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Variation in communities of seed-dispersing ants in habitats with different disturbance in Knox County, Ohio (1).

ABSTRACT. Disturbance may disrupt mutualisms between plants and seed dispersers in a variety of ways including changes in the community of dispersers present. We tested the hypothesis that habitat alteration disrupts the seed-dispersal mutualism between ants and spring-flowering, perennial herbs. Fourteen study sites in Knox County, OH, represented a range of disturbance including mature woodland, woods recovering from partial logging up to 30 years prior to the study, recently logged woods, early successional field, and corn field. Baits were distributed among 480 positions in 48 randomly located transects. Ground-foraging ants were collected and vegetation characteristics of the transects were recorded. In 315 encounters of ants with baits, locations with tuna and seeds of the myrmecochore, Sanguinaria canadensis, were visited at equal rates. Visitation rates to the baits were higher in the more disturbed sites. There was little evidence for depressed ant diversity in disturbed habitats, though ant community composition varied. Seed dispersal distances were likely to be depressed only in agroecosystems, due to the smaller average size of ants, but even this difference is moderated by the tendency for myrmecochores in disturbed sites to have small seeds relative to plants in forest habitats. Where sites have extensive tree canopies the ant communities and dispersal rates are likely to be very resistant to change. Thus, habitat alteration may only affect the ant-plant seed dispersal mutualism in highly and continually disturbed habitats.

INTRODUCTION

Disturbance to ecosystems can change the nature of interactions between species as well as influence the composition of communities. Mutualism where seeds are dispersed by animals is one kind of interaction that might be particularly vulnerable to disturbance, whether that disturbance is caused by invasive species (Bond and Slingsby 1985; Zettler and others 2001; Christian 2001) or by habitat alteration that shifts the composition of species (Andersen and Morrison 1998).

Dispersal of seeds by ants (myrmecochory) involves many species of plants and ants in mesic habitats of North America (Beattie 1985; Holldobler and Wilson 1990). Up to 30% of the ramets of spring-flowering, perennial herbs in these habitats are specialized for having their seeds carried by ground-foraging ants. Typical genera of plants with species using this dispersal syndrome include Asarum, Claytonia, Dentaria, Dicentra, Erythronium, Jeffersonia, Sanguinaria, Trillium, and Viola. Specialization for this mutualism involves plants producing small seeds that have a fat-rich aril (elaiosome). Although ants are not attracted from a distance to these seeds (Sheridan and others 1996), upon contact with the elaiosome, ants are stimulated to carry the elaiosome (and secondarily the attached seed) to their nests. There, the elaiosome is fed to larvae. Undamaged seeds can be deposited outside the nest or may become buried in the nest. Seed dispersal for these plants has both demographic (Hanzawa and others 1988; Kjellsson 1991) and genetic consequences (Kalisz and others 1999). Normally, ground-foraging ants collect insects from the leaf litter and ants are not obligately dependent on myrmecochory, but adding the food resource of elaiosomes can increase a nest's production of gynes (virgin queens) (Morales and Heithaus 1998). Producing more gynes is required for founding new colonies, so this is an important consequence.

Pudlo and others (1980) suggest that disturbance of a forest habitat decreases the diversity of ant fauna, including the numbers of seed-dispersing species, which eventually leads to a reduction in myrmecochorous plant species because of the loss of their seed-dispersing mutualists. In this study, we examined the hypothesis that disturbance disrupts the mutualistic system of myrmecochory. We sampled the ground-foraging ant community and the rate of discovery of baits in a series of habitats that represent a range of disturbance. We asked whether disturbance reduces the probability that ant-dispersed seeds are located and transported.

MATERIALS AND METHODS

Site Selection: Field work for this study was carried out from 23 May 1986 through 8 July 1986 in Knox County, OH. All sites were located within 8.0 km of Gambier, OH, USA. Potential sites were first located on recent aerial photographs obtained from the Ohio State Agricultural Extension Office. We used Sigma-Scan [TM] to digitize and measure areas of each site. Fifty potential sites were then visited, and fourteen sites were selected for study based on accessibility, availability of historical information, and representation across a range of disturbance. Three woodlots were sub-sampled to test for within-site variability, and samples within these different subsites were analyzed separately.

All sites were located on ground moraine deposited by the Wisconsin or Illinoisan glaciers, on upland habitats. Historically, these sites would have been occupied by mixed, deciduous forest (especially Quercus, Acer, Fagus, and Carya). All sites had been modified by some degree of timbering, but they varied in the time since the last harvest, the amount of canopy removed, and the use of the land after removal of trees.

Sites were characterized for "degree of disturbance" using parameters that literature suggests are important for ant communities (canopy closure, litter coverage, and understory coverage). The categories were "Least Disturbed," "Moderately Disturbed," and "Open or Mostly Open Canopy." Site descriptions follow and site characteristics are compared in Table 1.

Low Disturbance

All sites had closed canopy on the 1940 aerial photographs. The understory was comprised of perennial herbs and scattered saplings, with a well-developed layer of leaf litter. Myrmecochores comprised about one-quarter of the species of understory perennial herbs.

"Burns"--This woodlot had remained undisturbed for 30 yr (neither grazing nor selective cutting). Prior to that time, the site had been grazed and selectively cut for oak. The canopy over transects was closed and dominated by Acer saccharum and Quercus alba, with large Fagus grandifolia near but not over the transects.

"Sapp"--The canopy was closed and dominated by Acer saccharum, Carya ovata, and Fraxinus americana; the understory included six species of myrmecochorous plants, and the density of myrmecochores was high

"Crouch"--The canopy was closed at the time of sampling. Acer saccharum and Quercus rubra dominated trees.

