Northeast Natural History Conference 2011: Selected Papers
2012 Northeastern Naturalist 19(Special Issue 6):43–66
The Ants of Nantucket: Unexpectedly High Biodiversity in
an Anthropogenic Landscape
Aaron M. Ellison*
Abstract - This first comprehensive assessment of the ant fauna of Nantucket Island, MA
revealed that 43% of New England ant species and 70% of New England ant genera occur
on an island occupying only 0.07% of New England’s land area. Ants collected by four
different research groups between 2000 and 2009 included 32,158 individual ants (2911
incidences) from 384 spatially and temporally distinct samples representing 14 different
vegetation community types. The majority of the ant species were collected from anthropogenically
derived and maintained sandplain grasslands, sandplain heathlands, and
Scrub Oak shrublands. These three communities are state-ranked S1 community types;
the lower state-ranked communities of beaches and sand dunes, bogs, salt marshes, and
forest fragments had distinct ant assemblages with much lower species richness. The
large number of samples described here, from a wide range of vegetation community
types, expands the known list of Nantucket ant species more than three-fold and provides
a baseline for future assessment of the effects of ongoing, long-term ecosystem management
on Nantucket.
Introduction
Ants are one of the “little things that run the world” (Wilson 1987). They account
for 10–15% of the animal biomass in most terrestrial habitats (Alonso and
Agosti 2000) and they perform a myriad of ecosystem services (Folgarait 1998),
including, at least in New England, turning over more soil than earthworms
(Lyford 1963). The structure of ant assemblages—i.e., the number of ant species
and their relative abundance—is associated with habitat size and type (e.g., Goldstein
1975, Gotelli and Ellison 2002). Ant species richness may be associated
positively with human population density (Schlick-Steiner et al. 2008), but ant
assemblage structure responds rapidly to changes in environmental conditions
and usually reaches a new (quasi-)equilibrium on time-scales ranging from years
to only a few decades (Wike et al. 2010, Zettler et al. 2004).
Grazing and logging are examples of anthropogenic drivers that can bring
about rapid changes in the structure of ant assemblages. For example, on short
time scales (<10 years), ant species richness declined when forests were converted
to agriculture or pasture (Dunn 2004) and in intensively grazed grasslands
relative to nearby forests in Argentina and Mexico (Bestelmeyer and Wiens 1996,
Quiroz-Robledo and Valanzuela-Gonzalez 1995), but in dry climates in both
Australia and North America, ant species diversity was unaffected by moderate
to intensive grazing (Bestelmeyer and Wiens 2001, Read and Andersen 2000). In
*Harvard Forest, Harvard University, 324 North Main Street, Petersham, MA 01366;
aellison@fas.harvard.edu.
44 Northeastern Naturalist Vol. 19, Special Issue 6
the southeastern US, ant species richness declined with increasing pesticide use
and agricultural intensification (Peck et al. 1998).
On decadal time scales, logging per se has less of an impact on ant assemblage
structure than conversion of forests to other uses (Dunn 2004). More ant genera
have been found in clearcuts and mature (20–25 years old) forest stands than in
5- and 15-year-old stands (Wike et al. 2010). Ant species richness also increased
within 2 years following Tsuga canadensis (L.) Carr. (Eastern Hemlock) removal
(Sackett et al. 2011) and remained high throughout 15–20 years of succession
from forest clearings to young hardwood stands (Ellison et al. 2005). However,
little is known about the very long-term effects on ant species richness of grazing
and conversion of forestlands to open habitats, as represented by the over 200
years of intensive land-use on Nantucket Island, off the southeast coast of Massachusetts
(Fig. 1).
Most ecosystems in New England reflect centuries of human land use (Foster
and Aber 2004). The sandplain grasslands, sandplain heathlands, and Scrub Oak
shrublands of Nantucket are the result of centuries of overgrazing and other human
land uses (Dunwiddie 1989, Macy 1880). These vegetation community types
are now uncommon in New England; in Massachusetts, they are all state-ranked
S1 (vegetation) community types (“typically five or fewer occurrences, very few
remaining acres or miles of stream, or especially vulnerable to extirpation in
Massachusetts for other reasons”; Swain and Kearsley 2001). These vegetation
communities also host many species that were common in the mid-1800s at the
height of agricultural activities, but now, following 150 years of reforestation, are
rare (Motzkin and Foster 2002, Sorrie and Dunwiddie 1996). In short, Nantucket
Island is a premier example of a 19th-century landscape (Dunwiddie 1989), and
“the primary management strategy of the Nantucket Conservation Foundation
is to maintain sandplain grassland, sandplain heathland, and Scrub Oak shrublands
in accordance with documented Nantucket vegetation community types”
(Andrew McKenna-Foster, Maria Mitchell Natural History Museum, Nantucket,
MA, 23 December 2009 pers. comm.).
In this paper, I present new data on the ants of Nantucket Island, MA—the first
comprehensive survey of the Island’s ants since the 1920s. I explore relationships
between ant species diversity and vegetation community types, and test whether
different vegetation community types host different ant faunas. This work is part
of a broader effort to document patterns and drivers of the diversity of the ants of
New England (Ellison et al., in press).
