvae from sticklebacks as well as small- and intermediate-sized arctic charr and brown trout to their final bird hosts (Vik 1957; Halvorsen 1970). The plerocercoid larvae can also use large piscivorous individuals of brown trout and arctic charr as paratenic hosts (Halvorsen and Wissler 1973). Furthermore, predation rates may increase along with transmission due to parasite-induced host behavioural modifications that make infected individuals more vulnerable to predation (Moore 2002). In Takvatn, up to 60 % of sticklebacks older than 1 year may carry larvae of the tapeworm S. solidus during summer and early autumn (P.-A. Amundsen et al., unpublished data). Infections with S. solidus render stickleback more vulnerable to predation both from piscivorous birds and fish due to behavioural manipulation of the hosts (e.g. Barber et al. 2004). This host–behaviour manipulation enhances the transmission of S. solidus to their final hosts, but will also facilitate the transmission of other larval parasites infecting stickleback, emphasising the strong and complex food-web interrelationships between predation and parasitism.
Our approach of reconstructing the food web to estimate conditions prior to invasion was dictated by a lack of records about the historical food web. Ideally, we would have also been able to study replicated scenarios, but this option was not available to us. Future studies could compare the food webs of lakes with and without introduced fishes. Our results provide a starting point for such an effort. Similarly, we limited ourselves to the pelagic component of the food web because this was the part of the system where we had sufficient data. Our view of the system could change if we were able to add benthic species to the web. This will be an area of future work. We have more detailed ecological data on some of the species and their feeding interactions, but the only way for us to capture the complexity of the entire system was to use the topological abstraction. Although topological webs like ours provide a simple description of complexity and are amenable to descriptive statistics, they sacrifice important aspects of how energy flows through the system.
In conclusion, our study reveals large food-web alterations in the pelagic community following the introduction of arctic charr and three-spined stickleback into Lake Takvatn. Both species have become engaged in many trophic links and constitute important hubs in the post-introduction network. The introduction of these two fishes also facilitated several additional species entering the pelagic network, including new parasite species and avian predators, leading to large changes in species richness and food-web structure. Our study also reveals several associated consequences for the functioning of the pelagic web with potential implications for robustness, resilience and stability of the ecological community. Parasites, in particular trophically transmitted species, have a prominent role in the structure and function of this food web. Most notably, network topology and trophic dynamics can be altered after the addition of new free-living species and their associated parasites.
We thank staff and students of the Freshwater Ecology Group at the University of Tromsø for their invaluable support in the Takvatn studies, and in particular L. Dalsbø and J. Evjen for their enduring assistance in the field and laboratory work. N. Foster and M. Torchin provided comments on a draft of the paper. The University of Tromsø and the Norwegian Research Council contributed financial support. Any use of trade, product or firm names in this publication is for descriptive purposes only and does not imply endorsement by the US government.
This article is distributed under the terms of the Creative Commons Attribution License which permits any use, distribution, and reproduction in any medium, provided the original author(s) and the source are credited.
