Present address: Atlantic Canada Conservation Data Centre, PO Box 6416, Sackville, New Brunswick, Canada E4L 1G6.
Effects of fungal pathogens on seeds of native and exotic plants: a test using congeneric pairs
Article first published online: 20 APR 2002
Journal of Applied Ecology
Volume 38, Issue 5, pages 1104–1113, October 2001
How to Cite
Blaney, C.S. and Kotanen, P.M. (2001), Effects of fungal pathogens on seeds of native and exotic plants: a test using congeneric pairs. Journal of Applied Ecology, 38: 1104–1113. doi: 10.1046/j.1365-2664.2001.00663.x
- Issue published online: 20 APR 2002
- Article first published online: 20 APR 2002
- Received 5 May 2000; revision received 2 July 2001
- old fields;
- seed banks;
- Top of page
- Site description
- Materials and methods
- 1It has previously been hypothesized that low rates of attack by natural enemies may contribute to the invasiveness of exotic plants.
- 2We tested this hypothesis by investigating the influence of pathogens on survival during a critical life-history stage: the seed bank. We used fungicide treatments to estimate the impacts of soil fungi on buried seeds of a taxonomically broad suite of congeneric natives and exotics, in both upland and wetland meadows.
- 3Seeds of both natives and exotics were recovered at lower rates in wetlands than in uplands. Fungicide addition reduced this difference by improving recovery in wetlands, indicating that the lower recovery was largely attributable to a higher level of fungal mortality. This suggests that fungal pathogens may contribute to the exclusion of upland species from wetlands.
- 4The effects of fungicide on the recovery of buried seeds did not differ between natives and exotics. Seeds of exotics were recovered at a higher rate than seeds of natives in uplands, but this effect was not attributable to fungal pathogens.
- 5Fungal seed pathogens may offer poor prospects for the management of most exotic species. The lack of consistent differences in the responses of natives vs. exotics to fungicide suggests few aliens owe their success to low seed pathogen loads, while impacts of seed-pathogenic biocontrol agents on non-target species would be frequent.
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- Site description
- Materials and methods
Non-native plant species deliberately or accidentally introduced into new areas by humans now comprise a substantial fraction of the flora of many ecosystems around the world (Drake et al. 1989; Vitousek et al. 1996; Mack et al. 2000; Manchester & Bullock 2000). Exotic species can pose serious concerns for the conservation of native species, and may cost millions of dollars in remediation and control efforts (US Congress, Office of Technology Assessment 1993; Vitousek et al. 1996; Mack et al. 2000). Still, most arriving plant invaders never become established, or have no noticeable impact if they do (Williamson & Fitter 1996a,b; Manchester & Bullock 2000). Many researchers have tried to develop guidelines for the identification and control of the minority that will become problematic invaders, but these efforts have produced few rules with strong predictive or management value (Mack 1996; Williamson 1996; Mack et al. 2000; but see Kolar & Lodge 2001).
Seed banks may provide clues to invasiveness. Many plants suffer the majority of their mortality at the seed stage (Harper 1977; Leck, Parker & Simpson 1989; Fenner 1992), suggesting seed mortality has the potential to limit invasiveness. The presence of seed banks may also be important in buffering against the stochastic hazards faced by small populations (Venable & Brown 1988; Stöcklin & Fischer 1999); invading species generally face these hazards repeatedly, both at the original site of introduction and with range expansion as small colonizing subpopulations are formed (Barrett & Richardson 1986; Crawley 1989; Barrett & Husband 1990). It follows that the survival of invading populations may be enhanced in species able to produce persistent seed banks (Baker 1969, 1974), and there is some evidence that this is the case. For example, many invaders produce seed banks, including almost all of the world's worst weeds (Holm et al. 1977), and seed banks are one of the most important factors limiting efforts to biologically control exotic weeds (Holloway 1964; Dahlsten 1986). Crawley, Harvey & Purvis (1996) found that British aliens were more likely than natives to have long-term seed banks, although this may not apply equally to all groups (Hodkinson & Thompson 1997). Finally, Thompson, Hodgson & Rich (1995) found that many plants recently expanding in their European distribution had persistent seed banks, although this was less likely to be the case for exotics than natives.
