Plant and animal population sizes inevitably change following habitat loss, but the mechanisms underlying these changes are poorly understood. We experimentally altered habitat volume and eliminated top trophic levels of the food web of invertebrates that inhabit rain-filled leaves of the carnivorous pitcher plant Sarracenia purpurea. Path models that incorporated food-web structure better predicted population sizes of food-web constituents than did simple keystone species models, models that included only autecological responses to habitat volume, or models including both food-web structure and habitat volume. These results provide the first experimental confirmation that trophic structure can determine species abundances in the face of habitat loss.
Citation: Gotelli NJ, Ellison AM (2006) Food-Web Models Predict Species Abundances in Response to Habitat Change. PLoS Biol 4(10): e324. doi:10.1371/journal.pbio.0040324
Academic Editor: Robert Holt, University of Florida, United States of America
Received: January 22, 2006; Accepted: August 1, 2006; Published: September 26, 2006
Copyright: © 2006 Gotelli and Ellison. 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.
Funding: Supported by National Science Foundation grants DEB 02–34710, 02–35128, and 05–41936 to NJG and DEB 98–05722, 02–35128, and 05–41680 to AME.
Competing interests: The authors have declared that no competing interests exist.
The loss of natural habitat area often is accompanied by the disappearance of large-bodied top predators and the upper trophic levels of food webs [1–3]. However, several pieces of evidence suggest that habitat area alone may be insufficient to predict changes in population size. Predictions of ecological models [4,5], patterns of food-web structure in small versus large habitat fragments , and recent observations of collapsing island communities [1,7] all suggest that trophic interactions must be considered in order to predict how abundances of populations will change in the face of habitat loss and alteration. However, existing tests of the role of trophic interactions in determining species abundances as habitats contract are correlative only. In this study, we provide the first evidence from a controlled field experiment for the importance of trophic structure in controlling abundances of multiple species in an aquatic food web. Moreover, we demonstrate that models of trophic structure account for the results better than do simpler models that focus only on responses of individual species to changes in habitat size or structure, or models that include both food-web structure and habitat volume.
For multitrophic assemblages, two broad classes of community models predict the potential responses of populations to habitat change. (1) Single-factor models emphasize the unique responses of individual species to variation in habitat area. This framework includes island biogeographic models , as well as single-species demographic analyses  and assessments of extinction risk. Single-factor models also include keystone species effects, which emphasize responses of populations to changes in the abundance of a single keystone species, such as a top predator [10,11]. This framework includes much current research on habitat alterations by foundation species  and ecosystem engineers . (2) Food-web models emphasize the shifts in abundance that result from multiple trophic interactions and the transfer of energy and biomass through a food web. This framework includes top-down and bottom-up processes , trophic cascades , and more complex interactions across multiple trophic levels .
Unfortunately, published studies of the effects of habitat contraction have relied on conventional analyses that do not explicitly compare these alternative frameworks [17,18]. Although analysis of variance and other statistical protocols can quantify community change, they cannot be used to distinguish between simple responses of species to habitat contraction (single-factor volume model) and more complex responses to changes in the abundance of other species (food-web and keystone species models). A third possibility is that trophic responses dominate the responses, even in the face of habitat alterations. In this study, we used realistic field manipulations of habitat volume and removal of top trophic levels of entire aquatic communities. These manipulations induced major alterations in habitat size and community structure that have been studied previously in nonexperimental settings . For the first time, we have experimentally assessed the relative importance of autecological responses, keystone species effects, and trophic interactions in accounting for changes in species' abundance.
