Open Access
1 April 2004 Distribution, spread, and ecological associations of the introduced ant Pheidole obscurithorax in the southeastern United States
Shonna R. Storz, Walter R. Tschinkel
Author Affiliations +

A field survey of the southeastern United States showed that Pheidole obscurithorax Naves, an ant introduced from South America, inhabits a 80-km-wide band along the coast between Mobile, Alabama, and Tallahassee, Florida, and is continuing to increase its range. In Tallahassee P. obscurithorax is rapidly spreading, and its nest density increased by a factor of 6.4 over a two-year period. Evidence suggests that P. obscurithorax has spread gradually by natural means. It coexists with the fire ant Solenopsis invicta Buren, appears to be part of a largely exotic community of ants that are tolerant of highly disturbed habitats, and seems to have little negative effect on the ant communities that it invades.


Species introduced to new areas, whether naturally or by humans, can alter the receiving community. These invasive species are increasingly recognized for the economic and conservation problems they create through direct (competition, predation, herbivory, parasitism, hybridization, habitat alteration) and indirect effects on a community (Elton, 1958; Vitousek et al. 1987; Pimm 1991; Simberloff et al. 1997; Brown and Lomolino 1998; Manchester and Bullock 2000; Pimentel et al. 2001). Elton's (1958) early view that disturbed and less speciose habitats are most susceptible to invading species is now thought to be overly simplistic. The success of an invader in any habitat depends on the species present, their interactions within the community, their interactions with the invading species (Simberloff 1986), and the historical path by which the community arose (Vermeij 1991; Lodge 1993). This complexity is often compounded by the presence and effects of nonindigenous species already present in the community (Simberloff 1997), by the amount of disturbance to the habitat (Tschinkel 1988), and by the location and size of the area being invaded (Brown and Lomolino 1998; Holway et al. 2002). Of the many invading organisms, social insects are among the most destructive. They affect large geographic areas, damage agricultural systems, are expensive to control, and reduce biodiversity in the communities they invade (Vinson 1986; McKnight 1993; Williams 1994; Simberloff 1997). Among these, the fire ant Solenopsis invicta Buren and the Argentine ant, Linepithema humile Mayr, are well-known invaders of North America that disrupt ant and other arthropod communities (Porter and Savignano 1990; Holway 1998; Gotelli and Arnett 2000).

Given the publicity about destructive invasive organisms, introduced species that have little effect on the communities they invade are often overlooked, and ants are no exception. McGlynn (1999) reported that only 2% (147/9358) of all known ant species have become established outside their native ranges and that only 6% (9/147) of these are considered invasive in that they out compete native ants. Within Florida alone, a hot spot for introduced species, 25% (52/207) of the ant fauna is exotic and only 3% (7/207) are “potential ecological villains” (Deyrup et al. 2000). Many introduced species that do not have large obvious effects on communities often go unnoticed and are understudied, while a small number of invaders are studied in great detail (Vermeij 1996; McGlynn 1999). Regardless of the apparent effects of invaders, documenting their distributions, habitat characteristics, and species associations as well as investigating any effects they have on the communities they invade, be they small or large, is important for future comparisons.

Pheidole obscurithorax Naves is an ant native to northern Argentina and Paraguay (Wilson 2002). It occurs in mature flood plain and open pasture along the Parana River (A. V. Suarez, personal communication) and presumably along the Paraguay River, which are traveled by ocean-going vessels. Its occurrence in North America was first observed in the port city of Mobile, Alabama, in the early 1950s (Naves 1985; under the name, P. fallax obscurithorax). Several other ant species with ranges along the Paraguay River system (Brachymyrmex patagonicus Mayr, Linepithema humile, Solenopsis invicta, and Solenopsis richteri Forel) have been transported to the southeastern United States via the ports of New Orleans, Mobile, and Pensacola (Naves 1985). Pheidole obscurithorax coexists in disturbed habitats with the fire ant Solenopsis invicta, which was introduced at Mobile in the late 1930s (Buren et al. 1974), but has been much slower to expand its range, the extent of which is unknown. It was first observed in Tallahassee, Florida (400 km east of Mobile), in 1998 (W. R. Tschinkel, personal observation). To date no documented investigations of P. obscurithorax have been conducted, although its occurrence in the southeastern United States is well documented (Naves 1985; McGlynn 1999; Deyrup et al. 2000; Wilson 2002). The goals of the study reported here were to determine (1) its range and likely site of introduction in the southeastern United States, (2) whether any habitat characteristics are associated with its success, and (3) whether it is associated with differences in ant communities across its range and (4) to document its spread and population increase in Tallahassee, Florida, over a two-year period.