Methods
Nantucket Island: its history, vegetation, and historical ant collection
Nantucket is a small island (≈125 km2) off the southeast coast of Massachusetts
(Fig. 1), located between 41°14ʹ and 41°24ʹ N latitude and between 69°57ʹ
and 70°14ʹ W longitude. It has an average annual temperature of 10 °C and receives
an average of 1000 mm of rainfall each year.
2012 A.M. Ellison 45
Like Martha’s Vineyard and Cape Cod to its north, Nantucket is part of the
terminal moraine that was deposited ≈15,000 years ago during the Wisconsin
Glaciation by the Laurentide Ice Sheet (Oldale 2001). As sea level rose, Buzzards
Bay formed to its north ≈5000 years ago, whereupon Nantucket was
isolated from Cape Cod and the rest of the mainland (Oldale 2001). Prior to
European settlement in the mid-1600s, Nantucket was home to Native Americans
of the Wampanoag Tribe (Philbrick 1998). From the early 1700s to nearly
1850, it was the most prominent whaling port in the world (Macy 1880, Melville
1851), but it declined as a commercial port following the 1846 “Great
Fire” that burned Nantucket Town, concurrent siltation of the harbor, and the
development of railroad connections from the mainland whaling port of New
Figure 1. Nantucket Island, illustrating the natural communities of Nantucket and the
locations where and when ants were sampled. Yellow stars indicate approximate locations
of Charles Johnson’s samples from the 1920s (historical information from Avery
2009, Gardner 1947, and Walling 2009); the northernmost site is Maxcy Pond. Circles
identify locations of samples taken between 2000 and 2009. Orange circles indicate the
bogs collected by Aaron Ellison and Elizabeth Farnsworth in 2000; blue circles indicate
sites collected by Mark Mello and Aaron Weed from 2005–2009; green circles
indicate sites collected by Andrew McKenna-Foster in 2006; and red circles indicate
sites collected by Aaron Ellison, Mark Johnston, and Kelly McBride in 2007. Vegetation
classification based on a 1993 inventory by The Nature Conservancy. Precise
information on collection localities, including geographic coordinates and vegetation
community type at each location, is in Ellison and Gotelli (2009).
46 Northeastern Naturalist Vol. 19, Special Issue 6
Bedford to the rest of the United States. The colonial peak of its population
was in 1840, when just over 9000 individuals were recorded in the decennial
census. The population fell to <3000 by 1910, and did not reach 9000 again
until 2000. The 2010 census listed 10,172 permanent residents on the island
(US Census Bureau 2010).
Despite millenia of occupation by Native Americans, Nantucket was heavily
forested before Europeans colonized the island (Dunwiddie 1990, Motzkin and
Foster 2002). The colonists rapidly cleared and farmed the island, their sheep
heavily grazed it, and by the end of the 19th century, there was virtually no forest
cover on the island (Dunwiddie 1989, Macy 1880). Now, the remaining “natural”
vegetation—forests and wetlands—is highly fragmented and occurs only in small
patches restricted to Nantucket State Forest, the forested wetlands at Squam
Swamp, remnant patches at Coskata-Coatue (see Field sampling, below), and a
few kettle-hole bogs.
Currently, the predominant vegetation of Nantucket is a continuous mosaic
of anthropogenically derived and maintained sandplain grasslands, sandplain
heathlands, and Scrub Oak thickets (Dunwiddie 1989, Motzkin and Foster 2002,
Sorrie and Dunwiddie 1996). Sandplain grasslands are dominated by Schizachryium
scoparium (Michx.) Nash (Little Bluestem), Carex pensylvanica Lam.,
and other graminoids; in these grasslands there is <50% cover of Arctostaphylos
uva-ursi (L.) Spreng. (Bearberry), Gaylussacia baccata (Wangenh.) K. Koch
(Black Huckleberry), or other shrubs. Sandplain heathlands are dwarf shrublands
dominated by Bearberry, Huckleberry, Hudsonia tomentosa Nutt. (Woolly
Beachheather), and/or Corema conradii (Torr.) Torr. ex Louden (Broom Crowberry).
Scrub Oak thickets are dominated by Quercus ilicifolia Wangenh. (Scrub
Oak) and Quercus muehlenbergii Engelm. (Chinquapin Oak), with understories
of various Ericaceae, notably Black Huckleberry, Bearberry, or Vaccinium angustifolium
Aiton (Lowbush Blueberry).
Despite intensive collecting of ants in Massachusetts throughout the 20th
century (Ellison et al., in press), only one small ant survey was conducted on
Nantucket prior to those described here. Charles Williston Johnson, of the nowdefunct
Boston Society of Natural History (Johnson 2004), collected insects
throughout the island in the late 1920s. The ants were sent to William Morton
Wheeler at Harvard, who identified them and published a list of the 17 species
that he identified (Wheeler 1928). Johnson (1930) reprinted the list of species,
along with some locality information. Most of his collecting was done at Maxcys
[sic] Pond, with a few additional species collected from the town Common (i.e.,
the public grazing area), the Fairgrounds, and the Coleman Bird Sanctuary. The
specimens were returned to Johnson by Wheeler, and are now in the collection
of the Maria Mitchell Association (Anonymous 1933; Andrew McKenna-Foster,
21 June 2011 pers. comm.). In September 2011, I examined these specimens,
checking species identifications and updating the nomenclature to reflect current
taxonomy (Bolton and Alpert 2011); this re-examination added one species to
Wheeler’s list (Appendix 1).