The Aquatic Food Web of Sarracenia
The macroinvertebrate community associated with the northern pitcher plant Sarracenia purpurea (Figure 1) is a model system for testing mechanisms controlling abundance in the face of habitat change . S. purpurea is a long-lived perennial plant that grows in peat bogs and seepage swamps throughout southern Canada and the eastern United States . The plant grows as a rosette and produces a set of six to 12 new tubular leaves each year. During the growing season, leaves open approximately every 17 d and fill with rain water; an aquatic food web quickly develops in these water-filled leaves . Leaves are photosynthetically most active in their first year, but persist, capture prey, and are used as macroinvertebrate habitat for 1 to 2 y . The base of the food web is captured arthropod prey (predominantly ants and flies), which is shredded and partially consumed by midge (Metriocnemus knabi) and sarcophagid fly (Fletcherimyia fletcheri) larvae . Shredded prey are then processed by a subweb of bacteria and protozoa , which respectively are prey to filter-feeding rotifers (Habrotrocha rosi) and mites (Sarraceniopus gibsonii). Larvae of the pitcher plant mosquito Wyeomyia smithii feed on bacteria, protozoa, and rotifers . Large (third instar) larvae of F. fletcheri feed on rotifers and small (first and second instar) larvae of W. smithii . Thus, the Sarracenia food web exhibits the same complex linkages across multiple trophic levels that characterize other aquatic and terrestrial food webs . Furthermore, the same assemblage of macroinvertebrate species can be found associated with S. purpurea throughout its broad geographic range—from the Florida panhandle to Labrador and west to the Canadian Rocky Mountains .
Each leaf of the northern pitcher plant Sarracenia purpurea contains an entire aquatic food web, with a resource base consisting of captured arthropod prey. Sarracenia occurs in Sphagnum bogs and seepage swamps throughout the eastern United States and Canada (sites at which similar species assemblages can be found  are shown as black dots).
(Photo Montage: Aaron M. Ellison)
In a replicated field experiment, we simultaneously manipulated habitat volume (adding or removing water from leaves) and simplified the trophic structure of the Sarracenia food web (by retaining or removing larvae of all three dipterans: Metriocnemus, Wyeomyia, and Fletcherimyia). We measured the abundance of the resident species in each replicate leaf (Dataset S1) and compared the fit of food-web models, keystone species models, and autoecological response models to the data (see Materials and Methods).
Model Fit Statistics
The overall fit of the set of ecological models to the abundance data was food-web models > single factor models (Figure 2, lower panels versus upper panels). The fit of the food-web and keystone models was not improved by incorporating partial links or complete links with habitat volume (Figure 2, left panel versus center and right panels). The single best-fitting model was the Wyeomyia keystone model (blue symbol and dashed line in Figure 2), and the worst-fitting model was the Sarraceniopus partial-volume response model. The best-fitting group of models was composed of the four food-web models with no volume linkage (red symbols and red band in Figure 2). These models and the Wyeomyia keystone model did not reject the statistical hypothesis of a “close fit” with the variance-covariance structure of the data. Candidate models of other keystone species or of other food-web models with volume linkage performed more poorly.
The smaller the index, the better is the fit of the data to the predictions of the model. The upper row of panels includes all single-factor models (Tables S3 to S6). The single-factor model that has only habitat volume as a predictor variable (see Table S3) is indicated by a triangle to the left of the dashed vertical line. The lower row of panels includes all food-web models (Tables S7 to S9). Food-web models designated with a (B) include a latent variable to represent bacteria. The first column of panels includes models with no links to habitat volume (Tables S3, S4, and S7). The second column of panels includes models with limited links to habitat volume (Tables S5 and S8). For the bottom-up food-web models, the link was from habitat volume to prey abundance, and for the top-down food-web models, the link was from habitat volume to the abundances of Fletcherimyia and Wyeomyia. The third column of panels depicts models with all taxa linked to habitat volume (Tables S6 and S9). The single best-fitting model (Wyeomyia keystone with neither partial nor complete links with habitat volume) is indicated with a blue symbol. The group of best-fitting models (food-web models with no volume links) is indicated with red symbols. For reference in each panel, the cross-validation index for the Wyeomyia model is indicated by a dashed blue line, and the average cross-validation for the food-web models with no habitat links is indicated by a solid red band.