Materials and Methods

Southeast survey

A field survey was conducted during the summer of 2001 across five states (Florida, Georgia, Alabama, Mississippi, and Louisiana) in the southeastern United States. Approximate site locations were initially chosen such that they were located 80 to 96 km apart along five east-west transects centered on the longitude of Mobile (presumed site of entry) spanning and extending beyond the expected range of P. obscurithorax. The initial survey determined that P. obscurithorax occupied a much smaller range than expected. We therefore implemented a second, more intensive sampling regime, involving sites at 40-km intervals within the smaller potential geographic range of P. obscurithorax, which resulted in a larger sample of sites with P. obscurithorax. Fifty-five sites were surveyed; 41 of these were located within the second sampling area described above. The map shows all 55 sites (Fig. 1), but to avoid any bias due to uneven sampling or the inclusion of sites potentially not suitable for P. obscurithorax, we included only the data collected from the 41 sites within the second sampling area for all analyses.

All sites were located on rights of way along two-lane highways as in Porter et al. (1991). Characteristics were recorded at every site (latitude, longitude, elevation, surrounding vegetation type, type and percent of ground cover, grass height, and soil and air temperature), soil samples were collected, and standard survey methods (Porter et al. 1991) were used to estimate the nest densities of three conspicuous and easily identifiable ant species (Dorymyrmex bureni Trager, P. obscurithorax, and S. invicta). More specifically, ant nests were counted along four transects parallel to the road, two on each side of the highway (one along the pavement and the other along the tree/shrub line). Each transect was 54 m long by 2 m wide (108 m2) for a total of 432 m2 surveyed per site.

Bait traps were used at each site to collect ground-foraging ants. In order to attract and collect a wide array of ant species, we used two bait types placed inside individual glass test tubes—oil-rich carbohydrate (shortbread cookie crumbs) and protein (hot dog pieces)—and three collection times (15, 30, and 45 min). The use of cookie crumbs may allow less-dominant species to remain at baits with dominant species, and the use of time intervals may allow collection of both quick recruiters and those that are slower to recruit but may eventually dominate the bait (Bestelmeyer et al. 2000). At each site 60 baits were arranged linearly into groups of six (three carbohydrate and three protein) such that each group was placed 10 m from the next; baits within each group were arranged hexagonally with 1m spacing. Two previously designated baits from each group (one carbohydrate and one protein) were collected at each of the three collection times. Ants collected at baits were taken to the lab, counted, and identified to species (species identifications were aided by M. Deyrup; see Appendix I and II for site localities and species presence data).

Ant species abundance was estimated as the total number of bait tubes at each site that trapped a particular species rather than the number of individual ants trapped (counts of individual ants are estimates of both recruitment effort and abundance). Because the number of individuals collected is correlated with increasing number of species, and because of controversy over the use of diversity indices (Hurlbert 1971; Heck et al. 1975; James and Rathbun 1981; Gotelli and Colwell 2001), we used EstimateS software (Colwell 2000) to generate rarefaction curves to estimate expected number of species (species richness) at sites with and without P. obscurithorax.

We used the hydrometer method to conduct soil-texture analyses on the collected soil samples in order to determine the proportions of sand, clay, and silt at each site (Bouyoucos 1927, 1936, 1962).

Because of the unexpected distribution of P. obscurithorax (see results below), we tested the a posteriori hypothesis that wind direction after summer rains influences the flight paths of ants on mating flights or of newly mated queens. We collected precipitation and wind data for Mobile Regional Airport for four years (1998–2001) from the NOAA database online. For a randomly selected subset (n = 25) of the 76 days on which 0.25–1 inch of rain fell during June–July, wind speed and direction were collected. We used a Rayleigh test (Batschelet 1965) to determine whether a particular wind direction predominates.