Moderate Disturbance

These sites had varying history, but generally there was evidence of more extensive or more recent timber removal than for the Least Disturbed sites. The proportion of myrmecochores in the understory varied, but low frequencies were interpreted as another indication of historical disturbance (see Matlack 1994; Jessen 2000).

"Baube"--This site may have been cleared for row crops prior to 1940, but the canopy was continuous at the time of sampling. Trees tended to be even-aged and dominated by Fraxinus americana and Ulmus rubra

"Heithaus"--This closed-canopy site had been selectively cut at a high intensity prior to 1940, and then selectively cut at a low intensity about fifteen years prior to sampling. Trees were co-dominated by Fraxinus americana, Ulmus rubra, and Acer saccharum.

"Backbone"--Located on the Brown Family Environmental Center at Kenyon College, this woodlot in 1940 consisted of clumps of trees with many open areas. Many of the largest trees (dominated by Quercus alba and Carya glabra) were planted in a forest management program in 1912, and the canopy was continuous at the time of sampling.

"Biology"--A narrow section of closed-canopy woods between the main campus of Kenyon College and State Route 229. The site is more exposed than most other sites to trampling. The trees were dominated by

Quercus alba.

"Mager"--Major overstory trees were Acer saccharum, Ulmus rubra, and Quercus velutina. The understory included two species of myrmecochorous plants. The canopy was continuous in 1940, but some cutting of timber had occurred.

"Lepley"--The canopy was closed and dominated by Acer saccharum, Carya ovata, and Fraxinus americana.

"McPhail"--Although the canopy was mostly closed, tree stumps indicated moderately intensive, selective cutting in the last decade. Understory vegetation was denser than in most other, forested sites. The most common trees over transects were Acer saccharum, Ulmus rubra, and Prunus serotina.

High Disturbance

These sites had major portions of the canopy removed within the last two years. Remnants of the understory were present, but logging activity disrupted the soil surface. Sampling attempted to avoid downed wood and tracks in the soil left by heavy equipment.

"Prescott"--This site is adjacent to a state nature preserve, Knox Woods. Numerous large trees were removed in the spring just prior to sampling (approximately a 40% cu0. Prunus serotina and Acer rubra dominated the remaining overstory.

"Blanchard"--Most trees were removed from this site one year prior to sampling. Much of the understory was dominated by ruderal species, including Rosa multiflora.

Open Canopy

These sites had no trees, and the ground-level vegetation was quite different from that of forested areas.

"Corn"--A cornfield adjacent to the McPhail wooded site, approximately 25 m from the forest edge. Conventional tillage was used in this site.

"Field"--An old field approximately 200 m from the transects in "Heithaus" and adjacent to that woodlot. The field had been mowed in April and twice a year for the six years prior to sampling. Grasses, Solidago spp., and Aster spp. dominated the site.

Transect Location: Transects of 40 meters were established in all sites for both ant and vegetation sampling (see Table 1 for the distribution of transects among sites). To establish transects, we stopped at a haphazard point within the study area. To establish the start of a transect, we then selected a random distance and compass direction (1-360 degrees from north) from a table of random numbers to establish the transects starting point. Then, the direction of the transect from the starting point was, again, selected from a table of random numbers. The number of transects per site is indicated in Table 1.

Habitat Characterization: All herbaceous species within 1.0 m of a transect were identified and species' presence noted. The percentage of each transect covered by herbaceous flora ("percent cover") was determined by counting the number of times a leaf of an herb was above or below a decimeter division of alternating meters along the 40-m transect. All trees that had a branch or leaf overhanging the transect were identified, their location on the transect noted, and their diameters "at breast height" measured. The density and dominance of each species of tree in a transect were calculated and importance values were obtained for each species.

Ant Sampling: Most sampling was done between 10:00 and 14:00 hr. Air and soil surface temperatures were recorded, and we generally attempted to sample ants when the air temperature was at least 20[degrees]C.

Baits were either tuna (canned in oil) or seeds of the myrmecochore, Sanguinaria canadensis. Seeds of S. canadensis were collected from 1-7 June and stored in vials with BHT crystals at 5[degrees]C until the day of sampling, a treatment that preserves attractiveness to ants (Heithaus 1986). Baits were placed at ten, randomly selected points (using a random numbers table) along each 40-m transect. At all sites, similar amounts of tuna were placed on leaf litter or other visible location (for example, bare ground) at each point. Seeds of S. canadensis were used in additional transects at nine sites (ten seeds per point). Baits were monitored at least at 15 min intervals for at least 2 hr. A total of 480 bait stations were used.

When ants were first found at a bait, the time of discovery of that bait was noted. Ants were observed to note their response to the bait (whether it was being investigated or carried) and whether recruitment was occurring. Occasionally, individual ants were followed back to their nests and the distance to the nest was noted. Ants were collected from baits using an aspirator and then killed in cyanide-containing jars.

To supplement collections at baits, we collected ants near, but further than 2.0 m from transects. Visual inspection of ground, vegetation, and litter was done in the time intervals between monitoring transects, for up to 90 min of searching per transect. Ants encountered in these searches were collected with an aspirator and kept separate from collections at baits. This was done to test whether we were missing common species of ants by sampling with tuna and seed baits; visual searching was not intended to be quantitative.