|Allesina S,Pascual M. Network structure, predator-prey modules and stability in large food websTheor EcolYear: 20081556410.1007/s12080-007-0007-8|
|Amundsen P-A (1994) Piscivory and cannibalism in Arctic charr. J Fish Biol 45 (Suppl A):181–190. doi:10.1111/j.1095-8649.1994.tb01092.x|
|Amundsen P-A,Klemetsen A. Diet, gastric evacuation rates and food consumption in a stunted population of Arctic charr (Salvelinus alpinus L.) in Takvatn, northern NorwayJ Fish BiolYear: 19883369770910.1111/j.1095-8649.1988.tb05515.x|
|Amundsen P-A,Knudsen R,Klemetsen A. Intraspecific competition and density dependence of food consumption and growth in Arctic charrJ Anim EcolYear: 20077614915810.1111/j.1365-2656.2006.01179.x17184363|
|Amundsen P-A,Lafferty KD,Knudsen R,Primicerio R,Klemetsen A,Kuris AM. Food web topology and parasites in a subarctic lakeJ Anim EcolYear: 20097856357210.1111/j.1365-2656.2008.01518.x19175443|
|Barber I,Walker P,Svensson PA. Behavioural responses to simulated avian predation in female three spined sticklebacks: the effect of experimental Schistocephalus solidus infectionsBehaviourYear: 20041411425144010.1163/1568539042948231|
|Bascompte J,Jordano P,Melian CJ,Olesen JM. The nested assembly of plant-animal mutualistic networksProc Natl Acad Sci USAYear: 20031009383938710.1073/pnas.163357610012881488|
|Beckerman AP,Petchey OL. Infectious food websJ Anim EcolYear: 20097849349610.1111/j.1365-2656.2009.01538.x19374660|
|Byers JE. Including parasites in food websTrends ParasitolYear: 200925555710.1016/j.pt.2008.11.00319101206|
|Cohen JE. Food webs and niche spaceYear: 1978PrincetonPrinceton University Press|
|Dahl-Hansen GAP. Long-term changes in crustacean zooplankton—the effects of a mass removal of Arctic charr, Salvelinus alpinus (L.), from an oligotrophic lakeJ Plankton ResYear: 1995171819183310.1093/plankt/17.9.1819|
|Dobson AP,Lafferty KD,Kuris AM. Pascual M,Dunne JAParasites and food websEcological networks: linking structure to dynamics in food websYear: 2006OxfordOxford University Press119135|
|Dunne JA,Williams RJ,Martinez ND. Network structure and biodiversity loss in food webs: robustness increases with connectanceEcol LettYear: 2002555856710.1046/j.1461-0248.2002.00354.x|
|Dunne JA,Brose U,Williams RJ,Martinez ND. Belgrano A,Scharler UM,Dunne JA,Ulanowicz REModelling food-web dynamics: complexity-stability implicationsAquatic food webs: an ecosystem approachYear: 2005OxfordOxford University Press117129|
|Gliwicz ZM, Pijanowska J (1989) The role of predation in zooplankton succession. In: Sommer U (ed) Plankton ecology: succession in plankton communities. Springer, Berlin, pp 253–296|
|Halvorsen O. Studies of the Helminth fauna of Norway XV: on the taxonomy and biology of plerocercoids of Diphyllobothrium Cobbold, 1858 (Cestoda, Pseudophyllidea) from north-western EuropeNytt Mag ZoolYear: 197018113174|
|Halvorsen O,Wissler K. Studies of the helminth fauna of Norway. XXVIII. An experimental study of the ability of Diphyllobothrium latum (L.), D. dendriticum (Nitzsch), and D. ditremum (Creplin) (Cestoda, Pseudophyllidea) to infect paratenic hostsNorw J ZoolYear: 197321201210|
|Havens KE. Unique structural properties of pelagic food websOikosYear: 199778758010.2307/3545802|
|Hechinger RF,Lafferty KD. Host diversity begets parasite diversity: bird final hosts and trematodes in snail intermediate hostsProc R Soc Lond BYear: 20052721059106610.1098/rspb.2005.3070|
|Hernandez AD,Sukhedo MVK. Parasites alter the topology of a stream food web across seasonsOecologiaYear: 200815661362410.1007/s00442-008-0999-918305960|
|Hudson PJ,Dobson AP,Lafferty KD. Is a healthy ecosystem one that is rich in parasites?Trends Ecol EvolYear: 20062138138510.1016/j.tree.2006.04.00716713014|