Pitfall-trap study

During the summer of 2002 a pitfall-trap study was conducted in Tallahassee, Florida. This study was designed to complement our investigation of P. obscurithorax's associations with ant communities over a large geographic area (southeast survey) but on a smaller scale. Eight roadside sites were chosen in Tallahassee where P. obscurithorax occurred at varying nest densities (40–600 nests per ha) and had an average of 275 nests per ha. Roadside sites had similar habitat characteristics (ground cover, surrounding vegetation, % canopy, etc.). At each site 10 pitfall traps were spaced 10 m apart along linear transects. Pitfall traps consisted of 50-ml plastic centrifuge tubes partially filled with 15 ml of a soap/propylene-glycol solution buried with their openings (32 mm diameter opening) flush with the ground surface. All 80 traps were set up on the same day and were left in place, undisturbed, for seven days (560 trap days). On the seventh day all traps were collected and the holes filled. Trap contents were sorted manually or by salt extraction (Lattke 2000) depending on the amount of debris collected in the trap. All ants were counted and identified to species. Pitfall traps are commonly used to estimate the abundances and species compositions of ground-foraging ants (Bestelmeyer et al. 2000). Although they have been shown to sample species compositions adequately, they tend to be biased toward fast-moving species (Andersen 1991).

For each ant species, abundance was calculated as the number of individuals captured per pitfall trap. To investigate the association between P. obscurithorax abundance and species richness, we constructed rarefaction curves based on the number of species captured in each trap for three categories of P. obscurithorax abundance: (1) low (0 to 8 P. obscurithorax captured), (2) moderate (9 to 17 P. obscurithorax captured), and (3) high (>17 P. obscurithorax captured).

Tallahassee survey

Twenty-one roadside sites were surveyed in Tallahassee, Florida, during June 2000 and again during June 2002. At each site we estimated P. obscurithorax nest densities by counting visible nests along linear transects from 54 to 108 m long and 1 m wide (at least 54 m2 per site).


General observations

Pheidole obscurithorax is a large, dark ant up to 6 mm in length, and its workers are dimorphic; the majors are larger than the minors and have enlarged heads. It nests in soil in open areas, where it produces conspicuous nests, each generally with a single large (1- to 5-cm-wide) opening often covered by a leaf or other collected material. During one successful excavation of a colony in Tallahassee, a single queen was located 3m below the surface. Pheidole obscurithorax is omnivorous and collects a variety of arthropod prey, including other ants, and less frequently plant material such as flower petals. Its midden piles are often littered with heterospecific ant body parts, especially those of S. invicta, an abundant ant often found nesting near P. obscurithorax nests. Pheidole obscurithorax uses a combination of foraging tactics; if a prey item is small enough, scouts carry it unaided back to the nest. If the prey item is too large, teams of workers carry the prey to the nest whole. The size of prey handled and the speed at which it is carried to the nest are remarkable. The workers defend their prey items from other ants, including S. invicta, and P. obscurithorax both wins battles and loses them. Although little is known about its reproductive biology, small mating flights before dawn after summer rains have been observed (S. R. Storz, personal observation).

Southeast survey

P. obscurithorax inhabits a 80-km-wide band along the coast between Mobile, Alabama, and Tallahassee, Florida. Its highest nest density occurred north of Pensacola, Florida (Fig. 1). P. obscurithorax nest density declined with increasing distance from Mobile and Pensacola (Pearson r = −0.55 and r = −0.69 respectively, P < 0.05). P. obscurithorax abundance (number of bait tubes) also declined with increasing distance from Mobile (Pearson r = −0.50, P < 0.05) but not from Pensacola (Pearson r = 0.03, P > 0.20). P. obscurithorax presence was associated with shorter grass. Average grass height was greater at sites where P. obscurithorax was absent than that at sites where they were present (15.77 ± 0.87 cm vs. 12.08 ± 1.14 cm, average ± standard error; t = −2.63, d.f. = 39, P < 0.02). Within these roadside habitats, P. obscurithorax was not associated with any other habitat characteristics measured (Table 1). Grass height was not correlated with distance from Mobile or Pensacola.