Biological factors causing mortality of buried seeds in natural communities are incompletely understood, although they are known to include a wide range of vertebrate and invertebrate seed predators and many taxa of pathogens (Baskin & Baskin 1998). Fungi are believed to be among the most important enemies of buried seeds, but few field experiments have addressed their roles specifically (Kremer 1993; Baskin & Baskin 1998). There are two distinct reasons to expect that exotic plants may exhibit especially great resistance to seed-destroying fungi, with positive consequences for their survival in the seed bank. First, invaders may lose their pathogens when they are transported to a new area (the predator escape hypothesis; Elton 1958; Crawley 1986). Secondly, species intrinsically resistant to seed pathogens may make better invaders because they are less likely to be eliminated by natural enemies during colonization of new areas (the predator filter hypothesis; Blaney & Kotanen 2001). In both cases, a low pest load is important to invasion, but the escape hypothesis predicts invaders to have reduced pest loads in new habitats, while the filter hypothesis predicts pest loads to be low in both original and new areas. The escape hypothesis also relies on the loss of species-specific enemies, while the filter hypothesis applies to both generalists and specialists.
There is some support for both of these hypotheses. Evidence for the filter hypothesis is relatively sparse, but correlations between seed size, predation rates and invasiveness (Crawley, Harvey & Purvis 1996) together suggest species with low rates of seed predation may make the most successful invaders. Evidence for the escape hypothesis is more extensive. Although many soil-borne disease organisms may be non-selective, some are thought to be host-specific (Kirkpatrick & Bazzaz 1979; Harman 1983; Mills & Bever 1998), including some seed pathogens of agricultural plants (Neergaard 1977; Agarwal & Sinclair 1997). A few studies have also demonstrated that invaders develop larger seed banks in new regions than in their native habitats, suggesting that escape from seed predators may be occurring. For example, numerous Australian Acacia spp. develop much larger seed banks in South Africa than in their native regions, primarily as a result of escape from predispersal seed predators and gall rusts (Dean, Holmes & Weiss 1986). Similarly, seed banks of Chrysanthemoides monilifera are much larger in Australia than in its native South Africa, reflecting both greater seed production and enhanced persistence in the soil (Scott 1996).
In this study, we investigated whether susceptibility to natural enemies is lower in exotics than in natives, as predicted by both the predator filter and predator escape hypotheses. We chose to focus on fungal seed pathogens because of their presumed importance; elsewhere, we have considered vertebrate and invertebrate seed predators (Blaney 1999; Blaney & Kotanen 2001; C.S. Blaney & P.M. Kotanen, unpublished data). Because rates of fungal attack may vary among habitats, we explored this question with linked experiments in two types of communities: wetland and upland meadows. In order to look for recurring patterns, we used a set of 30 plant species drawn from a wide range of taxonomic groups. Analyses in which species are treated as independent data points can be useful in demonstrating community-level ecological patterns, and we have followed this approach in related studies (Blaney 1999; Blaney & Kotanen 2001; C.S. Blaney & P.M. Kotanen, unpublished data), but there is a risk that subtle native–alien differences may be lost in the ‘noise’ created by the inclusion of very different species in the same data set. Also, if a significant correlation was found between disease resistance and exotic status, it might not represent a causal relationship but instead might be attributable to some unmeasured characteristic of the taxonomic groups from which the exotic species were drawn (Felsenstein 1985; Harvey & Pagel 1991; Miles & Dunham 1993). In response, we employed comparisons within congeneric pairs of native and exotic species; comparing closely related species reduces the likelihood of phylogenetic biases, and can allow the detection of subtle effects despite using a great diversity of species (Mack 1996). This is one of few studies to test experimentally a hypothesis of invasiveness (Karieva 1996), and is the first to study experimentally seed bank ecology for a wide range of co-occurring natives and exotics.