In the laboratory, each ant was mounted on a triangular paper point on an insect pin and the specimen was labeled for date, site, location, bait, and transect point. Ants were identified to genus using Creighton (1950). D. R. Smith kindly identified ants to species; reference specimens are deposited in his collection at the Smithsonian Institution and at the Brown Family Environmental Center at Kenyon College. An ocular micrometer was used to measure alitrunk lengths for up to ten individuals of each species. The length of the alitrunk was used as an index of body size because this is reported in other studies and it appears to be functionally related to an ant's ability to carry loads of different sizes.

Statistical Analysis. Statistical analysis was done with JMP IN [R] 4.0.3 (Academic Version). The proportions of baits located by ants were arcsine transformed before statistical analysis, because raw proportions were not distributed normally. Confidence limits reported are back transformed values. The models for analysis of variance treated sites as nested within disturbance category, and disturbance category as a random effect. Log-Likelihood (G) tests were used for analysis of frequencies (Zar 1999). Species diversity of ants was characterized with the program, EstimateS (Colwell 1997).

RESULTS

From the perspective of an ant-dispersed seed, three questions are important in addressing the quality of seed dispersal services. These are: Will a seed be discovered? Will the seed be moved away from the parent plant? To what microsite will the seed be moved? Here, we present our data in terms of these questions.

The type of bait did not influence the probability that ants would be found at a transect point. This question was addressed by examining the frequency of baits visited by ants, where bait type was nested within site and site effects were included in the model, and also by comparing the frequencies of ant species visiting baits in sites where both types of bait were offered. Tuna and seed baits were similar in the probability of being located by ants (F = 0.65, df = 9, P = 0.74), and in the composition of the ant community visiting the baits (G = 0.02, P >0.995). Consequently, bait types were ignored as a variable when examining questions about the effects of disturbance and temperature on ant visitation patterns.

Both the category of disturbance and differences among sites within these categories influenced the visitation of baits by ants (Fig. 1, Table 2). In the sites with little or no shading from trees, nearly all the baits were visited. In sites with a tree canopy, whether the disturbance was "least" or "moderate," about half the baits were visited in the sampling period. Disturbance category explained 45.5% of the variation in visitation frequency (F = 7.31, df = 3, P = 0.0007). Given the difficulty in categorizing "disturbance," variation among sites within these categories is expected (F = 4.62, df = 11, P= 0.0002). For example, among "moderately disturbed" sites, the visitation rate varied from 13% to 83%, although transects within sites tended to be much more consistent. Much less variation in visitation was observed in the sites with more open canopies, as ants located most baits in those sites.

Higher soil surface temperatures in treeless sites may account for some of the differences in bait discovery among sites. Transects in "open" sites averaged 26.5[degrees]C, while soil surface temperatures in sites for all other categories of disturbance ranged from 18.7 to 20.3[degrees]C (in proportion to the openness of the canopy). Only the "open" sites were statistically distinct from any other sites (F = 12.39, df = 3, P<0.0001), so soil surface temperature alone cannot explain the higher rate of visitation to baits in the highly disturbed sites compared to other forested sites.

We asked whether removal rates of Sanguinaria canadensis seeds varied with disturbance and site. The question is important because plants tend to deposit many seeds in a locality, and dispersal success is influenced by whether ants remove all, or just a fraction, of the available seeds in that locality. For this analysis, we used only transects with seeds, and we evaluated the number of seeds removed if the transect site was visited by ants (Fig. 2). Seven sites had seed baits visited (2--12 baits among sites). Of the ten available seeds per baiting station, ants removed an average of from 4.1 (Burns) to 9.8 seeds (Field). Due to the high number of seeds removed from the open, field site, removal rates were significantly influenced by disturbance category (F = 4.30, df = 3, P = 0.008), and this factor accounted for 25% of the variability in seed removal rates. The general trend was for increasing removal rates in more disturbed habitats as just described, and for relatively low variability in seed removal among sites within disturbance category as indicated by the marginally insignificant effect of sites nested within disturbance categories (F = 2.48, df = 3, P = 0.07).

Another approach to predicting whether seeds will be removed is to evaluate the composition and characteristics of the ant community that would be attracted to seeds.

Twenty-two species of ants were collected in 315 encounters (Table 3). One indication of sampling effectiveness over the entire study is the fact that no additional species of ground-foraging ants were collected in sampling away from baits. Of 95 collections away from baits, only Protomognathus (=Harpagoxenus) americanus was newly encountered; this slave-making species would not be expected to visit baits. Within the forest sites, we encountered seventeen species of ants, and the accumulation curve for the Shannon Index (Fig. 3) indicated sufficient sampling for this parameter over all the sites (Colwell 1997). Within sites, however, due to the low activity of ants, we encountered relatively few individuals and we predict that much more extensive sampling would yield more species (Colwell and Coddington 1994). This would not alter the primary trends identified in this study.

Although all the sampled species of ants are likely to respond to seeds (given that they were attracted to these baits), they also are likely to vary in their behavior with respect to seeds. Ants can vary in whether elaiosomes are detached in situ or whole seeds are transported, and in the distances and destinations of seeds if seeds are transported. These issues will be examined more critically in the discussion, but the size of an ant is one factor influencing its ability to transport a seed. Ant size also is correlated with the foraging distances from nests, a factor influencing transport distance (Holldobler and Wilson 1990; Weseloh 1994; Gomez and Espadaler 1998a).

Among the ants we collected, there was nearly a six-fold increase in alitrunk length from the smallest species (Solenopsis molesta) to the largest (Camponotus pennsylvanicus). With the exception of ants in the cornfield, all sites showed a large range in sizes of ant species. Although the most disturbed, open sites tended to have smaller species of ants (Table 3), successional field transects also were patrolled by Formica spp., which are capable of handling the largest myrmecochorous seeds in our area.