2012 A.M. Ellison 47
Field sampling
The data presented here are from collections made on Nantucket between
2000 and 2009 by four different research groups (Fig. 1); detailed geographic
information on collection dates and localities are permanently stored in, and
publicly available from, the online Harvard Forest Data Archive, dataset HF-147
(Ellison and Gotelli 2009).
In July of 2000, ants were collected from Taupawshas Bog and Donut Pond
Bog by Aaron Ellison and Elizabeth Farnsworth using an array of 25 pitfall traps
and 25 bait stations, litter sampling, and hand-collecting (the ALL protocol of
Agosti and Alonso 2000); additional details on sampling methods are given in
Ellison et al. (2002). Samples were collected from both bog mats and from the
Scrub Oak thickets that surrounded the bogs.
From 2004–2008, Mark Mello and Aaron Weed set out arrays of barrier
pitfall traps across the island (Weed and Mello 2007). Each barrier pitfall trap
consisted of plastic 473-ml cups containing 20 ml of propylene glycol as a
preservative, four 1- × 0.15-m plastic barrier strips, and five 0.12-m2 plywood
squares for rain covers. Barriers were embedded in the soil at right angles to a
central cup, and four additional cups were set at the end of each barrier. Traps
were left in place for 12–22 days (mean = 14.5 days) from May through October
each year. In 2004, Mello and Weed sampled sandplain grasslands at
Ram Pasture (the former Lot Palmer Farm [Gardner 1947], which became the
Coleman Bird Sanctuary [Albertson 1926] sampled by Johnson in the 1920s);
coastal heathlands at the Smooth Hummocks north of Bartlett Farm Road; annually
burned Scrub Oak thickets; a Pinus rigida Mill. (Pitch Pine) woodland in
Nantucket State Forest; and an Acer rubrum L. (Red Maple) / Nyssa sylvatica
Marsh. (Tupelo) forest at Squam Swamp. From 2005–2008, their sampling was
focused on the sandplain grassland at Ram Pasture, and a Scrub Oak thicket
that had been burned in 2003. Also in 2005, Mello and Weed sampled dense
networks of barrier pitfall traps in the Milestone Harrier Restoration area, a
sandplain heathland mixed with Scrub Oak that has been mown annually since
1996, and in taller Scrub Oak thickets with dense understories of Black Huckleberry
south of the Milestone Harrier Restoration area. Although Mello and
Weed were focused on collecting beetles (Weed and Mello 2007), numerous
ants also accumulated in their pitfall traps; the ants were extracted from the rest
of the pitfall “by-catch” and sent to me for identification.
In 2006, Andrew McKenna-Foster collected spiders in pitfall traps and Berlese
funnels from: the coastal dunes at Eel Point dominated by Myrica pensylvanica
(Mirb.) Kartesz (Bayberry), Toxicodendron radicans (L.) Kuntze (Poison Ivy),
and Vaccinium oxycoccus L. (Small Cranberry); a Scrub Oak/Pitch Pine stand
with a dense understory of Black Huckleberry, Viburnum dentatum L. (Viburnum),
Bayberry, and Lowbush Blueberry at Madequecham; a sandplain grassland
owned by the Massachusetts Audubon Society; a Scrub Oak/Pitch Pine/Black
Huckleberry plot at Sheep Pond; and in the Red Maple/Tupelo swamp forest at
Squam Swamp (McKenna-Foster and Beaton n.d.). Five pitfall traps (240-ml
48 Northeastern Naturalist Vol. 19, Special Issue 6
jars with propylene glycol + ethanol as preservative) were placed at each location
throughout the summer. Traps were 10 m apart and were left open to collect
arthropods on four occasions for three days at all sites except for the sandplain
grassland, where traps were set only twice: once for four days and once for seven
days. At each site, 1 m2 of leaf litter was collected and distributed among eight
15-cm diameter Berlese funnels and placed under four 60-watt light bulbs. Arthropods
were extracted from the litter for four days directly into 70% ethanol.
Ants from both the pitfall traps and the litter samples were extracted from these
samples and sent to me for identification.
In July of 2007, ants were collected at Sesachacha Heathlands and Coskata-
Coatue by Aaron Ellison, Mark Johnston, and Kelly McBride. Habitats sampled
at Sesachacha included sandplain grasslands, sandplain heathlands, and Scrub
Oak thickets. Habitats sampled at Coskata-Coatue included a coastal oak/Pitch
Pine/Ilex opaca Aiton (Holly) forest, a maritime beach/dune covered with Ammophila
breviligulata Fernald (American Beachgrass), a salt marsh berm, and a
maritime Juniperus virginiana L. (Juniper) woodland. Sampling at Sesachacha
and Coskata-Coatue consisted of one person-hour of careful searching and handcollecting
within a 75- × 75-m (5625 m2) plot in each habitat.
