Site by Bennett Web & Design Co.
2009 SOUTHEASTERN NATURALIST 8(3):515–526
Infl uence of Microstegium vimineum Presence on Insect
Abundance in Hardwood Forests
Jordan M. Marshall1,2,* and David S. Buckley3
Abstract - Microstegium vimineum (Japanese Stiltgrass) is an exotic, annual grass
that has invaded hardwood forests throughout the Southeastern United States. Four
forests, in four Tennessee counties, were selected, and insects and plant communities
were sampled along transects with and without M. vimineum. Insects were sampled
using a terrestrial vacuum sampler. Percent plant cover was measured using a pointintercept
technique, and plant species richness and diversity were calculated. Of
the 60 families collected, significantly more individuals in the families Acrididae,
Cicadellidae, and Gryllidae, were collected in areas with M. vimineum, whereas
areas without M. vimineum resulted in significantly more individuals in the families
Blattellidae and Chrysomelidae. Herbaceous plant richness and diversity did not
significantly differ between areas with and without M. vimineum. Areas without M.
vimineum had significantly lower percent vegetation cover (30.41%) than areas with
M. vimineum (91.48%). The overall herbaceous plant community diversity and structure
may be more infl uential factors in the abundances of insect families in central
hardwood forests than the invasion of M. vimineum.
The addition of exotic plant species to landscapes can change the composition
of local plant communities, beyond a simple additive impact (e.g.,
Maskell et al. 2006, Meiners et al. 2002). In some cases, alterations to the
surrounding landscape as a result of an exotic plant species introduction
and eventual dominance can substantially alter the composition of native
plant communities (Mack et al. 2000, Siemann and Rogers 2006). However,
changes to plant communities as a result of exotic species introduction are
often more subtle, and do not necessarily result in restructuring of native
communities (Mandryk and Wein 2006). The addition of an exotic plant
species to the overall community is often associated with some other anthropogenic
factor, which, in turn, may be the overarching cause of alterations in
plant or insect communities (Maskell et al. 2006, Palmer et al. 2004).
One exotic species of concern within eastern hardwood forests is Microstegium
vimineum (Trin.) A. Camus (Japanese Stiltgrass; Poaceae).
This C4 annual grass species is native to Southeastern Asia and was first
collected in North America near Knoxville, TN, in 1919 (Fairbrothers and
1Department of Forestry, Wildlife, and Fisheries, 274 Ellington Plant Sciences Building,
University of Tennessee, Knoxville, TN 37996. 2Current address - Michigan
Technological University, Cooperative Emerald Ash Borer Project, 5936 Ford Court,
Suite 200, Brighton, MI 48116. 3University of Tennessee Agricultural Experiment
Station, Department of Forestry, Wildlife, and Fisheries, 274 Ellington Plant Sciences
Building, Knoxville, TN 37996. *Corresponding author - email@example.com.
516 Southeastern Naturalist Vol. 8, No. 3
Gray 1972). It is found throughout the Eastern United States from Florida
to Massachusetts and as far west as Texas (Fairbrothers and Gray 1972,
Hunt and Zaremba 1992, Redman 1995, USDA NRCS 2007). M. vimineum
has become a common target in the control of exotic species throughout its
introduced range on both private and public lands (Johnson 1997, Steele et
Although anecdotal information on this species has been sufficient to
generate considerable concern, relatively few formal scientific studies have
been implemented to establish the ecological impacts of M. vimineum on different
groups of native taxa. However, based on the impact studies that have
been conducted, it has been found that: 1) hardwood tree seedlings might
not be recruited into larger size classes due to suppression by M. vimineum
(however, Quercus spp. (oak) and Acer spp. (maple) seedlings, two genera
which are considered important in central hardwood forests, did not differ
between plots with and without M. vimineum [Cole 2006]); 2) increases in
M. vimineum biomass may reduce height growth of out-planted tree seedlings
as well as reduce woody stem densities of tree seedlings (Oswalt et al.
2004, 2007); and 3) M. vimineum was superior to a native grass in resource
acquisition, leading to reduced biomass accumulation in the native species
(Leicht et al. 2005).
To our knowledge, no studies have been implemented to investigate
impacts of M. vimineum on native bird or mammal species. In terms of impacts
of M. vimineum on arthropods, survival of nymphal and larval Ixodes
scapularis Say (Acari: Ixodidae) were not impacted by M. vimineum (Carroll
2003). Due to the importance of arthropods in trophic webs and as indicators
of ecosystem function, condition, and integrity, investigation of potential
impacts of M. vimineum on native insect communities is warranted.