Are seed-carrying ants likely to transport seeds between habitat types? Destinations are a function of both foraging distance and nest location (including habitat specialization), as well as ability of a worker to return the seed to her nest. For species visiting at least 15 baits, analyses of frequencies (G tests) were used to test the null hypothesis of equal distribution among baits in different disturbance categories (P values are Bonferroni corrected for multiple comparisons). Some of the largest species in our study were either restricted to forest areas (Camponotus spp. [G = 8.12, df = 3, P<.05], Myrmica punctiventris [G = 29.7, df = 3, P <0.05]) or were concentrated in sites with grasses and forbs (Formica spp. [insufficient sample for a statistical comparison]). Among the larger ants, Aphaenogaster rudis was found in nearly all types of habitats, but it was under-represented in open sites and over-represented in the least disturbed sites relative to the number of baits used (G = 26.0, df = 3, P <0.05). Many of the smaller species were highly concentrated in the more disturbed sites (for example, Myrmica americana [G = 61.2, df = 3, P <0.01], Tapinoma sessile [G = 46.6, df = 3, P <0.011). Lasius alienus was over-represented in the most disturbed sites, relative to sampling effort [G = 47.9, df = 3, P<0.01], but was found in both forested and open sites.

DISCUSSION

Sampling Issues. Numerous studies indicate that a thorough sampling of ant communities includes litter sampling (Winkler extractions) or pitfall trapping, so it is important to emphasize here that our goal in using baits was to evaluate the foraging activity of ants likely to interact with myrmecochorous seeds. When research has included multiple techniques, few additional species are seen at baits after compiling species lists from pitfall traps and litter extractions (Delabie and others 2000; Wang and others 2001). Also, Bestelmeyer and others (2000) recommend baits as a reasonable measure of ant foraging efficiency. We emphasize that our discussion about "ant community" refers to that set of ants that might interact with elaiosome-bearing seeds.

The set of ants that interact with these seeds includes most, if not all, of the guild of "ground-foraging ants." Our study shows virtual identity between the species of ants collecting tuna and those attracted to myrmecochorous seeds. A study of the reaction of ants to elaiosomes and chemical analysis of elaiosomes suggests a strong convergence between elaiosomes and insects that are prey for ants (Hughes and others 1994). The seventeen species of ants collected in wooded sites in this study compare favorably to other studies of ground-foraging ants in similar habitats (Herbers 1985; Lynch and others 1988; Kaspari and others 2000; Ward 2000; Soares and others 2001; Herbers, pers. comm.). Although some might expect that more ants should have been found in the wooded compared to the open sites, relatively low abundance of ants in forest areas is consistent with the findings of Ferguson (2001).

Monitoring baits for 2 hr appears to allow sufficient time to sample the most common species of ants based on species-accumulation curves and is consistent with that used in other studies using baits. Some caution, however, should be used in interpreting the frequencies of bait discovery with 2 hr monitoring time because the discovery rates are not exactly equivalent to the probability that a bait (or depot of myrmecochorous seeds) would be found eventually. Variation in eventual discovery can arise because ant density can be locally patchy (Weseloh 1994; Weseloh 1995; Kaspari 2001), or because alternative foods are locally common (Smith and others 1989). We use frequencies of discovery for comparative purposes in this paper. We also believe that a 2 hr period is biologically significant because even relatively short delays of several hours in discovery can negatively impact seeds. This is because seeds are then more vulnerable to seed predators such as day-foraging chipmunks or night-foraging deer mice (Heithaus 1981).

Disturbance and the Response of Ground-foraging Ants: Our results suggest that the community of potential seed-carrying ants responds to disturbance over a large spectrum (for example, comparing corn fields, early succession, and wooded sites), but that within wooded sites only small responses are seen as long as the habitat retains substantial shading from a tree overstory. The composition of ant communities changed qualitatively from wooded to open habitats, but only quantitatively within wooded habitats. Potential mechanisms by which disturbance might alter ant communities are through changes in temperature, plant productivity, and the availability of specialized nesting sites (Kaspari 2000; Kaspari 2001). In some ecosystems, habitat specialization appears to be more important than competition in influencing the composition of ant communities at a local scale (Soares and others 2001).

Recently, considerable attention has been given to the responses of ant communities to disturbance both to understand patterns of biodiversity and to assess the potential for using ants as bioindicators (Agosti and others 2000; Kaspari and Majer 2000). A comprehensive review is inappropriate here, but published studies show considerable variation in how ants respond to disturbance. Whether the composition of ant communities responds to disturbance depends, in part, on the ecosystem examined and the extent of disturbance (Roth and others 1994; Andersen 1995; King and others 1998; Peck and others 1998; Whitford and others 1999; Read and Andersen 2000; and Vasconcelos and others 2000). In mesic, forested ecosystems, disturbance can alter ant community composition although ant diversity may not vary substantially (Jennings and others 1986; Kidd and Longair 1997). This is consistent with our results. A thorough community sampling in Knox County woodlots (including all guilds, and not just ground-foragers) might reveal more response of ants to disturbance, but our study supports the view that ground-foraging ants that are potential seed-dispersers are not particularly sensitive to disturbance within wooded habitats. The guild of ground-foragers does change with major alterations in the forest canopy, however, one would not need to sample ants to detect the loss of forest canopy.