Finally, in 2009, Mark Mello set out 11 barrier pitfall traps (as described
above) for beetles in restored sandplain grassland habitats at Norwood Farm,
operated by the Norwood Farm Trust. Ants were extracted from the samples and
sent to me for identification.
Sampling methods and sampling effort differed among the different collectors
and at the different sample sizes, but all used pitfall traps or hand collecting.
Ellison et al. (2007) found that for northeastern US sites, these two methods of
collection yielded the most species and had substantial overlap with each other
and with collections made with baiting or litter collections. We accounted for
differences in sample sizes from different sites using regression analysis (see
Statistical analyses, below).
Species identification, vouchers, and data availability
Ants were identified to species using current keys (Creighton 1950; Ellison
et al., in press; Fisher and Cover 2007); nomenclature follows Bolton and Alpert
(2011). Voucher specimens are deposited at Harvard’s Museum of Comparative
Zoology (MCZ) and at the Maria Mitchell Association on Nantucket. All other
specimens are stored in the Harvard Forest sample archives either in 95% ethanol
or dry-mounted and pinned. Raw data are publicly available from the online
Harvard Forest Data Archive, dataset HF-147 (Ellison and Gotelli 2009).
Statistical analyses
For analysis purposes, an isolated pitfall trap or bait station, a single barrier
trap (which included multiple pitfall cups), a single litter sample (spread across
multiple Berlese funnels), or a temporally bounded (1-hr) hand-collection was
considered a single “sample”. From the 384 samples of pitfall traps, bait stations,
2012 A.M. Ellison 49
litter samples, and hand-collections, I identified 32,158 individual specimens.
Because a single colony represents a genetic “individual” and some colonies
have large numbers of workers that accumulate in pitfall traps, whereas others
have few workers, using counts of individual specimens instead of counts of
colonies can bias estimation of species richness (Gotelli et al. 2011). When nest
locations are unknown (as is the case here), the number of species occurrences, or
“incidences”, in a single sample (e.g., five individuals of a single species from a
single sample equals one incidence) is considered a better measure of abundance
than counts of individual workers (Gotelli et al. 2011). Thus, I use the number
of incidences (2911), not the number of workers, in all analyses. Note, however,
that the rank abundance of individual specimens was highly correlated with the
rank abundance of the number of incidences (Fig. 2), which suggests little differences
among collections in relative abundance of individual species. Additional
assessment of the effects of sampling effort and sample size in each vegetation
Figure 2. The relationship between the rank order of the number of specimens and the
rank order of the number of incidences of all ants collected on Nantucket Island between
2000 and 2009. The dotted line is the 1:1 line, and the solid line is the actual relationship
between incidences and specimens (slope = 0.95, r2 = 0.90, P < 0.001); there is no difference
in the rank-order of incidences and specimens (X2 = 24.8, d.f. = 57, P = 1.0).
50 Northeastern Naturalist Vol. 19, Special Issue 6
community was done by regressing ant species richness in each community on
the (log10-transformed) number of incidences. Provided the data met the assumptions
of linear regression, a linear increase in richness with incidences would
reflect a sampling effect.
All analyses except for species accumulation curves and estimation of the
total number of species on Nantucket were done using the R statistical software,
version 2.12.2 (R Development Core Team 2011). Relevant functions and
libraries used included: cor and lm in the stats library for correlation and linear
regression, respectively; chisq.test in the stats library for chi-square tests; d in
the vegetarian library for computing beta diversity across natural community
types (method of Jost 2007; 100 bootstrap iterations); and metaMDS in the vegan
library for non-metric multidimensional scaling (NMDS; Minchin 1987) and
ordination. For the NMDS, data were first standardized using the Wisconsin
transformation (based on the maximum number of species and the total number
of species per site: Oksanen 1983); the Bray-Curtis dissimilarity metric (Faith
et al. 1987) was used for the ordination. Species accumulation curves (i.e., sample-
based rarefaction curves; Gotelli and Colwell 2001) and 95% confidence
intervals (Colwell et al. 2004) were computed using the EstimateS software,
version 8.2.0 (Colwell 2011). The expected number of species on Nantucket
was estimated (extrapolated) from the data using the Chao-1 estimator (Chao
1987) as programmed in EstimateS.
Results and Discussion
Species richness of Nantucket ants
These seven years of intensive collecting on Nantucket yielded 58 species in
22 genera (Appendix 1, Fig. 3). This effort increases the ant species previously
known from Nantucket more than three-fold (Appendix 1), and only one of the
18 species that were collected in the 1920s, Formica obscuriventris, was not collected
again between 2000 and 2009 (Appendix 1). Despite having only 0.07%
of the land area of New England, Nantucket hosts 43% of the 136 species, 70%
of the 32 genera, and five of the six subfamilies known from, or suspected to
occur in, New England (Ellison et al., in press). Although such a rich ant fauna
might be expected in relatively undisturbed New England habitats (Ellison et al.,
in press), hundreds of years of intensive land use have transformed Nantucket’s
original ecosystems, and these anthropogenically derived habitats are maintained
by active management (Dunwiddie 1989).