If P. obscurithorax was introduced in Mobile, it appeared to have spread more extensively to the east (Fig. 1). We therefore hypothesized that, if winds blow predominately to the east after summer rains, the wind forces alates to fly eastward during mating flights which may explain the eastward spread of P. obscurithorax. For the 25 days of weather data collected, wind speed ranged from 0.7 to 9.2 mph. No predominant wind direction was detected (Rayleigh test, z = 1.8, P > 0.05) (Batschelet 1965).

Over 86,600 ants were collected at 1733 baits. Nineteen species of ants were collected, and the frequencies with which they occurred at the 41 sites were highly skewed. S. invicta occurred at 100% of the sites, whereas all other species occurred at less than 40% (Fig. 2). The collections followed a typical pattern of a few common species and many rare species. The proportions of bait tubes occupied by each ant species and the respective proportions of total ants collected showed a similar pattern. Eighty-five percent of the bait tubes were occupied by S. invicta, whereas the second and third most abundant species were D. bureni and P. obscurithorax, which occurred in 5 and 2% of the tubes respectively. S. invicta represented 92% of the individual ants collected. No other ant species represented more than 2% of the total, but their relative rankings differed somewhat from those of the frequencies collected at bait tubes (Fig. 2).

The abundances of the six most common ant species were not associated with either P. obscurithorax presence (Table 2) or its nest density (Table 3). Expected species richness estimated from the rarefaction curves was higher where P. obscurithorax was absent than where they were present (t = 29.3, df = 98, P < 0.0005) (Fig. 3). When approximately 800 ants are sampled, eight species are expected at sites with P. obscurithorax, but 16 species are expected at sites without P. obscurithorax. In fact, eight species of ants collected within the smaller sampling area (Camponotus floridanus Buckley, Forelius analis Andre, Formica schaufussi Mayr, Linepithema humile, Monomorium viride Brown, Odontomachus brunneus Patton, Pheidole dentata Mayr, and Pheidole morrisi Forel) were absent from sites occupied by P. obscurithorax, but many of these are common woodland species.

Pitfall-trap study

In the 80 pitfall traps, 2493 ants were captured, and 26 species were represented. Similar to those in the bait study, the distributions of percent of pitfall traps capturing each species and their relative abundances in the traps were highly skewed, but P. obscurithorax occurred in nearly as many pitfall traps as S. invicta and was ranked a close second in abundance behind S. invicta (Fig. 4). Interestingly, six of the seven most common ant species are introduced (Solenopsis invicta, Pheidole obscurithorax, Brachymyrmex musculus, Cyphomyrmex rimosus, Pheidole moerens, Cardiocondyla nuda).

P. obscurithorax abundance is not negatively associated with any of the six most common species' abundances. Rather, P. obscurithorax is positively, but weakly, associated with two of the commonest species (Brachymyrmex musculus Forel and Cyphomyrmex rimosus Spinola) (Spearman rank correlation, r = 0.30 and 0.29 respectively, P < 0.05). P. obscurithorax abundance is also positively, but weakly, associated with total ant abundance (Spearman rank correlation, r = 0.24, P < 0.05).

Expected species richness estimated from the rarefaction curves is highest in the low P. obscurithorax category and lowest in the high P. obscurithorax category, and the expected species richness of the moderate category falls in between (Fig. 5). The species-richness curve representing the high P. obscurithorax category is also shallower than the other two curves, suggesting a less even species distribution.

Tallahassee survey

P. obscurithorax nest density at the 21 roadside sites was greater in 2002 than that in 2000 (302.8 ± 87.2 nests per ha vs. 47.4 ± 20.6 nests per ha, average ± standard error; Wilcoxon matched pairs test, P < 0.001). On average, P. obscurithorax nest density in Tallahassee increased by a factor of 6.4 in two years. Nest density in June 2000 and nest density in June 2002 were positively related (Spearman rank test, P < 0.05; Fig. 6). With one exception, all sites occupied by P. obscurithorax in 2000 increased in nest density over the two-year period. Of the 14 sites not occupied by P. obscurithorax in 2000, seven were invaded by P. obscurithorax during the two-year period, and seven remained uninvaded (Fig. 7). Additionally, Figure 7 shows the distribution of nest densities in June 2002; populations located in the urbanized core have greater nest densities than those located in the periphery of the city (t = 2.3, df = 19, P < 0.03).