The Potential Effect of Varying Ant Communities on Seed Dispersal: Given that the guild of ground-foraging ants occurs in abundance across a wide variety of disturbance regimes, how might shifts in community composition influence the seed-dispersal mutualism? In fynbos shrublands of South Africa, the compositions of plant communities have changed as a result of changes in seed dispersal due to invasion and dominance of a small-bodied ant species (Christian 2001). In the mesic habitats of central Ohio, whether differences in ant communities have a similar effect depends on the degree to which different species of ground-foraging ants are interchangeable from the perspective of seed movement. Although species within this guild are likely to be attracted to seeds, there is interspecific variation in whether seeds are carried, how far seeds are carried, and how seeds are treated and deposited after removal from their original site of deposition (for example, Culver and Beattie 1978; Gorb and Gorb 1999b). Worker size, tendency to recruit, and colony structure are important variables. Small species of ants tend to remove parts of elaiosomes from large-seeded plants, rather than attempt to carry whole seeds (Espadaler and Gomez 1997; Andersen and Morrison 1998), and worker size strongly influences dispersal distance (Beattie and others 1979; Pudlo and others 1980; Weseloh 1994; G6mez and Espadaler 199819). In part, the relative size of ants and seeds is important because foraging distances tend to be smaller for small-bodied ants (H611dobler and Wilson 1990; Weseloh 1994; Gomez and Espadaler 1998a), but also because small ants more frequently drop seeds before they return to their nest (Gorb and Gorb 1999a). For different species of ants, average seed dispersal distances can vary from a centimeter to several meters; worldwide, the average seed dispersal distance based on carrying by ants is under 1.0 m (Gomez and Espadaler 1998a). For colonizing new sites, the "tail" of the dispersal curve may be more important than the average distance a seed might be carried. Extreme distances that ants carry seeds vary from centimeters to approximately 20 m. In temperate, broadleaf forests, dispersal distances average less than a meter, though large-bodied Camponotus spp. sometimes carry seeds 20 m (personal obs.). Finally, ants may differ in how seeds are treated after elaiosomes are removed in the nest by larvae (Beattie and Culver 1982; Heithaus 1986; Gorb and others 2000). To summarize, different species of ground-foraging ants show orders of magnitude differences in proportions of seeds removed and distances seeds are carried, and they vary in other parameters of interacting with seeds (though the impacts of those differences on plant evolution and demography is yet to be determined [Beattie 1991]).

How might differences in communities of ground-foraging ants in Knox County affect the dispersal of myrmecochorous seeds? In spite of their different ant communities and disturbance histories, a row-cropped agroecosystem, an early successional field, and diverse wooded areas differ little in whether myrmecochorous seeds are likely to be encountered and dispersed by ants. Although apparently in conflict with the conclusions of Pudlo and others (1980), our results are not strictly comparable. Their three study sites were at different altitudes or in different states (West Virginia and Illinois), and the most disturbed site included flooding events; while our study was within a single county and disturbance did not include flooding (which is more likely than forest clearing to have major, negative effects on ants). Their study examined dispersal of Sanguinaria canadensis seeds, which are at the large end of the range in size for myrmecochores; this would be expected to be among the most sensitive plants to variation in ant communities. In our study, we measured whether ants would encounter depots of any species of myrmecochore. For example, in our agroecosystem, where ant species tend to be smaller, local myrmecochorous plants (for example, Viola spp.) also tend to have small seeds, so that dispersal is likely to be successful for these more ruderal species. In fact, the foraging activity of ants tends to be high in the more exposed habitats (also see Bestelmeyer 1997), so dispersal frequency (if not distance) may be higher in more disturbed habitats. Myrmecochory, as a general dispersal strategy, should be successful within a wide range of habitats in Knox County. A similar result has been found in a range of sites and habitats in Australia (Andersen and Morrison 1998). The prediction for particular plant species, however, depends on the size of their seeds and the need for distance dispersal.

Ants appear to be poor promoters of colonization for plants. In addition to transporting seeds short distances, ants are relatively specialized in their choices of microhabitats or habitats (Holldobler and Wilson 1990; Soares and Schoereder 2001). Studies of plant colonization in disturbed areas show that ant-dispersed plants are slow to move into restored or recovering sites compared to species with other seed dispersal mechanisms (Matlack 1994; McLachlan and Bazely 2001).

The seed-ant mutualism, as a general adaptation, is apparently quite resilient. Plants that have adapted to conditions of disturbance (particularly those with small seeds) are likely to have their seeds dispersed. For forest species with relatively large seeds, however, new disturbance may negatively affect dispersal through the disproportionate loss of large-bodied ants from the local community. The long-distance colonization of new sites through other types of habitats appears to be much less likely. For plants adapted to old-growth forests, dispersal by ants probably could carry seeds into sites disturbed by selective logging. Here, the limit to colonization of moderately disturbed sites appears to be based on distance, not the habitat specialization of ground-foraging ants.
TABLE 1

Characteristics of study sites in Knox County, OH. "Ground Cover" was
calculated using a line intercept method along 20 m segments of each
transect. "Largest Tree Diameters" is the mean diameter of the three
largest trees intersect. "Percent Myrmecochore" reflects the
proportion of species of understory herbs along transects that have
their seeds dispersed by ants. See text for definitions of disturbance
categories.