Elsewhere in the world, deforested and heavily grazed ecosystems generally
support fewer ant species than forested and ungrazed habitats (e.g.,
Bestelmeyer and Wiens 1996, Dunn 2004, Wike et al. 2010). However,
Schlick-Stenier et al. (2008) have shown that ant species richness increases
with human population density in some anthropogenic landscapes, but their
relationship between population density, island area, and ant species richness
predicts <12 ant species for Nantucket. Even using Schlick-Steiner et al.’s
2012 A.M. Ellison 51
(2008) equations that include plant diversity, which is particularly high on
the island (>1200 plant species; Sorrie and Dunwiddie 2006), the expected
number of ant species increases to only 14 species, and only a few more species
would be expected to be added for the island’s 10 °C annual temperature
(Sanders et al. 2007, Schlick-Steiner et al. 2008). A more detailed analysis of
ant assemblages in each habitat suggests some reasons for the unexpectedly
high diversity of ants observed on Nantucket.
Structure of Nantucket ant assemblages
As is characteristic of most samples of species abundance, the overall ant
species-abundance curve was pronouncedly log-normal (Fig. 4). There were a
handful of common species—Tapinoma sessile, Formica incerta, Lasius alienus,
Nylanderia parvula, Aphaenogaster rudis, A. treatae, Crematogaster lineolata,
and a widespread, but as yet undescribed, species of Myrmica (species code AFscu;
Ellison et al., in press)—and a very long tail of rare species. Of particular
interest among the rare species, for which only one or two individuals were
collected, were Myrmica semiparasitica and Anergates atratulus. Myrmica semiparasitica
is a social parasite of the woodland species M. punctiventris; it was
described only in 2009 (Francoeur 2009), and the two Nantucket records are only
Figure 3. Species accumulation curve for ants collected on Nantucket Island between
2000 and 2009. The solid line is the observed data, and the grey dotted lines are 95%
confidence intervals based on 1000 bootstrap samples. The Chao-1 estimate (and
95% confidence intervals) of the estimated total number of ant species on Nantucket
is indicated by the solid square (and vertical line).
52 Northeastern Naturalist Vol. 19, Special Issue 6
the fourth and fifth time this species has been collected anywhere in the world
(Ellison et al., in press). Anergates atratulus is a non-native social parasite of its
non-native host, the pavement ant Tetramorium caespitum (Bruder and Gupta
1972); the Nantucket record is only the second time that this species has been
collected in New England (Ellison et al., in press). These two rare species were
collected in rare vegetation community types: sandplain grasslands, Scrub Oak
shrublands, and Pitch Pine heathlands.
Certain species were associated with particular natural community types
(Appendix 1, Fig. 5). Myrmica lobifrons is a bog specialist, and, along with
the wetland species Myrmica incompleta, was associated strongly with the two
Figure 4. Rank-abundance plot of the 58 ant species collected on Nantucket Island between
2000 and 2009. The abundance shown is the log10 of the number of incidences in
the total sample for each species. Like virtually all species-abundance curves that have
been published, this plot illustrates that there are a few common species and many rare
species in the Nantucket ant assemblage.
2012 A.M. Ellison 53
sampled kettle bogs. Dolichoderus plagiatus and Lasius neoniger were most
abundant along the landward edges of salt marshes. The pavement ant, Tetramorium
caespitum, has expanded its range into maritime juniper woodlands and
sand dunes, where it nests at the base of American Beachgrass, displacing L. neoniger.
Ants in the wide-ranging Aphaenogaster rudis species complex were the
only ants found in the one collection made in a residential area, but this habitat is
the most under-sampled of any on the island; further collections in town centers
and residential areas undoubtedly would yield more species such as Tetramorium
caespitum and carpenter ants (Camponotus spp.).
The remaining ant assemblages separated out the woodland communities
(deciduous forest, Red Maple/Tupelo swamp, Pitch Pine barrens, White Pine
stands, and Scrub Oak shrublands) from the more open heathland and grassland
communities (sandplain grasslands, sandplain heathlands, and Scrub Oak
heathlands) (Figs. 5 and 6). The most common ants in the shrubby woodlands
included Crematogaster lineolata, Formica rubicunda, Myrmica punctiventris,
Figure 5. Ordination plot of the non-metric multidimensional scaling of the ant assemblages
of the different vegetation communities sampled on Nantucket Island between
2000 and 2009. The community types are written in grey, and the ant species most commonly
associated with each community are written in black.
54 Northeastern Naturalist Vol. 19, Special Issue 6
and Tapinoma sessile, whereas the more common ants in the open heathlands and
grasslands included Aphaenogaster treatae, Formica pallidefulva, F. pergandei,
and Lasius umbratus. True forest specialists, including carpenter ants (Camponotus
americanus and C. novaeboracensis) and Lasius nearcticus, were uncommon
anywhere on the island (Fig. 4).
Similarity analysis (Fig. 6) provided additional statistical support for inferences
drawn from the ordination plot (Fig. 5); 3–4 distinct assemblages (sensu
Jost 2007) were identified in these data. The bog and residential areas were
species-poor, clearly different from each other, and clearly different from all
of the other sampled communities (Fig. 6). The ant assemblages of the woodland
and open communities formed a continuum from maritime to uplands, and
from woodland to open (Fig. 6). The maritime communities (salt marsh edges,
beaches and dunes, juniper woodlands) had far fewer species than the grasslands,
heathlands, Scrub Oak woodlands, and forests, but the species in the maritime
communities were simple subsets of the species in the upland communities. The
vegetation communities with the most ant species also were those of highest
conservation concern (Fig. 6).
