food web

Soil food web

The soil food web is the community of organisms living all or part of their lives in the soil. It describes a complex living system in the soil and how it interacts with the environment, plants, and animals.

Introduction

Food webs describe the transfer of energy between species in an ecosystem. While a food chain examines one, linear, energy pathway through an ecosystem, a food web is more complex and illustrates all of the potential pathways. Much of this transferred energy comes from the sun. Plants use the sun’s energy to convert inorganic compounds into energy-rich, organic compounds, turning carbon dioxide and minerals into plant material by photosynthesis. Plants are called autotrophs because they make their own energy; they are also called producers because they produce energy available for other organisms to eat. Heterotrophs are consumers that cannot make their own food. In order to obtain energy they eat plants or other heterotrophs.

Above ground foodwebs

In above ground food webs, energy moves from producers (plants) to primary consumers (herbivores) and then to secondary consumers (predators). The phrase, trophic level, refers to the different levels or steps in the energy pathway. In other words, the producers, consumers, and decomposers are the main trophic levels (DeAngelis 1992). This chain of energy transferring from one species to another can continue several more times, but eventually ends. At the end of the food chain, decomposers such as bacteria and fungi break down dead plant and animal material into simple nutrients.

Below ground foodwebs

How are soil food webs different? The decomposers at the end of the surface food web are only the beginning below ground. While living plants are the largest source of energy above ground, the most abundant energy resource in the soil is detritus, or dead plant and animal matter. The primary consumers in soil are often microbes such as bacteria and fungi that consume detritus. There are at least 10,000 species and more than 1 billion individual bacteria in 1 gram of soil (Torsvik et al. 1990). These fast growing microbes act as a food base for many other soil organisms such as mites, collembolans, nematodes and enchytraeids. Underground herbivores can also get energy directly by grazing on or parasitizing plant roots (see root-knot nematode) and these herbivores have their own predators (such as entomopathogenic nematodes). For an overview of soil organisms see: Soil life

Methodology

The nature of soil makes direct observation of food webs difficult. Since soil organisms range in size from less than 0.1 mm (nematodes) to greater than 2 mm (earthworms) there are many different ways to extract them. Soil samples are often taken using a metal core. Larger macrofauna such as earthworms and insect larvae can be removed by hand, but this is impossible for smaller nematodes and soil arthropods. Most methods to extract small organisms are dynamic; they depend on the ability of the organisms to move out of the soil. For example, a Berlese funnel, used to collect small arthropods, creates a light/heat gradient in the soil sample. As the microarthopods move down, away from the light and heat, they fall through a funnel and into a collection vial. A similar method, the Baermann funnel, is used for nematodes. The Baerman funnel is wet, however (while the Berlese funnel is dry) and does not depend on a light/heat gradient. Nematodes move out of the soil and to the bottom of the funnel because, as they move, they are denser than water and are unable to swim. Soil microbial communities are characterized in many different ways. The activity of microbes can be measured by their respiration and carbon dioxide release. The cellular components of microbes can be extracted from soil and genetically profiled, or microbial biomass can be calculated by weighing the soil before and after fumigation.

Types of food webs

There are three different types of food web representations: topological (or traditional) food webs, flow webs and interaction webs. These webs can describe systems both above and below ground.

Topological webs

Early food webs were topological; they were descriptive and provided a nonquantitative picture of consumers, resources and the links between them. Pimm et al. (1991) described these webs as a map of which organisms in a community eat which other kinds. The earliest topological food web, made in 1912, examined the predators and parasites of cotton boll weevil (reviewed by Pimm et al. 1991). Researchers analyzed and compared topological webs between ecosystems by measuring the web’s interaction chain lengths and connectivity (Pimm et al. 1991). One problem faced in standardizing such measurements is that there are often too many species for each to have a separate box. Depending on the author, the number of species aggregated or separated into functional groups may be different (De Ruiter et al. 1996). Authors may even eliminate some organisms. By convention, the dead material flowing back to detritus is not shown, as it would complicate the figure, but it is taken account in any calculations (De Ruiter et al. 1996).