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- Site description
- Materials and methods
The experiment was conducted in nine upland and 10 open wetland plots, each measuring 2·5 × 3·5 m, distributed around the 348-ha University of Toronto Joker's Hill field station, Regional Municipality of York, Ontario, Canada (44°02′ N, 79°31′ W). Plots of each habitat type were matched for moisture level, openness and vegetation type and were separated by at least 100 m. The upland plots were in open, dry, sandy old field habitats, with some combination of Bromus inermis, Poa pratensis and Poa compressa dominant. The wetland plots were in open, permanently wet meadows, dominated by wetland species including Eupatorium maculatum, Eupatorium perfoliatum, Agrostis stolonifera, Impatiens capensis, Onoclea sensibilis, Glyceria striata, Equisetum arvense and Equisetum fluviatile. Nomenclature follows Gleason & Cronquist (1991).
Materials and methods
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- Site description
- Materials and methods
Seeds were bulk-collected from wild populations in southern Ontario in 1997, with the exception of Elymus trachycaulus; this species was purchased from the Pterophylla Farm (Walsingham, Ontario), where seeds were grown in 1996 from plants originating from local, wild, seed stock. All seeds were stored dry in a freezer until needed. Thirty herbaceous species of open, upland, areas were chosen for this experiment, comprising 15 congeneric pairs of one native and one alien species (Table 1). Wild populations of each species occur in the Regional Municipality of York (Riley 1989), and most occur naturally within the Joker's Hill property (Table 1). We have defined exotics as species that are regionally or continentally non-native (Morton & Venn 1990), not simply as absent from our particular study site or experimental habitats; this reflects the expectation that while seed pathogens may be lost during long-distance invasions, they are unlikely to be unable to disperse between local habitats. Our data set included locally common and locally scarce examples of both natives and exotics.
|Asteraceae 1||Lactuca canadensis||Native||x|
|Asteraceae 2||Senecio pauperculus||Native|
|Poaceae 1||Bromus kalmii||Native|
|Poaceae 2||Elymus trachycaulus||Native|
|Rosaceae 1||Geum aleppicum||Native||x|
|Rosaceae 2||Potentilla arguta||Native||x|
|Total||30 species||15 native, 15 alien|
Upland and wetland soil was collected from the study site immediately before the experiment. This soil was dried and sieved but otherwise not treated before use. Seed bags, each made from a knee-high nylon stocking cut in thirds, were filled with 20 seeds of a single species mixed with 20 ml of field soil and then tied shut. These bags were subjected to one of two treatments: (i) control, seed bag saturated in water before burial, and (ii) fungicide addition, seed bag saturated in fungicide solution before burial. The fungicide solution was a 1 : 100 solution of Maestro 75DF in water (Zeneca Corp., Ontario, Canada); this concentration was recommended by the manufacturer for use as a dip for bulbs and tubers. The active ingredient in this fungicide is Captan (75% by weight). Captan is a non-systemic heterocyclic nitrogen fungicide used against a wide range of fungi in the Oomycota, Ascomycota and Basidiomycotina (Sharvelle 1961; Torgeson 1969; Neergaard 1977) and is noted as being particularly effective against seed-rotting fungi (Neergaard 1977). It has been shown to have minimal effects on endomycorrhizal fungi, which are important in grassland systems (Dix & Webster 1995), but can have both positive and negative effects on ectomycorrhizal development depending on the plant species involved (Vyas 1988).
Within each experimental plot, a 10 × 6 grid was created with points separated by 0·5 m. At each grid point, one seed bag was buried 5 cm below the soil surface, so that each plot contained all treatment × species combinations. Seed bags were buried in the field in June 1998, early in the natural cycle of seed dispersal, and were recovered in late October 1998, at the end of the growing season. After recovery, seed bags were opened and their contents spread over potting mix in 10-cm square pots. In a very small number of bags, one or two Bromus or Elymus seedlings had germinated and forced their way through the bag to the soil surface; these seedlings were added to the total number of seedlings germinated in the greenhouse. Pots were kept moist in the greenhouse for 3 months. After 1·5 months, seedlings were counted and soil was disturbed to allow the more deeply buried seeds a better chance to germinate. A final count of seedlings was done at the end of the 3-month germination period. We refer to seeds detected by germination as ‘recovered’.
The primary analysis variable was the proportion of seeds of each species that germinated; these values were arcsin transformed to improve normality (Kirk 1982). The basic analyses used were three-factor randomized block factorial anovas (type III sums of squares), with blocking by plot, and with origin, fungicide treatment and genus of each congeneric pair as factors. The presence of a significant fungicide × origin × genus interaction would indicate that the impacts of pathogens on aliens (relative to natives) is taxon-dependent, and thus that results may be statistically confounded or obscured by phylogeny; conversely, the lack of such an interaction would indicate that fungal effects (if any) are consistent across taxonomic groups.