The distribution of P. obscurithorax and its density within its range (Fig. 1) suggest that it was introduced near Mobile, Alabama, or Pensacola, Florida. Both cities have ports that have presumably allowed the introduction of numerous exotics. If no geographic or weather-driven barriers exist directly to the west of Mobile, then the data suggest that Pensacola was the more likely site of arrival because P. obscurithorax has spread more or less equally to the east and west of Pensacola. Lending credibility to this hypothesis is that no significant pattern of east-blowing wind was found, at least during the three years for which data were collected, that would explain an eastward spread. Alternatively, if such barriers do exist, then P. obscurithorax could have been introduced in Mobile, and it has spread mostly eastward. If ant abundance indicates colony size/age in P. obscurithorax, then the negative association between distance from Mobile and P. obscurithorax abundance suggests that the populations near Mobile are older than populations further away. Lack of a similar relationship with distance from Pensacola lends support to Mobile as the likely site of entry. If rates of spread to the east and west were available, a more precise location of entry could be determined.

The gradual change in P. obscurithorax nest densities outward from Mobile and Pensacola and its continuous occurrence throughout its range suggest that P. obscurithorax's range expansion is by queen flight rather than human transport. The apparent gap in distribution west of Tallahassee (Fig. 1) is likely due to sampling error in low-density areas rather than an actual gap in the range. P. obscurithorax has been observed in Jackson County, Florida, (J. R. King, pers. comm.) as well as at a rest area 80 km west of Tallahassee (S. R. Storz, personal observation); both of these localities fall within the apparent gap.

Although P. obscurithorax and S. invicta were introduced at approximately the same time, P. obscurithorax is clearly increasing its range more slowly, and, at least on the eastern front, its expansion still continues. It has not yet spread into peninsular Florida, but we presume, given enough time, it will. P. obscurithorax's low rate of spread compared to that of S. invicta is probably due to differences in reproductive biology such as less frequent mating flights, fewer alates, or lack of high altitude, long distance mating flights. Additionally, P. obscurithorax probably does not choose nest sites in nursery material that is transported by humans, and small nests are probably deep (attempted and successfully excavated nests were up to 3 m deep) and not easily scooped up and moved. Why P. obscurithorax has spread little to the north is unknown. Habitat and/or climate are likely important factors, but roadside habitat characteristics measured in the current study (with the exception of grass height) failed to elucidate any strong patterns of association with the occurrence of P. obscurithorax.

P. obscurithorax was associated with highly disturbed habitat (roadsides with shorter grass) and, so far as we know, is not found in less disturbed habitat. We have not found it in woods adjacent to roadside localities or native longleaf pine forest south of Tallahassee. In Tallahassee P. obscurithorax is clearly thriving. The marked increase of existing populations during the study and the colonization of several new sites lend support to the idea that this species thrives where disturbance is greatest. Its abundance on the Florida State University campus and the frequent affinity of exotic species for disturbed habitats (Elton 1958) reinforce this finding. McGlynn (1999) characterized P. obscurithorax as belonging to the “generalized myrmicine” functional group, members of which are generalists in food and nest-site choice and defend food resources near their nests, but P. obscurithorax's dependence on human activity (habitat disturbance) for successful invasion of and persistence in new habitats suggests it also shares characteristics with “opportunists” and “tramp” species.

To the extent that baits and pitfall traps adequately sample ant communities, P. obscurithorax does not appear to be causing decreases in species abundances, but, rather, it was positively associated with total ant abundance and with the abundance of two species of ants in pitfall traps. Although P. obscurithorax was associated with lower species richness at baits and in pitfall traps, we do not believe that P. obscurithorax is causing a decrease in species richness. The eight ant species collected within the range of P. obscurithorax that were not found to coexist with it were rare species collected at only one or two study sites, and at least six of these are common woodland species (D. Lubertazzi, M.S. Thesis, Florida State University, 1999) probably collected at the edge of their habitat. Highway roadsides are not species-rich habitats and may therefore provide little opportunity for nonnative ants to cause ecological effects. In addition, the large numbers of rare species may make detecting any effects difficult. Only an experimental study will be able to determine the cause of the smaller values of species richness associated with P. obscurithorax.