Flow webs

Flow webs build on topological webs, adding quantitative information on the movement of carbon or other nutrients from producers to consumers. Hunt et al. (1987) published the first flow web for soil, describing the short grass prairie in Colorado, USA. The authors estimated nitrogen transferral rates through the soil food web and calculated nitrogen mineralization rates for a range of soil organisms. In another landmark study, researchers from the Lovinkhoeve Experimental Farm in the Netherlands examined the flow of carbon and illustrated transfer rates with arrows of different thicknesses (Brussaard et al. 1988). In order to create a flow web, a topological web is first constructed. After the members of the web are decided, the biomass of each functional group is calculated, usually in kg carbon/hectare. In order to calculate feeding rates, researchers assume that the population of the functional group is in equilibrium. At equilibrium, the reproduction of the group balances the rate at which members are lost through natural death and predation (Hunt et al. 1987). When feeding rate is known, the efficiency with which nutrients are converted into organism biomass can be calculated. This energy stored in the organism represents the amount available to be passed on to the next trophic level. After constructing the first soil flow webs, researchers discovered that nutrients and energy flowed from lower resources to higher trophic levels through three main channels (Hunt et al. 1987; Brussaard et al. 1988). The bacterial and fungal channels had the largest energy flow, while the herbivory channel, in which organisms directly consumed plant roots, was smaller. It is now widely recognized that bacteria and fungi are critical to the decomposition of carbon and nitrogen and play important roles in both the carbon cycle and nitrogen cycle.

Interaction web

An interaction web, shown below, is similar to a topological web, but instead of showing the movement of energy or materials, the arrows show how one group influences another. In interaction food web models, every link has two direct effects, one of the resource on the consumer and one of the consumer on the resource (Stiling 1999). The effect of the resource on the consumer is positive, (the consumer gets to eat) and the effect on the resource by the consumer is negative (it is eaten). These direct, trophic, effects can lead to indirect effects. Indirect effects, represented by dashed lines, show the effect of one element on another to which it is not directly linked (Stiling 1999). For example, in the simple interaction web below, when the predator eats the root herbivore, the plant eaten by the herbivore may increase in biomass. We would then say that the predator has a beneficial indirect effect on the plant roots



Food web control

Bottom-up effects

Bottom-up effects occur when the population density of a resource affects the population of the resources’ consumer (Shurin et al. 2006). For example, in the figure above, an increase in root density causes an increase in herbivore density that causes a corresponding increase in predator density. Correlations in abundance or biomass between consumers and their resources give evidence for bottom-up control (Shurin et al. 2006). An often-cited example of a bottom-up effect is the relationship between herbivores and the primary productivity of plants. In terrestrial ecosystems, the biomass of herbivores and detritivores increases with primary productivity. An increase in primary productivity will result in a larger influx of leaf litter into the soil ecosystem, which will provide more resources for bacterial and fungal populations to grow. More microbes will allow an increase in bacterial and fungal feeding nematodes, which are eaten by mites and other predatory nematodes. Thus, the entire food web swells as more resources are added to the base (Shurin et al. 2006). When ecologists use the term, bottom-up control, they are indicating that the biomass, abundance, or diversity of higher trophic levels depend on resources from lower trophic levels (Stiling 1999).

Top-down effects

Ideas about top-down control are much more difficult to evaluate. Top-down effects occur when the population density of a consumer affects that of its resource (Stiling 1999); for example, a predator affects the density of its prey. Top-down control, therefore, refers to situations where the abundance, diversity or biomass of lower trophic levels depends on effects from consumers at higher trophic levers (Stiling 1999). A trophic cascade is a type of top-down interaction that describes the indirect effects of predators. In a trophic cascade, predators induce effects that cascade down food chain and affect biomass of organisms at least two links away (Stiling 1999). The importance of trophic cascades and top-down control in terrestrial ecosystems is actively debated in ecology (reviewed in Shurin et al. 2006) and the issue of whether trophic cascades occur in soils in no less complex (reviewed in Wardle 2002). Trophic cascades do occur in both the bacterial and fungal energy channels (Santos et al. 1981; Allen-Morley and Coleman 1989; Hedland and Ohrn 2000). However, cascades may be infrequent, because many other studies show no top-down effects of predators (Mikola and Setala 1998; Laakso and Setala 1999). In Mikola and Setala’s study, microbes eaten by nematodes grew faster when they were grazed upon frequently. This compensatory growth slowed when the microbe feeding nematodes were removed. Therefore, although top predators reduced the number of microbe feeding nematodes, there was no overall change in microbial biomass. Besides the grazing effect, another barrier to top down control in soil ecosystems is widespread omnivory, which by increasing the number of trophic interactions, dampens effects from the top. The soil environment is also a matrix of different temperatures, moistures and nutrient levels, and many organisms are able to become dormant to withstand difficult times. Depending on conditions, predators may be separated from their potential prey by an insurmountable amount of space and time. Any top-down effects that do occur will be limited in strength because soil food webs are donor controlled. Donor control means that consumers have little or no effect on the renewal or input of their resources (Stiling 1999). For example, aboveground herbivores can overgraze an area and decrease the grass population, but decomposers cannot directly influence the rate of falling plant litter. They can only indirectly influence the rate of input into their system through nutrient recycling which, by helping plants to grow, eventually creates more litter and detritus to fall (Moore 2003). If the entire soil food web were completely donor controlled, however, bacterivores and fungivores would never greatly affect the bacteria and fungi they consume. While bottom-up effects are no doubt important, many soil ecologists suspect that top-down effects are also sometimes significant. Certain predators or parasites, when added to the soil, can have a large effect on root herbivores and thereby indirectly affect plant fitness. For example, in a coastal shrubland food chain the native entomopathogenic nematode, Heterorhabditis marelatus, parasitized ghost moth caterpillars, and ghost moth caterpillars consumed the roots of bush lupine. The presence of H. marelatus correlated with lower caterpillar numbers and healthier plants. In addition, the researchers observed high mortality of bush lupine in the absence of entomopathogenic nematodes. These results implied that the nematode, as a natural enemy of the ghost moth caterpillar, protected the plant from damage. The authors even suggested that the interaction was strong enough to affect the population dynamics of bush lupine (Strong et al. 1996); this was supported in later experimental work with naturally-growing populations of bush lupine (Preisser 2003, Preisser and Strong 2004). Top down control has applications in agriculture and is the principle behind biological control, the idea that plants can benefit from the application of their herbivore’s enemies. While wasps and ladybugs are commonly associated with biological control, parasitic nematodes and predatory mites are also added to the soil to suppress pest populations and preserve crop plants. In order to use such biological control agents effectively, a knowledge of the local soil food web is important.