 Number of
Site Area (ha) W. Long/N. Lat Transecrs

Bums 247 82.377/40.358 6
Sapp 101 82.320/40.404 6
Crouch 74 82.401/40.337 2
Baube 247 82.376/40.356 3
Heithaus 153 82.419/40.400 2
Backbone 148 82.418/40.383 4
Biology 90 82.400/40.372 2
Magers 74 82.405/40.334 2
Lepley 35 82.373/40.391 6
McPhail 30 82.356/40.362 5
Prescott 252 82.429/40.402 3
Blanchard 153 82.413/40.395 2
Corn 99 82.359/40.363 2
Field 15 82.419/40.400 3

 % Ground Largest Tree Number of
Site Cover Diameters (cm) Myrmecochores

Bums 50 85 6
Sapp 45 59 6
Crouch 20 61 4
Baube 65 43 2
Heithaus 27 48 3
Backbone 42 92 1
Biology 59 65 1
Magers 44 54 2
Lepley 55 54 1
McPhail 45 63 2
Prescott 66 63 3
Blanchard 95 44 1
Corn 0 0 0
Field 100 0 0

 Percent Disturbance
Site Myrmecochores Category

Bums 27 low
Sapp 28 low
Crouch 24 low
Baube 13 moderate
Heithaus 25 moderate
Backbone 13 moderate
Biology 13 moderate
Magers 16 moderate
Lepley 8 moderate
McPhail 30 moderate
Prescott 20 high
Blanchard 5 high
Corn 0 open
Field 0 open

TABLE 2

The rate of visitation to baits among different sites.
Visitation varied among sites within category of
disturbance (F = 4.62, df = 11, P = 0.0002).

Site Disturbance Prop Visited S. E.

Burns least 0.35 0.016
Sapp least 0.45 0.014
Crouch least 1.00 0.0
Baube moderate 0.13 0.024
Heithaus moderate 0.65 0.003
Backbone moderate 0.42 0.016
Biology moderate 0.55 0.003
Magers moderate 0.40 0.044
Lepley moderate 0.83 0.034
McPhail moderate 0.26 0.023
Prescott high 0.90 0.019
Blanchard high 0.80 0.113
Corn open 0.90 0.0
Field open 1.00 0.0

TABLE 3

The frequency of baits visited by ants in fourteen sites (see Table 1)
in Knox County, OH, and alitrunk lengths (in mm) for observed species.
Species are ordered by alitrunk length. The 315 visits by more than
one species of ant). Of 95 collections of ants away from baits, only
one additional species was encountered (Protomognathus (=Harpagoxenus)
americanus in a moderately disturbed site). Average sizes of ants were
calculated considering frequency (weighted mean alitrunk length) and
simply by observed species (unweighted mean alitrunk length).

 Disturbance Category
Species attracted to baits Low Mod High Open

Camponotus pennsylvanicus 3 9 4 0
Camponotus ferrugineus 4 6 1 0
Formica subsericea 0 0 1 7
Camponotus nearcticus 0 1 0 0
Formica pallidefulva nitidiventris 0 0 0 3
Aphaenogaster tennesseensis 1 0 0 0
Aphaenogaster rudis 61 67 28 9
Camponotus subbarbatus 0 1 0 0
Myrmica lobicornis fracticornis 0 0 0 1
Lasius umbratus 0 2 0 0
Myrmica americana 0 1 0 14
Myrmica punctiventris 1 19 10 0
Prenolepis imparis 0 0 0 1
Tapinoma sessile 0 1 0 11
Lasius alienus 1 16 4 18
Lasius neoniger 0 0 0 1
Stenamma brevicorne 0 1 0 1
Stenamma impar 0 1 0 0
Stenamma schmittii 0 1 0 0
Leptothorax longispinosus 0 1 0 0
Leptothorax curvispinosus 1 2 0 0
Solenopsis molesta 0 0 0 1

Weighted mean alitrunk lengths 1.66 1.52 1.56 1.21
Unweighted mean alitrunk Ingths 1.72 1.39 2.00 1.18
Number of baits visited 72 129 48 67
Number of species 7 15 6 10
Number unique species 1 6 0 4

 Length of
 Alitrunk
Species attracted to baits (mm)

Camponotus pennsylvanicus 3.25
Camponotus ferrugineus 3.10
Formica subsericea 2.25
Camponotus nearcticus 2.20
Formica pallidefulva nitidiventris 2.00
Aphaenogaster tennesseensis 1.63
Aphaenogaster rudis 1.53
Camponotus subbarbatus 1.56
Myrmica lobicornis fracticornis 1.28
Lasius umbratus 1.16
Myrmica americana 1.15
Myrmica punctiventris 1.03
Prenolepis imparis 0.96
Tapinoma sessile 0.93
Lasius alienus 0.85
Lasius neoniger 0.80
Stenamma brevicorne 0.77
Stenamma impar 0.77
Stenamma schmittii 0.70
Leptothorax longispinosus 0.70
Leptotborax curvispinosus 0.65
Solenopsis molesta 0.44

Weighted mean alitrunk lengths
Unweighted mean alitrunk Ingths
Number of baits visited
Number of species
Number unique species


ACKNOWLEDGMENTS. Thanks to Greg Mosolf and Patricia Heithaus for assisting with vegetation sampling and other fieldwork. Thanks also to Michael Heithaus, Joan Herbers, and an anonymous reviewer for suggestions that improved this manuscript. Kenyon College supported research for this project through its Summer Science Scholarship program for undergraduate research.

(1) Manuscript received 20 November 2001 and in revised form 1 July 2002 (#01-31)

LITERATURE CITED

Agosti D, Majer JD, Alonso LE, Schultz TR. 2000. Ants: Standard Methods for Measuring and Monitoring Biodiversity. Washington and London: Smithsonian Institution Pr. 280 p.

Andersen AN. 1995. A classification of Australian ant communities, based on functional groups which parallel plant life-forms in relation to stress and disturbance. J Biogeography 22(1):15-29.