The Wyeomyia keystone model correctly identified the role of mosquito larvae as predators of rotifers and as prey of Fletcherimyia (Figure 3A) . These path analyses are consistent with other studies suggesting that Wyeomyia is a keystone predator with both top-down and bottom-up effects in this food web [25,27]. The latent variable analysis of the food-web models suggested that strong trophic links were associated with bacteria (Figure 3B), which supports the view of the Sarracenia food web as a commensal processing chain in which shredders, detritivores, and filter feeders sequentially process and transform arthropod prey . Although it fit the data relatively poorly (Figure 2), the simple model linking species abundances only to volume identified a strong link from pitcher-plant volume to prey abundance and a strong link from volume to Metriocnemus abundance (Figure 3C). Weaker links were from volume to Wyeomyia abundance and Habrotrocha abundance, and all other links in this model were close to zero.
Each circle indicates a taxon abundance, prey abundance, or average habitat volume, and each link indicates a hypothesized cause-and-effect relationship within a particular model. Standardized path coefficients are estimated for each link, and the size of the arrow is roughly proportional to the magnitude of the coefficient.
(A) Wyeomyia single-factor (“keystone”) model in which abundances of all taxa are determined only by direct links with the filter-feeding mosquito larva W. smithii.
(B) Bottom-up trophic model in which abundances are controlled by links from prey to predator. The triangle represents a latent variable for bacteria, which was not directly measured, but whose trophic linkages (shown in red) in the Sarracenia web are known [21,24].
(C) Single-factor volume model, in which the abundance of each taxon is determined solely by habitat volume.
The overall superiority of the Wyeomyia keystone model and the simple food-web models demonstrates the importance of trophic interactions in controlling species abundances in an aquatic food web. Even though habitat volume was radically altered by our manipulations (Table S1), the abundances of species in the food web were better predicted overall by trophic interaction models than by direct measures of habitat volume or the abundance of basal prey resources alone, or by models linking habitat volume partially or completely to food-web structure (Figure 2). Although a few taxa did show correlations with habitat volume (Figure 3C), the fit of the food-web models to the abundance data was worse when habitat volume linkages were included (Figure 2). Our experimental study confirms the importance of trophic interactions that have been observed on terrestrial islands that have been sharply reduced in area  or altered by an invasive species . Explicit statistical models of the trophic structure of communities may provide more accurate forecasts of plant and animal abundances in the face of habitat change than models that focus on the idiosyncratic responses of individual species to habitat loss alone.
Materials and Methods
At Moose Bog, a peat bog of northeastern Vermont, United States , we assigned 50 adult pitcher plants randomly to one of five treatment groups in which we experimentally manipulated the water level of the leaf and/or removed all of the dipteran larvae from the aquatic food web (see Protocol S1). The food web in each of three leaves of the plant underwent census nondestructively once a week through the summer 2000 growing season. We calculated average abundance of each taxon for each food web during the interval that the leaf was open. This averaging eliminated pseudoreplication and autocorrelation of temporal census data. Our analyses thus considered the average conditions that communities achieve in the face of sustained habitat alteration. The experimental treatments significantly altered average invertebrate abundances and generated substantial variation among leaves in habitat volume, prey availability, and assemblage structure (Table S1).
We used path analysis  (a form of structural equation modeling) to compare the fit of these abundance data to different models of community organization (see Protocol S1). We developed a priori models of cause-and-effect to potentially account for patterns of covariation in abundance of taxa among leaves that had been manipulated experimentally (Table S2). Two groups of models were developed: (1) single-factor models, in which abundances of each species respond individually to differences in habitat volume (Table S3), prey resources, or the presence of other species (“keystone” models; Tables S4 to S6), and (2) food-web models, in which species abundances respond to direct and indirect trophic interactions (Tables S7 to S9). We did not model the experimental treatments as dummy categorical variables because the habitat volume and dipteran manipulations were not orthogonal and because habitat volume and dipteran abundance are more appropriately treated as continuous variables, along with the other variables in our models. For the food-web models, we also introduced a latent variable to represent the effects of the unmeasured bacterial component of the assemblage.
