Just a few decades ago, even answering the simple question of ‘do herbivores influence plant abundance?’ was difficult. Manipulative experiments of consumer effects on plants were rare, and the prevailing sentiment was that herbivores were unlikely to have meaningful effects on plant abundance and dynamics. Over the past 5–10 years, however, there have been a growing number of studies on effects of herbivores on plant abundance. Many of these have demonstrated that herbivores can directly limit plant abundance. Thus, the relevant question at this juncture is not so much ‘do herbivores influence plant abundance?’ but instead ‘under what conditions do herbivores influence plant abundance?’ We structure the review that follows around several broad questions that ask when and where herbivores have their most meaningful impacts on plant distribution and abundance. As such, these questions evaluate our current state of understanding regarding consumer impacts on plant populations.
To obtain answers to our questions, we reviewed studies that documented how consumers influence the number of individuals in future generations. We omitted a large number of ‘within-generation’ studies that quantified how consumers influenced seed, seedling or adult plant survival, because these studies do not allow inference as to whether changes in the abundance of individual plants within one year influences the abundance of plants in future years. We also omitted community-level studies (e.g. Brown & Heske 1990
; Carson & Root 2000
; Jefferies et al. 2004
), because these do not usually elucidate the direct consumptive effects of herbivores on plant abundance.
We found 30 studies that fit our criteria (). These studies examined consumer effects on 23 plant genera. The majority of research (15) concerned insect herbivory, although nine considered effects of large mammalian grazers, two studies looked at impacts of voles and/or mice on plant dynamics, two studies documented the effects of snails/slugs on plant abundance and two studies experimentally clipped vegetation to simulate herbivory.
Table 1 Studies that have quantified population-level impacts of consumers on plants. (Multiple citations in a given row indicate cases where multiple studies were performed on the same study system. In ‘type of herbivore and damage’ column, ‘sd’, (more ...)
(a) Do particular types of consumers (mammals versus insects, seed predators versus other functional groups) have predictably greater population-level impacts on plants than others?
Whether mammals or insects have greater impacts on plant dynamics has been a topic of considerable debate. This is an interesting question because it touches on a broader issue, which is the relative impact of generalist versus specialist herbivores in affecting plant dynamics (mammals are typically generalists, whereas insects are often specialists). Owing in part to their greater size, Crawley (1988
) first suggested that mammals generally have larger negative effects on plants than do insects. This assertion has subsequently been supported by a majority of studies that have explicitly compared the relative effects of insects and mammals on the performance of a focal species (Hulme 1994a
; Palmisano & Fox 1997
; Gomez & Zamora 2000
; Sessions & Kelly 2001
; Warner & Cushman 2002
; Maron & Kauffman 2006
, but see Strauss 1991
; Ehrlén 1995
). In contrast, based on a meta-analysis involving 246 comparisons of plant size from consumer exclusion studies, Bigger & Marvier (1998)
found that insects had larger impacts on plant biomass than did mammals. A major problem in interpreting results from these studies, however, is that comparisons have been based on how strongly various herbivores influence single components of plant performance, such as reproduction or biomass. Whether these results extrapolate to the plant population level is uncertain, and clouds generalizations about the relative importance of particular consumers in influencing plant abundance.
To overcome these limitations, we calculated the average reduction in future seedling recruitment or projected plant population growth rate (λ
) that has been reported in studies involving native vertebrate and invertebrate consumers, as well as biocontrol insects and domesticated grazers. Our analysis reveals no consistent or overwhelming pattern in terms of whether invertebrate or vertebrate consumers have greater impacts on plant populations. Studies that have experimentally quantified the effects of herbivores on future seedling recruitment (but not λ
) have documented substantial effects of both insects (Louda 1982
; Maron et al. 2002
) and mammals (Gómez 2005
) on the recruitment of future generations of seedlings. In studies that estimated effects of consumers on plant population growth, on average, native invertebrate consumers decreased λ
by 0.12 (±s.e.m. 0.06), whereas native mammalian herbivores decreased λ
by an average of 0.06 (±s.e.m. 0.96). Where quantified, biocontrol insects had even stronger effects on plant abundance, decreasing λ
by an average of 0.93 (±s.e.m. 0.38). Several studies on effects of non-native grazers (Gillman et al. 1993
; Bullock et al. 1994
; Bastrante et al. 1995
; Lennartsson & Oostermeijer 2001
) have shown that these consumers can have positive to mildly or even strongly negative effects on λ
depending on whether consumers have mostly indirect or direct effects on vegetation. Where sheep act solely as agents of disturbance and create gaps in vegetation (e.g. Gillman et al. 1993
; Bullock et al. 1994
), they can have positive effects on plant population growth. In contrast, where herbivores both create disturbance but also have consumptive effects on the focal plant (such as was the case in Lennartsson & Oostermeijer's (2001)
study on horse herbivory), overall impacts can be mildly negative. Where effects appear to be primarily consumptive (i.e. Bastrante et al. 1995
), effects can have even greater negative effects on plant population growth ().