For all analyses, a non-interactive model was used, as recommended by Newman, Bergelson & Grafen (1997): treatment was treated as a fixed effect, plot was treated as a random blocking effect, and the residual was used as the error term. Of the 600 and 540 experimental replicates, respectively, comprising the wetland and upland experiments, 17 and three were missing because seed bags were not relocated. To restore the design, these cells were interpolated using treatment × species means and adjusting degrees of freedom accordingly (Underwood 1997). Wetland and upland habitats differed with respect to many factors, including their responses to experimental treatments, and were analysed separately. Means are reported ± 1 SE.
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- Site description
- Materials and methods
For each species, rates of seed recovery (germination) were strongly correlated between upland and wetland habitats (rcontrols = 0·87; rfungicide = 0·84; n = 30, P < 0·0001 for both tests: Fig. 1). Recovery tended to be lower in wetlands than uplands, but this difference was less pronounced for fungicide-treated seeds (Fig. 2). Recovery differed significantly between plots in upland habitats, although not in wetlands (Tables 2 and 3); overall values for the 10 wetland plots ranged from 16·9% to 22·6%, while rates for the nine upland plots ranged from 24·8% to 31·3%. Recovery also varied significantly among taxa in both habitats (Tables 2 and 3). In the upland trial, recovery rates for six species were less than 5% while recovery rates exceeded 50% for seven species (Fig. 3). Highest recovery rates were obtained for Lepidium densiflorum (84·7%) and Senecio vulgaris (81·7%) (Fig. 3). In the wetland trial 10 species had recovery rates below 5% (the same six species as in the upland trial plus four additional species) (Fig. 3). Only Chenopodium album (59·8%), Lepidium densiflorum (58·9%) and Senecio vulgaris (52·8%) had recovery rates above 50% (Fig. 3).
|Fungicide × origin||1||0·125||1·069|
|Fungicide × genus||14||0·243||2·078*|
|Origin × genus||14||7·179||61·381***|
|Fungicide × origin × genus||14||0·093||0·795|
|Fungicide × origin||1||0·070||0·506|
|Fungicide × genus||14||0·170||1·229|
|Origin × genus||14||5·871||42·441***|
|Fungicide × origin × genus||14||0·144||1·041|
Effects of fungicide addition
Higher rates of fungal attack reduced the recovery of seeds from wetlands, relative to uplands. Fungicide addition significantly improved seed recovery in the wetland trial from 18·0 ± 1·3% to 22·4 ± 1·5% (Fig. 2 and Table 2). In contrast, fungicide had no effect on recovery in the upland trial (28·3 ± 1·7% control vs. 28·6 ± 1·7% fungicide addition) (Fig. 2 and Table 2). The tendency for the same species to have lower rates of recovery in wetlands than in uplands was nearly eliminated in the fungicide addition treatment (Fig. 1); this tendency was highly significant in the controls (Z = −4·498; P < 0·0001) but was reduced in the fungicide addition treatment (Z = −2·300; P = 0·02) (Wilcoxon signed rank tests).
Variation in recovery by origin
Aliens tended to be recovered at a greater rate than natives in both the upland and wetland trials (Fig. 2); this difference was significant in the uplands but not the wetlands (Tables 2 and 3). There were highly significant origin × genus interactions in both habitats, indicating that relative recovery of exotics vs. natives differed from one genus to another (Fig. 3, Table 2 and Table 3).
Origin × fungicide treatment interactions were non-significant in both habitats, indicating that native and alien species behaved similarly in their responses to fungicide addition (Tables 2 and 3). In uplands, where overall response to fungicide addition was non-significant, native recovery was 2·4% lower in fungicide addition treatments, while alien recovery was only 4·2% greater (Fig. 2). In the wetland trial, where fungicide addition produced a significant overall increase in recovery, both natives and exotics were affected similarly: native recovery increased by 22·4% and alien recovery increased by 26·3% (Fig. 2). Restricting analyses to congeneric pairs in which both species occurred at Joker's Hill did not alter the principal conclusions: fungicide effects remained highly significant in wetland habitats (F1,351 = 19·25, P < 0·001) but not in upland habitats (F1,312 = 0·10, P > 0·05), whereas responses to fungicide still did not differ between natives and exotics (wetland: F1,351 = 0·57, P > 0·05; upland: F1,312 = 0·06, P > 0·05).