The single-factor and food-web models were orthogonally crossed with three other groupings, based on the inclusion of habitat volume (= leaf pitcher liquid volume) in the path models. In the first grouping (left pair of panels in Figure 2), habitat volume was not included in the models, so that abundances were predicted entirely on the basis of single-species effects (Table S4) or trophic interactions (Table S7). In the second grouping (middle pair of panels in Figure 2), we introduced habitat volume with only a link to the focal taxon (Tables S5 and S8). In the bottom-up food-web models, this link was from habitat volume to prey, and in the top-down food-web models, the link was from habitat volume to the abundances of Fletcherimyia and Wyeomyia, the two top predators in this food web (Table S8). In the third grouping (right pair of panels in Figure 2), we modeled links from habitat volume to all food-web components (Tables S6 and S9). All models were fit to the observed correlation matrix for the Sarracenia food web (Table S2).
Dataset S1. Average Abundances of Inquilines, Average Habitat Volume, Leaf Age, and Treatment
(283 KB DOC)
Protocol S1. Experimental Manipulations, Model Structure, and Path Model Analysis
(192 KB DOC)
Table S1. Split-Plot Analysis of Variance Results for Tests of Treatment and Leaf Age on Inquiline Abundances
(31 KB DOC)
Table S2. Observed Correlation Matrix for Path Analyses
(34 KB DOC)
Table S3. Path Structure for Simple Volume Model
(34 KB DOC)
Table S4. Path Structure for Wyeomyia Keystone Species Model
(33 KB DOC)
Table S5. Path Structure for Wyeomyia Keystone Species Model with Simple Volume Linkage
(33 KB DOC)
Table S6. Path Structure for Wyeomyia Keystone Species Model with Full Volume Linkages
(33 KB DOC)
Table S7. Path Structure for Top-Down Food-Web Model
(33 KB DOC)
Table S8. Path Structure for Top-Down Food-Web Model with Simple Volume Linkage
(33 KB DOC)
Table S9. Path Structure for Top-Down Food-Web Model with Full Volume Linkages
(34 KB DOC)
We thank J. Sears for monitoring inquilines and maintaining experimental treatments, and L. Bledzski for counting protozoa and rotifers. The manuscript benefited from comments by E. Farnsworth, G. Graves, A. Brody, the Ecology Reading Group at the University of Vermont, and three anonymous reviewers.
NJG and AME conceived and designed the experiments. NJG performed the experiments. NJG and AME analyzed the data. NJG and AME wrote the paper.
- 1. Terborgh J, Lopez L, Nunez P, Rao M, Shahabuddin G, et al. (2001) Ecological meltdown in predator-free forest fragments. Science 294: 1923–1926.
- 2. Robinson GR, Holt RD, Gaines MS, Hamburg SP, Johnson ML, et al. (1992) Diverse and contrasting effects of habitat fragmentation. Science 257: 524–526.
- 3. Pauly D, Alder J, Bennett E, Christensen V, Tyedmers P, et al. (2003) The future for fisheries. Science 302: 1359–1361.
- 4. Holt RD, Lawton JH, Polis GA, Martinez ND (1999) Trophic rank and the species-area relationship. Ecology 80: 1495–1504.
- 5. Post DM (2002) The long and short of food-chain length. Trends Ecol Evol 17: 269–277.
- 6. Kruess A, Tscharnkte T (2000) Species richness and parasitism in a fragmented landscape: Experiments and field studies with insects on Vicia sepium.. Oecologia 122: 129–137.
- 7. O'Dowd DJ, Green PT, Lake PS (2003) Invasional ‘meltdown' on an oceanic island. Ecol Lett 6: 812–817.