Figure 6. Similarity (beta diversity) in ant assemblages of the different natural communities
sampled on Nantucket Island between 2000 and 2009. Shading (from white to black)
indicates increasing similarity (from 0–100%). The numbers on the diagonal are the total
number of ant species collected in each natural community. The font of the community
indicates the state ranking of that habitat (community type): S1 in bold-italic, S2 or S3
in bold, and S5 in grey.
2012 A.M. Ellison 55
It was not possible to determine how contemporary land management, the
goal of which is to maintain vegetation community types and landscapes created
by land use occurring from the 17th to the 19th centuries, has altered the structure
of ant assemblages. Johnson’s 1927 ant collection (Wheeler 1928, Johnson 1930)
was too small and restricted in habitats to compare with the data presented here,
but it is noteworthy that 17 of the 18 species he collected in 1927 were collected
again in the last decade, and most of the species that he collected are also species
of open habitats (Appendix 1). This result suggests that the ant assemblages on
Nantucket likely have stabilized and that the species identified above could serve
as useful indicators of successful management of the anthropogenically derived
sandplain grasslands, sandplain heathlands, and Scrub Oak shrublands. In contrast,
the ant assemblages of “natural” communities—bogs, other wetlands, and
forests likely are relicts of more widespread assemblages, and these assemblages
may lose more species over time (Schoereder et al. 2004). Future standardized
collections focused on all of Nantucket’s vegetation community types would allow
for a more rigorous test of this hypothesis.
Were the samples biased by collection effort?
Although there was a strong and significant positive relationship between
the number of incidences and the number of species across the 14 sampled
vegetation community types (i.e., a sampling effect: r2 = 0.89, P = 9.2 × 10-7;
Fig. 7), further examination of the residuals (deviations of observed data from
the regression line) revealed that they were not normally distributed. This result
suggested that the relationship between the number of incidences and species
richness in the natural communities was not random. In particular, Figure 7
shows that several of the most species-rich communities of conservation concern
(Scrub Oak shrublands, sandplain heathlands, and Scrub Oak/sandplain
grasslands) had more ant species than expected for the number of incidences,
whereas the most species-poor communities (the bogs and maritime beach/
dunes) had fewer ant species than expected for the number of incidences. The
Pitch Pine/heathland barren also had many more species than expected for the
number of incidences in the overall sample.
This overall result appears to be driven by the species-rich communities that
are “pulling” the regression line towards the left of Figure 7. The bogs were
sampled intensively using many methods (Ellison and Gotelli 2009, Ellison et
al. 2002), and the number of ant species collected from Nantucket bogs and on
its beaches and dunes was not unusual (Ellison et al., in press). The sampling intensity
of pitfall trapping in the sandplain grasslands, sandplain heathlands, and
Scrub Oak shrublands was indeed high, but not disproportionately high relative
to the other habitats when scaled to the number of samples (Ellison and Gotelli
2009, Weed and Mello 2007). Nevertheless, these habitats still had many more
species than would have been expected.
56 Northeastern Naturalist Vol. 19, Special Issue 6
How does the Nantucket ant fauna compare with the ants of mainland New
England?
Compared with other counties in New England, Nantucket has a relatively
small area (Fig. 8A). Note that Nantucket County includes not only Nantucket
Island (≈125 km2) but also the islands of Tuckernuck (≈3.6 km2) and Muskeget
(≈3.1 km2), neither of which have been systematically surveyed for ants. Both
for counties of its size, and for all counties in New England, the observed ant
species richness of Nantucket is in the upper 20%; more ant species have been
recorded in only ten other counties (out of 67 total) in all of New England (Fig.
8A). The high species richness of Nantucket Island could reflect the intensive
sampling of ants on the island (Fig. 8B); the intensive sampling described
here provides more specimen records from Nantucket Island than from any
other county in New England, except for York County, ME (Ellison et al., in
press). However, many other counties, including half of those on mainland
Figure 7. Relationship between species richness and the log10(number of incidences) in
the overall sample. The dotted line is the best-fit linear regression of the observations.
As the residential site was an outlier—it was represented in the dataset by only a single
incidence, which by definition can only have 1 species—it was excluded from the regression
analysis.
2012 A.M. Ellison 57
Figure 8. Relationship between species richness and county area (A) and sampling intensity
(B) throughout New England. Individual county areas from US Census Bureau
data; sampling intensity data from Ellison et al. (2012). Different colors indicate different
states (dark blue = Maine; blue = New Hampshire; light blue = Vermont; light red = Massachusetts;
red = Rhode Island; dark red = Connecticut); the black square is Nantucket
(data from this paper).
58 Northeastern Naturalist Vol. 19, Special Issue 6
Massachusetts, have more recorded species despite having fewer specimen
records (Ellison et al., in press; Fig. 8B). I conclude, therefore, that the high
species richness observed on Nantucket Island more likely reflects the diversity
of habitats on Nantucket than it does a sampling effect.