Community matrix models

A community matrix model is a type of interaction web that uses differential equations to describe every link in the topological web. Using Lotka-Volterra equations , that describe predator-prey interactions, and food web energetics data such as biomass and feeding rate, the strength of interactions between groups is calculated (de Ruiter et al. 1995). Community matrix models can also show how small changes affect the overall stability of the web.

Stability of food webs

Mathematical modeling in food webs has raised the question of whether complex or simple food webs are more stable. Until the last decade, it was believed that soil food webs were relatively simple, with low degrees of connectance and omnivory (Wardle 2002). These ideas stemmed from the mathematical models of May (1973) which predicted that complexity destabilized food webs. May used community matrices in which species were randomly linked with random interaction strength to show that local stability decreases with complexity (measured as connectance), diversity, and average interaction strength among species. The use of such random community matrices attracted much criticism. In other areas of ecology, it was realized that the food webs used to make these models were grossly oversimplified (Polis 1991) and did not represent the complexity of real ecosystems. It also became clear that soil food webs did not conform to these predictions. Soil ecologists discovered that omnivory in food webs was common (Walter et al. 1991), and that food chains could be long and complex (Hunt et al. 1987) and still remain resistant to disturbance by drying, freezing, and fumigation (Wardle 2002). But why are complex food web more stable? Many of the barriers to top-down trophic cascades also promote stability. Complex food webs may be more stable if the interaction strengths are weak (May 1973) and soil food webs appear to consist of many weak interactions and a few strong ones (De Ruiter et al. 1995). Donor controlled food webs may be inherently more stable, because it is difficult for primary consumers to overtax their resources (De Angelis 1992). The structure of the soil also acts as a buffer, separating organisms and preventing strong interactions (Wardle 1995). Many soil organisms, for example bacteria, can remain dormant through difficult times and reproduce quickly once conditions improve, making them resilient to disturbance.

Interactions not included in food webs

Despite their complexity, some interactions between species in the soil are not easily classified by food webs. Litter transformers, mutualists, and ecosystem engineers all have strong impacts on their communities that cannot be characterized as either top-down or bottom-up. Litter transformers, such as isopods, consume dead plants and excrete fecal pellets. While on the surface this may not seem impressive, the fecal pellets are moister and higher in nutrients than the surrounding soil, which favors colonization by bacteria and fungi. Decomposition of the fecal pellet by the microbes increases its nutrient value and the isopod is able to re-ingest the pellets. When the isopods consume nutrient-poor litter, the microbes enrich it for them and isopods prevented from eating their own feces can die (Hassall and Rushton 1982). This mutualistic relationship has been called an “external rumen”, similar to the mutualistic relationship between bacteria and cows. While the bacterial symbionts of cows live inside the rumen of their stomach, isopods depend on microbes outside their body. Ecosystems engineers, such as earthworms, modify their environment and create habitat for other smaller organisms. Earthworms also stimulate microbial activity by increasing soil aeration and moisture, and transporting litter into the ground where it becomes available to other soil fauna (Wardle 2002). In aboveground and aquatic food webs, the literature assumes that the most important interactions are competition and predation. While soil food webs fit these sorts of interactions well, future research needs to include more complex interactions such as mutualisms and habitat modification. While they cannot characterize all interactions, soil food webs remain a useful tool for describing ecosystems. The interactions between species in the soil and their effect on decomposition continue to be well studied. Much remains unknown, however, about soil food webs stability and how food webs change over time (Wardle 2002). This knowledge is critical to understanding how food webs affect important qualities such as soil fertility.