We compared the average reduction in plant population growth reported in studies on floral, pre- and post-dispersal seed predators compared to those reported for all other herbivore types identified in our review. On average, seed predators reduced λ
by 0.43 (±s.e.m. 0.19), whereas other herbivores reduced λ
by 0.33 (±s.e.m. 0.26). If we exclude studies of biocontrol insects and domestic grazers which might artificially inflate the effects of herbivory, on average seed predators reduce λ
by 0.16 (±s.e.m. 0.05), whereas other herbivores decrease λ
by 0.11 (±s.e.m. 0.14). While these results should be viewed cautiously, they are surprising because they suggest that seed predators may be as important as other types of consumers in affecting plant population growth. Moreover, they demonstrate that demographic sensitivities alone may not provide accurate predictions about whether consumers that attack specific life stages will or will not have population-level consequences. Equally important is the relative magnitude of response of particular life stages to the experimental exclusion of consumers (Ehrlén et al. 2005
(b) Are particular plant life-histories more vulnerable to population-level impacts of consumers than others?
We know from the large literature on the effects of herbivores on plant performance that plant life history can often influence how much herbivore damage plants incur. For example, plants that produce large seeds are clearly more vulnerable to post-dispersal seed predation than plants that produce small seeds (Mittelbach & Gross 1984
; Schupp et al. 1989
; Hulme 1993
; Reader 1993
). Often less-defended fast-growing plants receive more herbivore damage than slow-growing better-defended species (Coley et al. 1985
). Can similar predictions be generated regarding how plant life history influences the vulnerability of plants at the population level?
One recurrent suggestion is that short-lived fugitive plants with a strong reliance on current seed rain for regeneration should be more negatively affected by herbivores that reduce seed production than long-lived perennials or short-lived annuals with long-lived seed banks (Louda & Potvin 1995
). Species with long lifespans, either as adults or as dormant seeds, should be more buffered from heavy herbivory, because they can compensate across years for times when herbivore pressure is particularly intense. For example, regeneration out of a long-lived seed bank can compensate for years of low seed production. Additionally, species with long adult lifespans often have sufficient energy reserves to enable substantial compensatory regrowth after defoliation compared to shorter-lived species lacking reserves in energy.
How well are these predictions borne out by empirical studies? Of the studies we reviewed where population-level effects of herbivores are quantified (), most (19/24 or 79%) have been conducted on herbaceous species with either limited adult longevity or transient seed banks. Thus, the only comparisons we can make with this dataset are differences between herbs of open versus forest habitats, and taxa with and without seed banks. Through direct consumptive effects, herbivores decreased λ
by an average of 0.46 (±s.e.m. 0.27) for herbs found in open grassland habitats, whereas herbivores reduced λ
by an average of only 0.09 (±s.e.m. 0.03) for species that inhabit forest understory. It is tempting to speculate that this reflects the fact that forest herbs are relatively insensitive to changes in growth and fecundity, but the limited sample size and wide standard errors caution against reading too much into this result. Only 10 studies examined the effects of consumers on plants with persistent seed banks; two of these studies ignored seed banks in their population model (McEvoy & Coombs 1999
; Parker 2000
), and only one of the remaining studies was on a species with a seed bank that persisted for longer than 5 years (Kauffman & Maron submitted
). Nevertheless, excluding studies of biocontrol and studies where grazers created gaps in vegetation and increased plant population abundance, herbivores decreased λ
by an average of 0.3 (±s.e.m. 0.19) for species lacking a seed bank, whereas herbivores decreased λ
by an average of only 0.08 (±s.e.m. 0.03) for species with persistent seed banks.