|Jonsson T,Cohen JE,Carpenter SR. Food webs, body size, and species abundance in ecological community descriptionAdv Ecol ResYear: 20053618410.1016/S0065-2504(05)36001-6|
|Jørgensen L,Klemetsen A. Food resource partitioning of arctic charr, Salvelinus alpinus (L.) and three-spined stickleback, Gasterosteus aculeatus L., in the littoral zone of Takvatn in northern NorwayEcol Freshw FishYear: 19954778410.1111/j.1600-0633.1995.tb00120.x|
|Knudsen R. Relationships between habitat, prey selection and parasite infections in Arctic charr (Salvelinus alpinus)Nordic J Freshw ResYear: 199571333344|
|Knudsen R,Klemetsen A,Staldvik FJ. Parasites as indicators of individual feeding specialization in Arctic charr during winter in northern NorwayJ Fish BiolYear: 1996481256126510.1111/j.1095-8649.1996.tb01819.x|
|L’Abée-Lund JH, Langeland A, Sægrov H (1992). Piscivory by brown trout Salmo trutta L. and Arctic charr Salvelinus alpinus (L.) in Norwegian Lakes. J Fish Biol 41:91–101. doi:10.1111/j.1095-8649.1992.tb03172.x|
|Lafferty KD,Kuris AM. Parasites reduce robustness because they are sensitive to secondary extinction in the Carpinteria salt marshPhilos Trans R Soc Lond BYear: 20093641659166310.1098/rstb.2008.022019451117|
|Lafferty KD,Dobson AP,Kuris AM. Parasites dominate food web linksProc Natl Acad Sci USAYear: 2006103112111121610.1073/pnas.060475510316844774|
|Lafferty KD,Allesina S,Arim M,Briggs CJ,DeLeo G,Dobson AP,Dunne JA,Johnson PTJ,Kuris AM,Marcogliese DJ,Martinez ND,Memmott JP,Marquet A,McLaughlin JP,Mordecai EA,Pascual M,Poulin R,Thieltges DW. Parasites in food webs: the ultimate missing linksEcol LettYear: 20081153354610.1111/j.1461-0248.2008.01174.x18462196|
|Langeland A,Nøst T. Gill raker structure and selective predation on zooplankton by particulate feeding fishJ Fish BiolYear: 19954771973210.1111/j.1095-8649.1995.tb01937.x|
|MacLeod CJ,Paterson AM,Tompkins DM,Duncan RP. Parasites lost—do invaders miss the boat or drown on arrival?Ecol LettYear: 20101351652710.1111/j.1461-0248.2010.01446.x20455925|
|Marcogliese DJ (2003) Food webs and biodiversity: are parasites the missing link? J Parasitol 82(S):389–399|
|Marcogliese DJ. Parasites of the superorganism: are they indicators of ecosystem health?Internat J ParasitolYear: 20053570571610.1016/j.ijpara.2005.01.015|
|Marcogliese DJ,Cone DK. Food webs: a plea for parasitesTrends Ecol EvolYear: 19971232032510.1016/S0169-5347(97)01080-X21238094|
|Matveev V. Testing predictions of the lake food web theory on pelagic communities of Australian reservoirsOikosYear: 200310014916110.1034/j.1600-0706.2003.11651.x|
|Moore J. Parasites and the behavior of animalsYear: 2002OxfordOxford University Press|
|Mullarney K,Svensson L,Zetterström D,Grant PJ. Birds of EuropeYear: 2000PrincetonPrinceton University Press|
|Persson L,Amundsen P-A,De Roos AM,Klemetsen A,Knudsen R,Primicerio R. Culling prey promotes predator recovery—alternative states in a whole-lake experimentScienceYear: 20073161743174610.1126/science.114141217588929|
|Petchey OL,Eklöf A,Borvall C,Ebenman B. Trophically unique species are vulnerable to cascading extinctionsAm NatYear: 200817156857910.1086/58706818419567|
|Poulin R. Network analysis shining light on parasite ecology and diversityTrends ParasitolYear: 20102649249810.1016/j.pt.2010.05.00820561821|
|Poulin R,Leung TLF. Body size, trophic level, and the use of fish as transmission routes by parasitesOecologiaYear: 201116673173810.1007/s00442-011-1906-321249395|
|Poulin R, Morand S (2004) Parasite biodiversity. Smithsonian Institution Press, Washington D.C|
|Prenter J,MacNeil C,Dick JTA,Dunn AM. Roles of parasites in animal invasionsTrends Ecol EvolYear: 20041938539010.1016/j.tree.2004.05.00216701290|
|Primicerio R. Seasonal changes in vertical distribution of zooplankton in an oligotrophic, subarctic lake (Lake Takvatn, Norway)LimnologicaYear: 20003030131010.1016/S0075-9511(00)80021-3|