Interestingly, nearly all of the commonest and most abundant ants captured in pitfall traps are introduced. Either these exotic species have out-competed native species, or, more likely, native ants are not adapted to open, disturbed habitats and are, therefore, not likely to be found in abundance in these habitats. A similar pattern is found for birds where introduced species are commonly found in disturbed, open habitat and native species tend to occur in native habitats (Case 1996). Large expanses of open, disturbed habitat, mostly caused by human activities, may simply be native-species-poor habitats to begin with but are favored by introduced species already adapted to similar habitats. It is likely that P. obscurithorax belongs to a smaller subset of ants that are tolerant of even more highly disturbed habitat within the generally disturbed areas we surveyed. A comparison of urban sites (Tallahassee) with non-urban sites throughout the Southeast shows that the most disturbance-tolerant species (S. invicta, P. obscurithorax, B. musculus, C. rimosus, P. moerens, D. bureni, and C. nuda), all exotics except for D. bureni, rank higher, and cluster, in the more highly disturbed urban sites than the more rural ones. Two of these species do not occur in the rural samples, and those that do move down in rank. Altogether, the case for a community of ants that covaries with degree of habitat disturbance seems strong.


Special thanks to M. Deyrup for assistance with ant species identifications. This study would not have been possible without the support and field assistance of B. L. Storz. For advice and assistance we thank K. L. Haight, A. S. Mikheyev, T. E. Miller, J. N. Seal, and C. R. Smith. Florida State University undergraduates T. Ballinger, N. Dix, M. Fisher, R. Moore, and T. Rhoades helped with specimen sorting and counting. This project was partially funded by the Theodore Roosevelt Memorial Fund through the American Museum of Natural History.



A. N. Andersen 1991. Sampling communities of ground-foraging ants: pitfall catches compared with quadrat counts in an Australian tropical savanna. Australian Journal of Ecology 16:273–279. Google Scholar


E. Batschelet 1965. Statistical Methods for the Analysis of Problems in Animal Orientation and Certain Biological Rhythms. American Institute of Biological Sciences, Washington, DC. Google Scholar


B. T. Bestelmeyer, D. Agosti, L. E. Alonso, C. R. F. Brandão, W. L. Brown Jr, J. H. C. Delabie, and R. Silvestre . 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, pp. 122–144. Smithsonian Institution Press, Washington, DC. Google Scholar


G. J. Bouyoucos 1927. The hydrometer as a new method for the mechanical analysis of soils. Soil Science 23:343–349. Google Scholar


G. J. Bouyoucos 1936. Directions for making mechanical analyses of soils by the hydrometer method. Soil Science 42:225–228. Google Scholar


G. J. Bouyoucos 1962. Hydrometer method improved for the mechanical analyses of soil. Agronomy Journal 54:464. Google Scholar


J. H. Brown and M. V. Lomolino . 1998. Biogeography. Sinauer Associates, Sunderland. Google Scholar


W. F. Buren, G. E. Allen, W. H. Whitcomb, F. E. Lennartz, and R. N. Williams . 1974. Zoogeography of the imported fire ants. Journal of the New York Entomological Society 82:113–124. Google Scholar


T. J. Case 1996. Global patterns in the establishment and distribution of exotic birds. Biological Conservation 78:69–96. Google Scholar


R. K. Colwell 2000. EstimateS: Statistical Estimation of Species Richness and Shared Species from Samples (Software & user's Guide), Version 6. Scholar


M. Deyrup, L. Davis, and S. Cover . 2000. Exotic ants in Florida. Transactions of the American Entomological Society 126:293–326. Google Scholar


C. S. Elton 1958. The Ecology of Invasions by Animals and Plants. Wiley, New York. Google Scholar


N. J. Gotelli and A. E. Arnett . 2000. Biogeographic effects of fire ant invasion. Ecology Letters 3:257–261. Google Scholar