Could there be still more ant species on Nantucket?
Not only was the observed species richness much higher than would be expected
on a small island with a relatively high population density (80 people/
km2), historically extensive land use, and ongoing active ecosystem management,
the estimated species richness (Chao-1 estimator) for Nantucket was 62
species (95% confidence interval = [59–80]; Fig. 3). This result suggests that
there are still a few more species to be found on the island. Where would it be
best to look?
Six subfamilies of ants are represented in New England; five were collected
on Nantucket (Appendix 1). The missing subfamily, the Proceratiinae, includes
three species in the single genus Proceratium, all of which nest in rotten logs in
forests and woodlands. These species, along with the three New England species
in the genus Pyramica (Myrmicinae), might yet be found in the woodland
fragments on Nantucket. However, the small size and fragmented distribution of
forests on the island makes it unlikely that their populations would persist over
the long term (Schoereder et al. 2004).
Other missing genera include the New England native genera Formicoxenus,
Harpagoxenus, and Pheidole (all Myrmicinae) and Polyergus (Formicinae), and
the non-native genus Pachycondyla (Ponerinae). All of the native genera except
Harpgoxenus are warm-climate species that could occur on Nantucket given
suitable habitat. Formicoxenus provancheri (Emery) is a social parasite of bogdwelling
Myrmica species, and could be found in the kettle bogs with its host.
Polyergus lucidus Mayr is a slave-making species of Formica incerta. As this
host is one of the most common species in the sandplain grasslands, there is no
reason that P. lucidus couldn’t survive there as well, but it is generally uncommon
(Marlin 1971) and rare throughout New England (Ellison et al., in press).
Pheidole pilifera (Roger) is a seed-harvesting species that is common in open areas,
but it is rare in the pure-sandy soils of pine barrens and sandplain grasslands,
and would be unexpected on Nantucket.
New England overall has only 13 non-native ant species, and most are (sub)
tropical “tramp” species that nest only in heated structures (Ellison et al., in
press). Only five can handle New England’s winter climate, and two of those,
Tetramorium caespitum and its specialist parasite Anergates atratulus, already
are on Nantucket. Two more, Nylanderia flavipes (Smith) and Pachycondyla
chinensis Emery are rare in New England (Ellison et al., in press) but are increasing
in abundance in the urbanized Mid-Atlantic states (Pećarević et al.
2010). The last, Myrmica rubra (L.), is widespread in coastal New England
and maritime Canada from eastern Rhode Island north to Nova Scotia (Groden
et al. 2005; Ellison et al., in press) in salt marshes, coastal woodlands, urban
2012 A.M. Ellison 59
areas, and along river margins. There is certainly suitable habitat for M. rubra
on Nantucket, and it seems unlikely that it is too warm on Nantucket for M. rubra
to persist. Perhaps the long period of sustained land use and management
has allowed the ant communities to stabilize to an extent that it is difficult for
M. rubra to establish.
Conclusion
There are distinctive, unusually species-rich assemblages of ants in the sandplain
grasslands, sandplain heathlands, and Scrub Oak shrublands that were
created by colonial-era land use and that are maintained by active management.
Likewise, there are distinctive, species-poor assemblages of ants in bogs, forest
remnants, and on sandy beaches and dunes. The large number of samples described
here, from a wide range of vegetation community types, provide a useful
baseline for future studies of Nantucket’s biodiversity and suggest that some
species of ants may be valuable indicators for evaluating ecosystem management
and restoration on the island.
Acknowledgments
The ants were collected and/or sorted by Chelsea Carr, Aaron Ellison, Elizabeth
Farnsworth, Mark Johnston, Kelly McBride, Andrew McKenna-Foster, Mark Mello,
Scott Smyers, and Aaron Weed. Aaron Ellison, Mark Johnston, and Kelly McBride
identified the ants, and Stefan Cover confirmed identification of the more troublesome
species. Andrew McKenna-Foster uncovered Charles Williston Johnston’s 1927
samples and loaned them to me for this study. Permits to access and sample sites, and
logistical support in the field, were provided by The Trustees of Reservations, the
Massachusetts Audubon Society, and the Maria Mitchell Association. Karen Beattie
(Nantucket Conservation Foundation) provided the Nantucket vegetation map and
GIS data layer, and Brian Hall (Harvard Forest) produced Figure 1. A version of this
paper was presented at the 11th Northeast Natural History Conference in 2011; I thank
the participants in the Ant Ecology session, as well as Elizabeth Farnsworth, Nick
Gotelli, Israel Del Toro, Michael Weiser, and two anonymous reviewers for helpful
comments that substantially improved the manuscript. Financial support was provided
by the Arthur Green Fund of Harvard’s Museum of Comparative Zoology, the Conservation
Research Foundation, the Harvard Forest, the Massachusetts Natural Heritage
and Endangered Species Program, the Nantucket Conservation Foundation, the US
Department of Energy (grant DE-FG02-08ER64510), and the US National Science
Foundation (grants DBI 04-52254, DEB 05-41680, and 08-02655).