The relative responses of exotics and natives to fungicide did not depend on relationship. Rates of recovery were not correlated between members of each congeneric pair, in any treatment or habitat (r < 0·25, n = 15, P > 0·4; Fig. 4); this indicates that congenerics did not in general behave similarly. There were no significant three-way interactions, indicating that relationship did not influence origin × fungicide interactions in either habitat (Tables 2 and 3).
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- Site description
- Materials and methods
Effects of fungal mortality on seed persistence in the soil
This experiment demonstrates that soil fungi can reduce the recovery of viable seeds of a taxonomically broad range of native and exotic species, at least in wetland soils. The particular fungi involved in seed decomposition in natural soils are poorly understood, although those causing seed rots of agricultural plants are comparatively well researched (Neergaard 1977; Agarwal & Sinclair 1997). Potentially important species include members of Oomycota (Pythium spp., Phythopthora spp.), Basidiomycota (Rhizoctonia spp.) and imperfect members of the Ascomycota (e.g. Alternaria spp., Botrytis spp.). As a result of physiological differences, few fungicides are equally effective against all groups (Paul, Ayres & Wyness 1989) but Captan is widely used in agriculture to control species of oomycetes, ascomycetes and basidiomycetes in the soil and on fruit, leaf and seed surfaces (Sharvelle 1961; Torgeson 1969; Neergaard 1977). Consequently, our results are likely to reflect the collective impacts of a wide range of fungal taxa.
In our study, the effects of fungicide addition generally were small in magnitude; however, our estimates of fungal impacts are probably conservative for several reasons. First, some pathogens may have been resistant, especially as our frequency of application was low compared with many agricultural systems. Secondly, lack of specificity may have resulted in unintended negative effects of Captan on non-target mutualists (Sharvelle 1961; Torgeson 1969; Neergaard 1977); we believe this is unlikely to have been a serious problem, both because we focused this study on dormant seeds, which are unlikely to be dependant on mycorrhizae, and because we observed significant positive effects of fungicide addition rather than the negative effects expected if we were harming mutualists more strongly than pathogens. Finally, it is probable that some of the seeds that failed to germinate were dormant rather than dead; thus, our data provide only a minimum estimate of viability. Because dormant seeds should have occurred in all experimental treatments, their occurrence should not have affected our detection of significant treatment effects or interactions. However, dormancy may have contributed to lower rates of recovery for some species, exaggerating interspecific differences and obscuring treatment effects by preventing the detection of viable seeds.
There are a number of other lines of evidence suggesting the importance of fungi to soil seed banks in natural habitats. Soil fungi (including Oomycota) are ubiquitous and abundant (Dix & Webster 1995). Many fungal plant pathogens, including some that can have significant population level effects, are soil borne (Dinoor & Eshed 1984; Burdon 1987). Finally, the importance of fungicidal seed coatings in agriculture (Taylor & Harman 1990), and the presence of fungal-inhibiting compounds in seed coats (Baskin & Baskin 1998), suggest that soil fungi are an important source of seed mortality. Despite these lines of evidence, few other studies have demonstrated the occurrence of fungal mortality in seeds and seedlings in natural plant communities, although there are examples from several very different ecosystems. Crist & Friese (1993) found that proportions of decomposed seeds among five shrub–steppe species ranged from < 5% to 93·5% over 10 months. They implicated fungi as a causal agent by isolating seven fungal species from the retrieved seeds. Lonsdale (1993) demonstrated that seed survival of the exotic Mimosa pigra in northern Australia increased by 10–16% over 7 months following the addition of fungicide to the soil. Augspurger (1983) and Augspurger & Kelly (1984) demonstrated that damping-off disease killed 0–95% of seedlings of a wide range of tropical tree species, and that mortality increased with seedling density, shade and proximity to the parent tree. Packer & Clay (2000) found Pythium caused significant mortality in seedlings of the temperate tree Prunus serotina. Finally, Leishman et al. (2000) found fungicide significantly increased recovery of intact seeds of some, but not all, experimental species in a British grassland.