As Louda & Potvin (1995)
originally asserted, it is likely that plant vulnerability to consumers lies along a continuum of life-history variation. Our review suggests that fugitive forbs with no or a very limited seed bank may sit at one end of this spectrum. Effects of consumers on populations of annual species with abundant seed banks have seldom been studied, but species with this life-history type may lie at the other end of the continuum. Recruitment for many annual plants with abundant seed banks may be more safe-site than seed limited, making these taxa insensitive to seed predation, whereas this is not the case for fugitives. What is less clear is how vulnerable may be plants with intermediate life histories. For example, how buffered from population impacts of herbivores are plants that produce dormant seeds, but with dormancy of moderate duration (say, 10 years)? Based on simulations, Maron & Gardner (2000)
found that a hypothetical seed predator could significantly influence plant abundance even when seed dormancy (and hence seed bank persistence) was prolonged. Their results suggested that while seed banks can clearly ‘buffer’ populations, they also provide a ‘memory’ of the cumulative effects of consumers on past seed production.
Another area in need of research is how consumers impact populations of plants that reproduce clonally in addition to or instead of sexually. One might assume that these species would be buffered from population impacts of consumers, both because some of these species have multiple means of reproduction, but also because they often have substantial stored resources that can be used to compensate for herbivory. Of the population-level papers we reviewed, we could find no study on a clonal forb. However, we note that research on rhizomatous cordgrass, Spartina alterniflora
, suggests that grazers can play a key role in affecting its distribution in tidal marshes on the east coast of the US (Silliman & Bertness 2002
; Silliman et al. 2005
). Strong long-term effects of insect herbivores on populations of rhizomatous goldenrod (Solidago altissima
) have also been demonstrated (Carson & Root 2000
(c) Does the impact of consumers on plant population abundance change predictably across environmental gradients or habitat types?
Our review reveals that spatial variation in the population-level impacts of consumers is ubiquitous. Of the 15 studies where herbivore impacts were compared among sites, microhabitat, or habitats, strong context-dependent effects were found in every case except the study by Herrera et al. (2002)
. For example, Fagan & Bishop (2000)
and Fagan et al. (2005)
found striking spatial variation in herbivory within patches of Lupinus lepidus
growing on recently erupted Mount St Helens. Variation in herbivory was based on lupine density. Herbivory was more intense, and had greater effects on population growth at the edges of lupine patches where plants grow at lower density than it did in the middle or ‘core’ of dense patches where plants occur at high density (Fagan et al. 2005
). Finally, on a larger spatial scale, Louda (1982
) found differential effects of herbivory on plant abundance across a distributional gradient from coast to inland sites.
Given that spatial variation in both the performance and population-level effects of herbivory is extremely common, can these context-dependent effects be placed in a broader predictive framework? That is, can we predict the strength of plant–consumer interactions based on particular attributes of the abiotic or biotic environment or do herbivore impacts vary idiosyncratically across a plant's distribution?
One environmental factor that can clearly affect how greatly herbivores influence plant abundance is the extent to which there is open space or bare ground for recruitment. In open habitats, there is often a close correspondence between seed input and recruitment (Harper 1977
; Fenner 1985
; Maron et al. 2002
). Recruitment is more likely to be seed limited in more open or disturbed habitats with less interspecific competition than in closed habitats with greater litter or plant cover, where populations may be microsite limited (Crawley 1997
). This suggests that herbivory that reduces seed production should have greater impacts on plant abundance in open versus closed microhabitat. This prediction appears to be borne out in studies conducted to date. For example, Maron & Kauffman (2006)
found that post-dispersal seed predation by mice had large effects on the abundance of bush lupine in open dune habitat but not in adjacent grasslands where there was greater cover. Louda & Potvin (1995)
and Maron et al. (2002)
similarly found differences in consumer impacts on two related native thistles based on their microhabitat. Pre-dispersal insect herbivores had greater effects on plant recruitment in more sparsely vegetated areas than in microhabitats with greater plant cover. McEvoy & Coombs (1999)
found that biocontrol insects had their greatest effect on the population growth of ragwort (Senecio jacobaea
) when habitat was disturbed and competition reduced compared to situations where habitat was undisturbed and plants faced stiff competition for safe sites during recruitment. Yet, even though biocontrol agents had their greater effect on reducing Senecio
population growth in disturbed habitats, the combination of low disturbance and biocontrol was the most successful strategy for eliminating Senecio
populations, simply because of the powerful effects of competition exerted on suppressing Senecio
Beyond predicting how seed loss might influence recruitment in different microhabitat types, there are insufficient data to generate more robust predictions about how limits to plant abundance imposed by consumers should change across larger spatial scales. Menge & Olson's (1990)
work on stress response gradients offers an interesting conceptual framework in which to start to make these predictions. Menge & Olson (1990)
assert that when and where consumers have their greatest effects on plants depend on whether any given environment is more stressful to plants or consumers. Critically evaluating these ideas will require a more mechanistic understanding of how context mediates the per capita effects of herbivores on plant abundance. Especially, future studies would be helpful that simultaneously: (i) quantified population effects of consumers across environmental gradients, (ii) measured environmental variation across this gradient and (iii) experimentally manipulated aspects of the abiotic environment to determine whether the strength of consumer effects on plants could be experimentally switched to reproduce observed patterns in herbivore impacts across environment gradients.