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64 Northeastern Naturalist Vol. 19, Special Issue 6
Appendix 1. Ant species of Nantucket, their occurrence in the different vegetation community types sampled, the state rank of each vegetation community
type (following Swain and Kearsley 2001), and the total species richness of each vegetation community type. A single asterisk (*) indicates a species in
the 2000–2009 sample that was also collected by C.W. Johnson in the early 1900s (Wheeler 1928). A double asterisk (**) indicates a species that was collected
by Johnson (Wheeler 1928) but not collected in 2000–2009. Nomenclature follows Bolton and Alpert (2011); subfamilies are in bold-faced type. The
species codes for the one undescribed species of Leptothorax and the two undescribed species of Myrmica parallel those used by André Francoeur for his
forthcoming revision of these two genera (see also Ellison et al., in press). Community types: R= residential, SM = salt marsh, B/D = beach/dune, B = bog,
SG = sandplain grassland, SH = sandplain heathland, SO/SG = Scrub Oak/sandplain grassland, SO/SH = Scrub Oak/sandplain heathland, SOS = Scrub Oak
shrubland, MJW = maritime juniper woodland, PP/HB = Pitch Pine/heath barren, PPF = Pitch Pine Forest, MDF = mixed deciduous forest, RM/TS = Red
Maple/Tupelo swamp.
Community type
R SM B/D B SG SH SO/SG SO/SH SOS MJW PP/HB PPF MDF RM/TS
State Rank – S3 S3 S2 S1 S1 S1 S1 S1 S1 S5 S5 S5 S3
Species richness 1 4 13 7 44 35 25 13 42 9 15 17 12 15
Amblyoponinae
Amblyopone pallipes (Haldeman) √ √ √ √ √
Ponerinae
*Ponera pennsylvanica Buckley √ √ √ √ √ √ √ √
Dolichoderinae
*Dolichoderus plagiatus (Mayr) √ √ √
D. pustulatus Mayr √ √
*Tapinoma sessile (Say) √ √ √ √ √ √ √ √ √ √
Formicinae
Brachymyrmex depilis Emery √ √
Camponotus americanus Mayr √ √ √ √
*C. novaeboracensis (Fitch) √
*Formica difficilis Emery √
*F. dolosa Buren √ √ √
*F. exsectoides Forel √ √ √
*F. incerta Buren √ √ √ √ √ √ √ √ √
F. integra Nylander √
F. lasioides Emery √
2012 A.M. Ellison 65
Community type
R SM B/D B SG SH SO/SG SO/SH SOS MJW PP/HB PPF MDF RM/TS
F. neogagates Viereck √ √ √ √ √ √ √ √
**F. obscuriventris Mayr
*F. pallidefulva Latreille √ √ √ √ √
F. pergandei Emery √ √
F. rubicunda Emery √ √
F. subaenescens Emery √ √
F. subintegra Wheeler √ √ √ √ √
*F. subsericea Say √ √ √ √ √ √ √ √ √ √ √ √
*Lasius alienus (Foerster) √ √ √ √ √ √ √ √ √ √ √
L. claviger (Roger) √ √ √ √ √
*L. flavus (Fabricius) √ √ √ √
L. interjectus Mayr √ √ √ √
L. latipes (Walsh) √ √
L. nearcticus Wheeler √ √
L. neoniger Emery √ √ √ √ √
L. subglaber Emery √ √ √ √ √ √ √
L. umbratus (Nylander) √
Nylanderia parvula (Mayr) √ √ √ √ √ √ √ √ √
Prenolepis imparis (Say) √ √ √ √ √
Myrmicinae
Anergates atratulus (Schenck) √
Aphaenogaster fulva Roger √
A. rudis Enzmann (species complex) √ √ √ √ √ √ √ √ √ √ √
Aphaenogaster treatae Forel √ √ √ √
*Crematogaster lineolata (Say) √ √ √ √ √ √ √ √ √ √ √ √
Leptothorax sp. nov. (L. sp. AF-can) √
*Monomorium emarginatum DuBois √ √
Myrmecina americana Emery √ √ √ √ √
*Myrmica americana Weber √ √ √ √ √
M. fracticornis Forel √
*M. incompleta Provancher √ √
66 Northeastern Naturalist Vol. 19, Special Issue 6
Community type
R SM B/D B SG SH SO/SG SO/SH SOS MJW PP/HB PPF MDF RM/TS
M. lobifrons Pergande √
M. pinetorum Wheeler √ √
M. punctiventris Roger √ √ √ √ √ √ √ √
M. semiparasitica Francoeur √ √
*Myrmica sp. nov. (M. sp. AF-scu) √ √ √ √ √ √ √ √ √ √
Myrmica sp. nov. (M. sp. AF-smi) √ √ √ √ √
Protomognathus americanus (Emery) √ √
Solenopsis molesta (Say) √ √ √
Solenopsis sp. nov. (S. cf. texana Emery) √ √ √
Stenamma brevicorne (Mayr) √ √ √ √ √
S. impar Forel √ √ √ √ √
S. schmitti Wheeler √ √
Temnothorax ambiguus (Emery) √ √ √
T. curvispinosus (Mayr) √ √ √ √ √
Tetramorium caespitum (L.) √ √ √ √ √ √ √