N. J. Gotelli and R. K. Colwell . 2001. Quantifying biodiversity: procedures and pitfalls in the measurement and comparison of species richness. Ecology Letters 4:379–391. Google Scholar


K. L. Heck Jr, G. Van Belle, and D. Simberloff . 1975. Explicit calculation of the rarefaction diversity measurement and the determination of sufficient sample size. Ecology 56:1459–1461. Google Scholar


D. A. Holway 1998. Effect of Argentine ant invasions on ground-dwelling arthropods in northern California woodlands. Oecologia 116:252–258. Google Scholar


D. A. Holway, L. Lach, A. V. Suarez, N. D. Tsutsui, and T. J. Case . 2002. The causes and consequences of ant invasions. Annual Review of Ecology and Systematics 33:181–233. Google Scholar


S. H. Hurlbert 1971. The nonconcept of species diversity: a critique and alternative parameters. Ecology 52:577–586. Google Scholar


F. C. James and S. Rathbun . 1981. Rarefaction, relative abundance, and diversity of avian communities. Auk 98:785–800. Google Scholar


J. E. Lattke 2000. Specimen processing: building and curating an ant collection. In: Agosti D, Majer JD, Alonso LE, Schultz TR, editors. Ants: Standard Methods for Measuring and Monitoring Biodiversity, pp. 155–171. Smithsonian Institution Press, Washington, DC. Google Scholar


D. M. Lodge 1993. Biological invasions: lessons for ecology. Trends in Ecology and Evolution 8:133–137. Google Scholar


T. P. McGlynn 1999. The worldwide transfer of ants: geographical distribution and ecological invasions. Journal of Biogeography 26:535–548. Google Scholar


B. N. McKnight editor. 1993. Biological Pollution: The Control and Impact of Invasive Exotic Species. Indiana Academy Press, Indianapolis. Google Scholar


S. J. Manchester and J. M. Bullock . 2000. The impacts of non-invasive species on UK biodiversity and the effectiveness of control. Journal of Applied Ecology 37:845–864. Google Scholar


M. A. Naves 1985. A monograph of the genus Pheidole in Florida (Hymenoptera: Formicidae). Insecta Mundi 1:53–90. Google Scholar


D. Pimentel, S. McNair, J. Janecka, J. Whitman, C. Simmonds, C. O'Connell, E. Wong, L. Russel, J. Zern, T. Aquino, and T. Tsomondo . 2001. Economic and environmental threats of alien plant, animal, and microbe invasions. Agriculture, Ecosystems and Environment 84:1–20. Google Scholar


S. L. Pimm 1991. The Balance of Nature? Ecological Issues in the Conservation of Species and Communities. University of Chicago Press, Chicago. Google Scholar


S. D. Porter and D. A. Savignano . 1990. Invasion of polygyne fire ants decimates native ants and disrupts arthropod community. Ecology 71:2095–2106. Google Scholar


S. D. Porter, A. Bhatkar, R. Mulder, S. B. Vinson, and D. J. Clair . 1991. Distribution and density of polygyne fire ants (Hymenoptera: Formicidae) in Texas. Journal of Economic Entomology 84:866–874. Google Scholar


D. Simberloff 1986. Introduced insects: A biogeographic and systematic perspective. In: Mooney HA, Drake JA, editors. Ecology of Biological Invasions of North America and Hawaii, pp. 3–26. Springer-Verlag, New York. Google Scholar


D. Simberloff 1997. The biology of invasions. In: Simberloff D, Schmitz DC, Brown TC, editors Strangers in Paradise: Impact and management of nonindigenous Species in Florida, pp. 3–17. Island Press, Washington, DC. Google Scholar


D. Simberloff, D. C. Schmitz, and T. C. Brown . editors. 1997. Strangers in Paradise: Impact and Management of Nonindigenous Species in Florida. Island Press, Washington, DC. Google Scholar


W. R. Tschinkel 1988. Distribution of the fire ants Solenopsis invicta and S. geminata (Hymenoptera: Formicidae) in northern Florida in relation to habitat and disturbance. Annals of the Entomological Society of America 81:76–81. Google Scholar