Andersen AN, Morrison SC. 1998. Myrmecochory in Australia's seasonal tropics: effects of disturbance on distance dispersal. Australian J Ecology 23(5):483-91.

Beattie AJ. 1985. The Evolutionary Ecology of Ant-plant Mutualisms. Cambridge (MA): Cambridge Univ Pr.

Beattie AJ. 1991. Problems outstanding in ant-plant interaction research. In: Huxley CR, Cutler DF, editors. Ant-Plant Interactions. Oxford: Oxford Univ Pr. p 559-76.

Beattie AJ, Culver DC. 1982. Inhumation: how ants and other invertebrates help seeds. Nature 297:627.

Beattie AJ, Culver DC, Pudlo RJ. 1979. Interactions between ants and the diaspores of some common spring-flowering herbs in West Virginia. Castanea 44:177-86.

Bestelmeyer BT. 1997. Stress tolerance in some Chacoan dolichoderine ants: implications for community organization and distribution. J Arid Environments 35:297-310.

Bestelmeyer BT, Agosti D, Alonso LE, Brandao CRF, Brown WL Jr, Delabie JHC, Silvestre R. 2000. Field techniques for the study of ground-dwelling ants. In: Agosti D, Majer JD, Alonso LE, Schultz TR, editors. Ants: Standard Methods for Measuring and Monitoring Biodiversity. Washington (DC): Smithsonian Institution Pr. p 122-44.

Bond W, Slingsby P. 1985. Collapse of an ant-plant mutualism: The Argentine ant (Iridomyrmex humilis) and myrmecochorous Proteaceae. Ecology 65(4):1031-7.

Christian CE. 2001. Consequences of a biological invasion reveal the importance of mutualism for plant communities. Nature 413:635-9.

Colwell RK. 1997. EstimateS: Statistical estimation of species richness and shared species from samples. Version 5. User's Guide and Application. Published at: Http://Viceroy.Eeb.Uconn.Edu/ Estimates

Colwell RK, Coddington JA. 1994. Estimating terrestrial biodiversity through extrapolation. Philosophical Transactions of the Royal Society (Series B) 345:101-18.

Creighton WS. 1950. The Ants of North America. Cambridge (Ma): Cosmos Pr. 585 p.

Culver DC, Beattie AJ. 1978. Myrmecochory in Viola: dynamics of seed-ant interactions in some West Virginia species. J Ecology 66:53-72.

Delabie JHC, Fisher BL, Majer JD, Wright IW. 2000. Sampling effort and choice of methods. In: Agosti D, Majer JD, Alonso LE, Schultz TR, editors. Ants: Standard Methods for Measuring and Monitoring Biodiversity. Washington (DC): Smithsonian Institution Pr. p 145-54.

Espadaler X, Gomez C. 1997. Soil surface searching and transport of Euphorbia characias seeds by ants. Acta Oecologica 18(1):39-46.

Ferguson S. 2001. Changes in trophic abundance of soil arthropods along a grass-shrub-forest gradient. Canadian J Zoology-Revue Canadienne Zoologie 79:457-64.

Gomez C, Espadaler X. 1998a. Myrmecochorous dispersal distances: a world survey. J Biogeography 25:573-80.

Gomez C, Espadaler X. 1998b. Seed dispersal curve of a Mediterranean myrmecochore: influence of ant size and the distance to nests. Ecological Research 13:347-54.

Gorb SN, Gorb EV. 1999a. Dropping rates of elaiosome-bearing seeds during transport by ants (Formica polyctena Forest.): implications for distance dispersal. Acta Oecologica-International J Ecology 20(5):509-18.

Gorb SN, Gorb EV. 1999b. Effects of ant species composition on seed removal in deciduous forest in Europe. Oikos 84(1):110-18.

Gorb SN, Gorb EV, Punttila P. 2000. Effects of redispersal of seeds by ants on the vegetation pattern in a deciduous forest: a case study. Acta Oecologica-Intemational J Ecology 21(4-5):293-301.

Hanzawa FM, Beattie AJ, Culver DC. 1988. Directed dispersal: demographic analysis of an ant-seed mutualism. American Naturalist 131(1):1-13.

Heithaus ER. 1981. Seed predation by rodents on three ant-dispersed plants. Ecology 62:136-45.

Heithaus ER. 1986. Seed dispersal mutualism and the population density of Asarum canadense, an ant-dispersed plant. In: Estrada A, Fleming TH, Dirzo R, Vasquez-Yanes SC, editors. Frugivores and seed dispersal. Dordrecht: Dr W. Junk Publishers. p 199-210.

Herbers JM. 1985. Seasonal structuring of a north temperate ant community. Insectes Sociaux 32(3):224-40.

Ho11dobler B, Wilson EO. 1990. The ants. Cambridge (MA): Belknap Pr of Harvard Univ Pr. 732 p.

Hughes L, Westoby M, Jurado E. 1994. Convergence of elaiosomes and insect prey: evidence from ant foraging behaviour and fatty acid composition. Functional Ecology 8:358-65.

Jennings DT, Houseweart MW, Francoeur A. 1986. Ants (Hymenoptera: Formicidae) associated with strip-clearcut and dense spruce-fir forests of Maine, USA. Canadian Entomologist 118(1):43-50.

Jessen GB. 2000. The impact of forest continuity and management on forest floor vegetation evaluated by species traits. Ecography 23(6):720-31.

Kalisz S, Hanzawa FM, Tonsor SJ, Thiede DA, Voigt S. 1999. Antmediated seed dispersal alters pattern of relatedness in a population of Trillium grandiflorum. Ecology 80(8):2620-34.