|Rodríguez-Gironés MA,Santamaría L. A new algorithm to calculate the nestedness temperature of presence-absence matricesJ BiogeogrYear: 20063392493510.1111/j.1365-2699.2006.01444.x|
|Srinivasan UT,Dunne JA,Harte J,Martinez ND. Response of complex food webs to realistic extinction sequencesEcologyYear: 20078867168210.1890/06-097117503595|
|Streble H, Krauter D (2006) Das Leben im Wassertropfen. Mikroflora und Mikrofauna des Süßwassers. Ein Bestimmungsbuch. Kosmos, Stuttgart|
|Thieltges DW,Reise K,Prinz K,Jensen KT. Invaders interfere with native parasite-host interactionsBiol InvasionsYear: 2009111421142910.1007/s10530-008-9350-y|
|Torchin ME,Lafferty KD,Dobson AP,McKenzie VJ,Kuris AM. Introduced species and their missing parasitesNatureYear: 200342162863010.1038/nature0134612571595|
|Torchin ME,Byers JE,Huspeni TC. Differential parasitism of native and introduced snails: replacement of a parasite faunaBiol InvasionsYear: 2005788589410.1007/s10530-004-2967-6|
|Vik R. Studies of the helminth fauna of Norway I. Taxonomy and ecology of Diphyllobothrium norvegicum n.sp. and the plerocercoid of Diphyllobothrium latum (L.)Nytt Mag ZoolYear: 195752593|
|Whoriskey FG,Fitzgerald GJ. The effects of bird predation on an estuarine stickleback (Pisces: Gasterosteidae) communityCan J ZoolYear: 19856330130710.1139/z85-046|
|Wood CL,Byers JE,Cottingham KL,Altman I,Donahue MJ,Blakeslee AMH. Parasites alter community structureProc Natl Acad Sci USAYear: 20071049335933910.1073/pnas.070006210417517667|
Summary of food-web metrics in the pre- and post-introduction pelagic web of the subarctic lake Takvatn including (a) the total web including parasites, (b) the predator–prey subweb, (c) the parasite–host subweb, and (d) the predator–parasite subweb
|Parameters||(a) Total web||(b) Predator–prey subweb||(c) Parasite–host subweb||(d) Predator–parasite subweb|
|Pre-introd. web||Post-introd web||Pre-introd. web||Post-introd web||Pre-introd web||Post-introd. web||Pre-introd. web||Post-introd. web|
|No. of consumer levels||4||5||4||5||–||–||–||–|
|No. of species||39||50||31||37||39||50||39||50|
|Potential no. of links||1,521||2,500||961||1,369||248||481||248||481|
|Observed no. of links||282||440||165||198||43||75||74||167|
aOmnivory average no. of trophic levels being fed on
Body size (length ranges) of common free-living species in the Takvatn pelagic food web and their trophic level in the pre- and post-introduction webs
|Taxon||Species||Body size||Trophic level|
|Pre-introd. web||Post-introd. web|
|Phytoplanktona||Asterionella formosa||40–130 μm||0||0|
|Cyclotella spp.||10–40 μm||0||0|
|Ceratium hirundinella||200–300 μm||0||0|
|Gymnodinium helveticum||20–30 μm||0||0|
|Rotifersa||Keratella cochlearis||80–320 μm||1||1|
|Kellicottia longispina||450–860 μm||1||1|
|Conochilus unicornis||200–380 μm||1||1|
|Asplanchna priodonta||420–1,500 μm||2||2|
|Cladoceransb||Daphnia galeata||0.6–2 mm||1||1|
|Bosmina spp.||0.2–0.9 mm||1||1|
|Copepodsb||Cyclops scutifer||0.4–1.5 mm||2||2|
|Eudiaptomus graciloides||0.4–1.3 mm||2||2|
|Fishb||Three-spined stickleback||1–7 cm||Absent||3|
|Arctic charr||5–45 cm||Absent||4|
|Brown trout||11–60 cm||3||5|
|Gulls and terns||33–45 cm||4||5|
|Mergansers and loons||60–73 cm||4||5|
aStreble and Krauter (2006) (literature-retrieved data)
cMullarney et al. (2000) (literature-retrieved data)
Keywords: Keywords Non-native species, Pelagic community, Species additions, Topology, Trophic interactions.
Previous Document: Increased production of soluble inducible costimulator in patients with diffuse cutaneous systemic s...
Next Document: Testing Bergmann's rule and the Rosenzweig hypothesis with craniometric studies of the South America...