Variation in fungal mortality between wetlands and uplands
Seed recovery in controls was consistently lower in wetland sites than in uplands. The fact that fungicide addition reduced this difference by improving wetland recovery indicates that it was largely attributable to a higher level of fungal mortality in wetlands. There is evidence that fungal pathogens generally are more prevalent in moist soils than in dry soils. The best example comes from Augspurger (1983) and Augspurger & Kelly (1984), whose studies of spatial variation in the rates of damping-off mortality in tropical tree seedlings showed that mortality was greater in low light areas with higher soil moisture and humidity. Rotem (1978) suggests that this is a general trend that may apply to non-fungal plant pathogens as well. Apparent counterexamples do exist: Leishman et al. (2000) found that supplementing summer rainfall did not lead to higher levels of fungal mortality for seeds of four experimental species.
Alternatively, although few studies have examined the effects of soil moisture on seed bank survival in natural plant communities, limited evidence suggests that seeds survive best in the moisture range in which they typically occur (Leck 1996). If so, fungally induced seed mortality could limit the penetration of wetlands by upland species, and could help to define wetland boundaries. Our results are consistent with this hypothesis: we deliberately chose species largely restricted to uplands and found that recovery was greatest in upland habitats. In a mesocosm experiment using turves collected from the field, Bekker, Oomes & Bakker (1998) also found that seeds of species typical of dry grasslands tended to survive best in a low water treatment, while wet grassland species survived best in a high water treatment.
Variation in fungal mortality between natives and exotics
We found that responses to fungicide additions did not differ between native and exotic species in either wetland or upland habitats. The most likely explanation is that the most important pathogens were generalist fungi that did not distinguish between seeds of natives and aliens; many soil-borne plant pathogens and decay organisms are known to be generalists (Dix & Webster 1995). It is also possible that pathogens specific to native species have become adapted to aliens since their introduction, or that specialist pathogens may have been introduced along with their plant hosts. Some fungal and other pathogens can be transported with seeds (Neergaard 1977; Kirkpatrick & Bazzaz 1979; Agarwal & Sinclair 1997), which is probably the form in which most exotic plants are introduced. In any case, it is clear that alien status per se did not result in a lower pest load for exotics than for related natives.
These results strongly argue against the predator escape hypothesis: if exotics are escaping species-specific seed pathogens when colonizing new regions, this escape must be temporary at best. The lack of differential response also suggests that the filter hypothesis does not apply: there is little reason to believe that the exotics that have successfully established in these habitats have unusually low intrinsic pest loads, at least compared with native congeners. It is still possible that predator filters may operate at higher taxonomic levels: the majority of exotics may come from genera that are relatively pest-resistant. However, in two studies in which we did not employ congeneric pairs, but instead used larger and more taxonomically diverse sets of locally occurring species, we found no evidence that this was the case for either seed predators (Blaney & Kotanen 2001) or soil fungi (Blaney 1999; C.S. Blaney & P.M. Kotanen, unpublished data).
Seed banking and invasions
Our study was designed around the idea that invasiveness may be increased amongst species with a persistent seed bank. However, population growth or spread of invaders may often be controlled more strongly by interactions involving other life-history stages. For example, a recent survey suggests that many plant populations, especially in mesic grasslands, are limited by microsite or growing conditions rather than by the availability of viable seed (Turnbull, Crawley & Rees 2000). Invasion is also a multistage event (Williamson 1996; Mack et al. 2000); as a result processes operating during initial establishment may differ from those during spread or following the development of naturalized populations. For example, a persistent seed bank may well be an advantage during the earliest stages of an invasion, when it may enhance the persistence of small founder populations (Venable & Brown 1988), but by removing seeds from the actively growing population it also may reduce subsequent population growth and spread (Rees & Long 1992; Rees 1997). Trade-offs between dormancy and dispersal (Rees 1993, 1997) may also reduce the rate of spread of species with a persistent seed bank. Finally, in naturalized populations, delayed germination again may improve population persistence, depending on details of temporal and spatial variability, and the nature of interspecific interactions (Venable & Brown 1988; Rees & Long 1992; Rees 1997). Conflicts of this kind suggest that the seed ecology of different invaders may represent different strategies: some may rely more on persistence, some on spread (Thompson, Hodgson & Rich 1995; Crawley, Harvey & Purvis 1996; Hodkinson & Thompson 1997).