Kaspari M. 2000. A primer on ant ecology. In: Agosti D, Majer JD, Alonso LE, Schultz TR, editors. Ants: Standard Methods for Measuring and Monitoring Biodiversity. Washington (DC): Smithsonian Institution Pr. p 9-24.

Kaspari M. 2001. Taxonomic level, trophic biology and the regulation of local abundance. Global Ecology and Biogeography 10(3):229-44.

Kaspari M, Majer JD. 2000. Using ants to monitor environmental change. In: Agosti D, Majer JD, Alonso LE, Schultz TR, editors. Ants: Standard Methods for Measuring and Monitoring Biodiversity. Washington (DC): Smithsonian Institution Pr. p 89-98.

Kaspari M, O'Donnell S, Kercher JR. 2000. Energy, density, and constraints to species richness: ant assemblages along a productivity gradient. American Naturalist 155(2):280-93.

Kidd MG, Longair RW. 1997. Abundance and diversity of ant (Hymenoptera: Formicidae) assemblages in regenerating forests of northern Saskatchewan. Canadian Field-Naturalist 111(4):635-7.

King JR, Andersen AN, Cutter AD. 1998. Ants as bioindicators of habitat disturbance: validation of the functional group model for Australia's humid tropics. Biodiversity and Conservation 7(12):1627-38.

Kjellsson G. 1991. Seed fate in an ant-dispersed sedge, Carex pilulifera L.: recruitment and seedling survival in tests of models for spatial-dispersion. Oecologia 88(3):435-43.

Lynch JF, Johnson AK, Balinsky EC. 1988. Spatial and temporal variation in the abundance and diversity of ants (Hymenoptera: Formicidae) in the soil and litter layers of a Maryland, USA forest. American Midland Naturalist 119(1):31-44.

Matlack GR. 1994. Plant species migration in a mixed-history forest landscape in eastern North America. Ecology 75(5): 1491-502.

McLachlan SM, Bazely DR. 2001. Recovery patterns of understory herbs and their use as indicators of deciduous forest regeneration. Conservation Biology 15(1):98-110.

Morales MA, Heithaus ER. 1998. Food gained from seed dispersal mutualism shifts sex ratios in colonies of the ant, Aphaenogaster rudis. Ecology 79:734-9.

Peck SL, McQuaid B, Campbell CL. 1998. Using ant species (Hymenoptera: Formicidae) as a biological indicator of agroecosystem condition. Environmental Entomology 27(5):1102-10.

Pudio RJ, Beattie AJ, Culver DC. 1980. Population consequences of changes in an ant-seed mumalism in Sanguinaria canadensis. Oecologia 146:32-7.

Read JL, Andersen AN. 2000. The value of ants as early warning bioindicators: responses to pulsed cattle grazing at an Australian arid zone locality. J Arid Environments 45(3):231-51.

Roth DS, Perfecto I, Rathcke B. 1994. The effects of management-systems on ground-foraging ant diversity in Costa Rica. Ecological Applications 4(3):423-36.

Sheridan SL, Iverson KA, ltagaki H. 1996. The role of chemical senses in seed-carrying behavior by ants: a behavioral, physiological, and morphological study. J Insect Physiology 42(2):149-59.

Smith BH, DeRivera CE, Bridgman CL, Woida JJ. 1989. Frequency-dependent seed dispersal by ants of two deciduous forest herbs. Ecology 70(6):1645-8.

Soares SM, Schoereder JH. 2001. Ant-nest distribution in a remnant of tropical rainforest in southeastern Brazil. Insectes Sociaux 48:280-6.

Soares SM, Schoereder JH, DeSouza O. 2001. Processes involved in species saturation of ground-dwelling ant communities (Hymenoptera: Formicidae). Austral Ecology 26(2):187-92.

Vasconcelos HL, Vilhena JMS, Caliri GJA. 2000. Responses of ants to selective logging of a Central Amazonian forest. J Applied Ecology 37(3):508-14.

Wang CL, Strazanac J, Butler L. 2001. A comparison of pitfall traps with bait traps for studying leaf litter ant communities. J Economic Entomology 94(3):761-5.

Ward PS. 2000. Broad-scale patterns of diversity in leaf litter ant communities. In: Agosti D, Majer JD, Alonso LE, Schultz TR, editors. Ants: Standard Methods for Measuring and Monitoring Biodiversity. Washington (DC): Smithsonian Institution Pr. p 99-121.

Weseloh RM. 1994. Spatial distribution of the ants Formica subsericia, F. neogagates, and Aphaenogaster fulva (Hymenoptera: Formicidae) in Connecticut. Environmental Entomology 23(5): 1165-70.

Weseloh RM. 1995. Forest characteristics associated with abundance of foraging ants (Hymenoptera: Formicidae) in Connecticut. Environmental Entomology 24(6):1453-7.

Whifford WG, Van Zee J, Nash MS, Smith WE, Herrick J. 1999. Ants as indicators of exposure to environmental stressors in North American Desert grasslands. Environmental Monitoring and Assessment 54(2):143-71.

Zar JH. 1999. Biostatistical Analysis, Fourth Edition. Upper Saddle River (NJ): Prentice-Hall. 929 p.

Zettler JA, Spira TP, Allen CR. 2001. Ant-Seed mutualisms: can red imported fire ants sour the relationship? Biological Conservation 101(2):249-53.

E. RAYMOND HEITHAUS AND MARCIA HUMES, Biology Department. Kenyon College, Gambier, OH 43022
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