(d) To what extent do consumers control local patterns of plant distribution or range limits?
At least in some cases, herbivores control the local distribution of plants among habitat types. Louda's (1982
) research was one of the first exclusion studies to determine whether local patterns of plant distribution might be controlled by insect herbivory. In this classic work, Louda (1982)
documented that the shrub Haplopappus squarrosus
(current name: Hazardia squarrosa
) was more abundant at inland sites than at sites close to the coast. By excluding pre-dispersal seed-feeders on plants across this gradient, Louda (1982)
found that herbivory on H. squarrosus
was intense at all sites, but that insect exclusion led to greater gains in recruitment at coastal versus inland sites. Thus, herbivory appeared to drive the pattern in plant abundance across this geographical gradient.
More recent work has similarly implicated herbivores in affecting local plant distribution. For example, Gómez (2005)
demonstrated that herbivores influence the spatial distribution of two species of Erysimum
that typically gain refuge from ungulate herbivory by growing under shrubs. Ungulate exclusion enabled these species to colonize the interstitial spaces between shrubs, thereby altering their habitat distribution. As well, recent work by Fine et al. (2004)
demonstrated that heavy insect herbivory on tropical tree seedlings may be responsible for limiting the local distribution of particular tree species to sites with specific soil conditions. Thus, researchers have found effects of consumers on local distributions where they have looked for them, but too few studies exist to generalize the importance of consumers, relative to abiotic conditions.
The importance of consumers for local patterns of distribution suggests that herbivores could also affect the broader distributional limits of plants. Might herbivores influence plant range boundaries? Although range boundaries of plants are often assumed to be ‘fixed’, it is likely that range boundaries are very dynamic, expanding or contracting depending on how variation in the abiotic or biotic environment constrains or facilitates population growth. Historically, thinking on the factors that limit plant distributional ranges has been dominated by a focus on abiotic factors, such as climate and edaphic conditions (Salisbury 1926
; Arris & Eagleson 1989
; Demers et al. 1998
). Theory suggests that homogenizing gene flow coming from the range centre makes it difficult for species to adapt to conditions at or beyond their current range edge (Kirkpatrick & Barton 1997
). Yet, areas immediately beyond the range of many plants are often abiotically similar to sites within the range of these species, and it appears that many plants could physiologically tolerate areas outside their current distribution. For example, Stokes et al. (2004)
found that population growth rates for two species of Ulex
were not lower at their range boundaries compared to more interior sites. A few other studies have failed to detect a decline in plant performance from interior to range edge (Prince & Carter 1985
; Carey et al. 1995
). In cases such as these, it is not clear what limits distribution, which begs the question of whether biotic rather than abiotic factors may be important. Though the idea that species interactions can set range boundaries has been floated for some decades (Rochow 1970
; MacArthur 1972
; Galen 1990
), few studies of range limits explicitly consider how biotic factors influence range edges. In fact, no study, to our knowledge, has examined how consumers may influence either the location of plant range boundaries, or the dynamics of plant populations at their range boundary compared to the centre of their range (Strauss & Zangrel 2002
). Future work that combined transplant experiments (sensu Prince & Carter 1985
; Stokes et al. 2003
) with consumer exclusion to estimate how consumers combined with spatial variation in abiotic conditions influenced plant population growth both at a range edge and beyond would be informative and extremely valuable.