We did find one intriguing difference between the seed bank dynamics of natives and exotics: seeds of exotics were more likely to be recovered than seeds of natives in upland habitats. Fungi apparently were not responsible for this difference, because exotics and natives in uplands did not differ in their lack of response to fungicide. The explanation instead may lie with lower susceptibility of exotics to non-fungal sources of mortality, such as poor seed longevity, inappropriate germination or bacterial pathogens (Baskin & Baskin 1998); the upland species that we used apparently lose this advantage in wetter soils. These results suggest that, at least in dry soils, exotics tend to form more persistent seed banks than natives, as also reported by Crawley, Harvey & Purvis (1996). This agrees with the our original hypothesis that persistent seed banks may facilitate invasions, but not because exotics have greater resistance than natives to fungal diseases. This result also supports the view that the value to invaders of characteristics such as seed dormancy is likely to be habitat-dependent (Thompson et al. 1995; Hodkinson & Thompson 1997): strategies that work under some conditions may fail under others, obscuring efforts to identify characters that increase invasiveness.
Our study demonstrates that while soil pathogens reduce the survival of seeds of many native and exotic species, and while exotics may benefit from persistent seed banks, exotics are no more resistant to fungal seed pathogens than related natives. It is important to realize that this result does not necessarily apply to other life-history stages, nor does it preclude the possibility that the most seriously invasive species are exceptions to this rule: they may be problems precisely because they enjoy atypically low pathogen levels. Certain spectacularly successful biological control efforts, as with Opuntia spp. in Australia (Mann 1970) and South Africa (Zimmermann, Moran & Hoffmann 1986) and Hypericum perforatum in California (Huffaker & Kennett 1959), suggest this to be true for some plant invaders: these were species whose success was dependent upon escape from insect natural enemies. However, the fact that most biological control efforts fail (Crawley 1986) also suggests that these examples may be exceptional. Comparing invasions in which low predator or pathogen loads are important, and the probable majority in which they are not, may improve efforts at biological control as well as our general understanding of biological invasions.
Our results also demonstrate the need for caution. The apparently generalist nature of most soil seed pathogens and the lack of consistent differences between natives and exotics suggest that it may be very difficult to develop control agents or management strategies that target seeds of exotics without negatively affecting at least some natives. For example, attempts to enhance fungal populations, or to deploy fungal biocontrol agents, may equally harm target exotics and susceptible non-target natives. Conversely, fungicide applications may improve recruitment of native species but are likely to increase populations of some exotics as well. Such considerations do not apply only to fungal pathogens. Efforts to reduce the reproduction of exotic plants using insects have had unintended effects on non-target relatives (Pemberton 2000); for example, the flowerhead weevil Rhinocyllus conicus was introduced to North America to control seed production of exotic thistles in the genus Carduus, but has had serious non-target impacts on scarce native thistles as well (Louda et al. 1997). As with other forms of biological control (Simberloff & Stiling 1996a,b), efforts to control exotics by manipulating their seed ecology must be undertaken with great caution.
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- Materials and methods
This research was supported by an NSERC Research Grant to P.M. Kotanen and an NSERC PGS to C.S. Blaney. Additional support was provided by The University of Toronto, the Connaught Fund and Human Resources Development Canada. Many students and volunteers contributed invaluable assistance, including Marc Johnson, Uyen Dias, Bill Kilburn, Vijanti Ramlogan, Joel Sotomayor, Sheenagh Bell and numerous seed collectors. Spencer Barrett, Bob Jefferies, Linda Kohn, and Gary Sprules all contributed invaluable advice and guidance, and comments by Leslie Ambedian and three anonymous referees improved the manuscript. Special thanks to Murray Koffler for his generous and far-sighted donation to the University of Toronto of the property that has become the Joker's Hill research station.
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- Materials and methods
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