- 8. Haila Y (2002) A conceptual genealogy of fragmentation research: From island biogeography to landscape ecology. Ecol Appl 12: 321–334.
- 9. Dooley JL, Bowers MA (1998) Demographic responses to habitat fragmentation: Experimental tests at the landscape and patch scale. Ecology 79: 969–980.
- 10. Paine RT (1966) Food web complexity and species diversity. Am Nat 100: 65–75.
- 11. Holling CS (1992) Cross-scale morphology, geometry, and dynamics of ecosystems. Ecol Monogr 62: 447–502.
- 12. Ellison AM, Bank MS, Clinton BD, Colburn EA, Elliott K, et al. (2005) Loss of foundation species: Consequences for the structure and dynamics of forested ecosystems. Front Ecol Env 9: 479–486.
- 13. Wright JP, Jones CG (2006) The concept of organisms as ecosystem engineers ten years on: Progress, limitations, and challenges. Bioscience 56: 203–209.
- 14. Matson PA, Hunter MD (1992) The relative contributions of top-down and bottom-up forces in population and community ecology. Ecology 73: 723.
- 15. Brett MT, Goldman CR (1996) A meta-analysis of the freshwater trophic cascade. Proc Natl Acad Sci U S A 93: 7723–7726.
- 16. Polis GA, Strong DR (1996) Food web complexity and community dynamics. Am Nat 147: 813–846.
- 17. Debinski D, Holt RD (2000) A survey and overview of habitat fragmentation experiments. Cons Biol 14: 1–13.
- 18. Bender DJ, Contreras TA, Fahrig L (1998) Habitat loss and population decline: A meta-analysis of the patch size effect. Ecology 79: 517–533.
- 19. Ellison AM, Gotelli NJ, Brewer JS, Cochran-Stafira DL, Kneitel J, et al. (2003) The evolutionary ecology of carnivorous plants. Adv Ecol Res 33: 1–74.
- 20. Ellison AM, Buckley HL, Miller TE, Gotelli NJ (2004) Morphological variation in Sarracenia purpurea (Sarraceniaceae): Geographic, environmental, and taxonomic correlates. Am J Bot 91: 1930–1935.
- 21. Fish D, Hall DW (1978) Succession and stratification of aquatic insects inhabiting the leaves of the insectivorous pitcher plant Sarracenia purpurea. Am Midl Nat 99: 172–183.
- 22. Wolfe LM (1981) Feeding behavior of a plant: Differential prey capture in old and new leaves of the pitcher plant (Sarracenia purpurea). Am Midl Nat 106: 352–359.
- 23. Heard SB (1994) Pitcher plant midges and mosquitoes: A processing chain commensalism. Ecology 75: 1647–1660.
- 24. Cochran-Stafira DL, von Ende CN (1998) Integrating bacteria into food webs: Studies with Sarracenia purpurea inquilines. Ecology 79: 880–898.
- 25. Addicott JF (1974) Predation and prey community structure: An experiment study of the effect of mosquito larvae on the protozoan communities of pitcher plants. Ecology 55: 475–492.
- 26. Bledzki LA, Ellison AM (1998) Population growth and production of Habrotrocha rosa Donner (Rotifera: Bdelloidea) and its contribution to the nutrient supply of its host, the northern pitcher plant, Sarracenia purpurea L (Sarraceniaceae). Hydrobiologia 385: 193–200.
- 27. Buckley HL, Miller TE, Ellison AM, Gotelli NJ (2003) Reverse latitudinal trends in species richness of pitcher-plant food webs. Ecol Lett 6: 825–829.
- 28. Gotelli NJ, Ellison AM (2002) Biogeography at a regional scale: Determinants of ant species density in bogs and forests of New England. Ecology 83: 1604–1609.
- 29. Wootton JT (1994) Predicting direct and indirect effects: An integrated approach using experiments and path-analysis. Ecology 75: 151–165.