G. J. Vermeij 1991. When biotas meet: understanding biotic interchange. Science 253:1099–1104. Google Scholar


G. J. Vermeij 1996. An agenda for invasion biology. Biological Conservation 78:3–9. Google Scholar


S. B. Vinson editor. 1986. Economic Impact and Control of Exotic Insects. Praeger, New York. Google Scholar


P. M. Vitousek, L. L. Loope, and C. P. Stone . 1987. Introduced species in Hawaii: biological effects and opportunities for ecological research. Trends in Ecology and Evolution 2:224–227. Google Scholar


D. F. Williams editor. 1994. Exotic Ants: Biology, Impact, and Control of Introduced Species. Westview Press, Boulder. Google Scholar


E. O. Wilson 2002. Pheidole in the New World: A Dominant, Hyperdiverse Ant Genus. Harvard University Press, Cambridge. Google Scholar


Appendix I. Southeast survey site locality information. The first two letters of site ID represent the state. The date is the date of sampling. In range describes which sites were included in the analyses (Y = yes, N = no) as described in methods.


Appendix II. Species presence/absence data at southeast survey sites. An “X” signifies the species presence at each site, and a dash signifies its absence. Names of introduced species are blue.


Appendix II. Species presence/absence data at southeast survey sites. An “X” signifies the species presence at each site, and a dash signifies its absence. Names of introduced species are blue.


Figure 1.

Pheidole obscurithorax nest densities at each site plotted on a map of the southeastern United States. Sites within the oval are those included in analyses. P. obscurithorax occurs within a narrow band along the coast, and its nest densities are highest near Pensacola, Florida.


Figure 2.

Collection frequencies of 19 bait-collected ant species. (a) Percentage of sites (n = 41) at which each species was collected. (b) Percentage of all bait tubes (n = 1733) that captured each species. (c) Percentage of all ants collected (n = 86,681). Each representation of collections shows a typical pattern of one or a few common and many rare species.


Figure 3.

Rarefaction curve for southeast survey. Curves represent the expected number of species at sites with and without Pheidole obscurithorax determined by resampling of each data set 50 times without replacement for each category. “Individuals” are the numbers of baits that collected each species as a surrogate for abundance. Fewer species are expected at sites with P. obscurithorax than at sites without it.


Figure 4.

Frequency of 26 ant species collected in pitfall traps in Tallahassee. (a) Percentage of pitfall traps (n = 80) in which each species was trapped. (b) Percentage of all ants trapped (n = 2,493). Species marked with diamonds are nonnative. Solenopsis invicta and Pheidole obscurithorax were the most common ants trapped, and six of the most common ants are introduced.


Figure 5.

Rarefaction curves for pitfall-trap study. Curves represent the expected number of species per pitfall trap for three categories of Pheidole obscurithorax abundance and were determined by resampling of each data set 50 times without replacement for each category. Pitfall traps that capture the greatest number of P. obscurithorax are expected to capture the smallest number of species.


Figure 6.

Relationship between Pheidole obscurithorax nest densities measured at 21 sites in Tallahassee in two years (Spearman rank correlation, r = 0.5, P < 0.05). Each number in parentheses is the number of sites represented by the point to its left. Dashed line signifies no change in density (isometric population growth); sites on the line did not change in density (n = 7), sites above the line increased in density (n = 13), and site below the line decreased in density (n = 1).


Figure 7.

Pheidole obscurithorax nest densities at 21 sites in Tallahassee, Florida, in June 2002. Seven sites coded with hash marks were new infestations since June 2000. Densities are greatest near the center of town, and new infestations followed no apparent geographic pattern.


Table 1.

Site characteristics at sites with P. obscurithorax present and absent.


Table 2.

Mann-Whitney U tests of the abundances of the six most common ant species at sites with P. obscurithorax present and absent.


Table 3.

Spearman rank order correlations of the abundances of the six most common ant species and P. obscurithorax nest density. P-values are not corrected for multiple comparisons.

Shonna R. Storz and Walter R. Tschinkel "Distribution, spread, and ecological associations of the introduced ant Pheidole obscurithorax in the southeastern United States," Journal of Insect Science 4(12), 1-11, (1 April 2004).
Received: 20 August 2003; Accepted: 1 March 2004; Published: 1 April 2004
nest density
pitfall trap
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