See also

References

  • Allen-Morley, C.R. and D.C. Coleman. 1989. Reiliance of soil biota in various food webs to freezing perturbations. Ecology. 70: 1127–1141.
  • Brussaard, L.J., A. van Veen, M.J. Kooistra, and G. Lebbink. 1988. "The Dutch Programme on soil ecology of arable farming systems I. Objectives, approach, and preliminary results." Ecological Bulletins. 39:35–40.
  • De Angelis, D.L. 1992. Dynamics of nutrient cycling and food webs. Chapman and Hall. London. England.
  • de Ruiter, P.C., Neutel, A.-M., & Moore, J.C. 1995. "Energetics, patterns of interaction strengths, and stability in real ecosystems." Science 269:1257–1260.
  • de Ruiter P.C., A.M. Neutel and J.C. Moore. 1996. "Energetics and stability in belowground food webs." In: Food webs: integration of patterns and dynamics (eds. G. Polis and K.O Winemiller). Chapman & Hall.
  • Hassall, M., S.P. Rushton. 1982. "The role of copraphagy in the feeding strategies of terrestrial isopods". Oecologia 53: 374–381
  • Hedland, K. and M.S. Ohrn. 2000. "Tritrophic interactions in a soil community enhace decommpostion rates". Oikos. 88: 585–591.
  • Hunt, H.W., D.C. Coleman, E.R. Ingham, R.E. Ingham, E.T. Elliott, J.C. Moore, S.L. Rose, C.P.P. Reid, and C.R. Morley. 1987. "The detrital food web ina shortgrass prairie." Biology and Fertility of Soils. 3: 57–68.
  • Laakso J. and H. Setala 1999. "Population- and ecosystem-effects of predation on microbial-feeding nematodes". Oecologica. 120: 279–286.
  • Mikola J. and H. Setala 1998. "No evidence of tropic cascades in an experimental microbial-based food web". Ecology 79: 153–164.
  • May, R.M. 1973. Stability and complexity in model ecosystems. Princeton: Princeton University Press. New Jersey.
  • Moore, J.C., K. McCann, H. Setala, and P.C. de Ruiter. 2003. "Top down is bottom up: does predation in the rhizosphere regulate aboveground dynamics?" Ecology. 84: 846–857.
  • Pimm S.L., Lawton J.H. & Cohen J.E. 1991. "Food web patterns and their consequences". Nature 350:669–674.
  • Polis, G.A. 1991. "Complex trophic interactions in deserts: an empirical critique of food web theory." American Naturalist. 138: 123–155.
  • Preisser, E.L., D.R. Strong. 2004. "Climate affects predator control of an herbivore outbreak". American Naturalist 163: 754–762.
  • Santos, P.F., J. Phillips, and W.G. Whitford. 1981. "The Role of mites and nematodes in early stages of buried litter decomposition in a desert". Ecology (Washington DC) 62 (3): 664–669.
  • Shurin, J.B., D.S. Gruner, and H. Hillebrand. 2006. "All wet or dried up? Real differences between aquatic and terrestrial food webs." Proceedings of the Royal Society. 273: 1–9.
  • Stiling, P. 1999. Ecology, Theories and Applications. Third Edtn. Prentice Hall. New Jersey USA.
  • Strong, D. R., H.K. Kaya, A.V. Whipple, A.L, Child, S. Kraig, M. Bondonno, K. Dyer, and J.L. Maron. 1996. "Entomopathogenic nematodes: natural enemies of root-feeding caterpillars on bush lupine." Oecologia (Berlin) 108(1): 167–173.
  • USDA-NRCS, 2004, "The Soil Food web" in The Soil Biology Primer. Url accessed 200604-11
  • V. Torsvik, J. Goksøyr, and F. L. Daae. 1990. "Title?" Applied Environmental Microbiology 56, 782.
  • Walter, D.E. D.T. Kaplan, and T.A. Permar. 1991. "Missing links: a review of methods used to estimate trophic links in food webs." Agriculture, Ecosystems and Environment 34: 399–405.
  • Wardle, D.A. 2002. "Communities and Ecosystems: Linking the aboveground and belowground components." Monographs in population biology Vol. 31. Princeton University Press. New Jersey. USA.

External links

Search another word or see food webon Dictionary | Thesaurus |Spanish
Copyright © 2014 Dictionary.com, LLC. All rights reserved.
  • Please Login or Sign Up to use the Recent Searches feature
FAVORITES
RECENT

;