The objectives of this study were to 1) test the null hypothesis that insect
communities do not differ between plant communities with and without M.
vimineum, and 2) investigate relationships between insect family abundances
and plant species richness and diversity in this forest type.
Insect collection forest sites were located in Anderson, Blount, Knox,
and Morgan counties, TN (Fig. 1). Study sites were within the Appalachian
section of central hardwood forest characterized as being an Oak-Hickory
forest type (Fralish 2003). For all four sites, mean annual temperature was
15 °C and mean annual total precipitation was 1400 mm (National Climatic
Data Center 2007).
Patches dominated by M. vimineum of sufficient size for multiple samples
were selected at each study site and had defined edges, beyond which
M. vimineum had not invaded. Patch area was not measured. M. vimineum
dominance was estimated within each patch to be at least 75 percent cover
through an ocular measurement. Patches were located at the University of
Tennessee Oak Ridge Forest (Anderson County, TN; 36°0'4"N, 84°13'34"W),
2009 J.M. Marshall and D.S. Buckley 517
Springbrook Park (Blount County, TN; 35°48'4"N, 83°58'52"W), the
Ijams Nature Center Quarry Restoration (Knox County, TN; 35°57'2"N,
85°52'54"W), and the University of Tennessee Cumberland Forest (Morgan
County, TN; 36°3'43"N, 84°26'53"W). The Anderson County site was actively
managed using silvicultural techniques, with recent harvesting activities occurring
in 2005 (R.M. Evans, The University of Tennessee, Oak Ridge, TN,
pers. comm.). A municipality managed the Blount County site with minimal
activity within the forested sampling locations and there appeared to be little
recent disturbance in this location (J.M. Marshall, pers. observ.). A restoration
program was initiated in 2001 at the Knox County site by the Ijams Nature
Center, which included trail construction and maintenance (James 2003).
Grading of a road at the Morgan County site occurred in 1998, but the site has
remained undisturbed since that time (M.R. Schubert, The University of Tennessee,
Oliver Springs, TN, pers. comm.).
A portable terrestrial vacuum sampler, as described by Harper and Guynn
(1998), was used to collect insects. Vacuum samples were collected within a
Figure 1. Insect and plant sampling locations in Anderson, Blount, Knox, and Morgan
518 Southeastern Naturalist Vol. 8, No. 3
bottomless frame box (50 x 50 x 50 cm). Ten sampling locations, with 5-m
intervals, were selected along a transect established on the long axis of each
patch of M. vimineum. At the Anderson County and Morgan County sites,
large patches of M. vimineum existed that accommodated all ten sampling
locations within a single, contiguous patch. Patches of M. vimineum at the
Blount County and Knox County sites were smaller, but were large enough
for 3–5 samples per patch. Patches in close proximity (20–40 m apart) at
these sites were sampled to approximate the area covered by the large patches
at sites in Anderson and Morgan counties. Native forest understory areas
without M. vimineum were selected along transects within the same forest
stand as controls. Ten sampling locations were selected along the control
transects at each site, with 5-m spacing.
Three insect collections were made 6 June, 20 July, and 7 September
2006, between 10:00 am and 3:00 pm, allowing for six-week periods between
collections. These non-sampling periods were long enough to ensure
recolonization of plots by insects, and thus a reasonable level of independence
existed between samples obtained on different dates (Tscharntke et
al. 2005). Insects were identified to family using Daly et al. (1998) and
Triplehorn and Johnson (2005). Taxonomic arrangement was based on the
Integrated Taxonomic Information System (2007), with the inclusion of the
order Collembola. Family richness and Shannon diversity index were calculated
for each collection period for each site (n = 24). Richness (S) was
the count of families that were encountered. Shannon diversity indices were
calculated as H = -Σ pi ln (pi), where pi = the proportion of the ith family
(Hayek and Buzas 1997).
A plant survey, centered on the insect-collection points, was conducted
at each sampling location in areas with and without M. vimineum on 7 and
9 June 2006. Plants were identified to species, except for individuals in the
genera Carex, Rubus, Solidago, Vaccinium, and Viola. Percent cover for each
species was measured using a point-intercept technique within a 0.34-m2
frame containing 49 points spaced 7 cm apart. Percent plant cover was calculated
as the proportion of points intercepted x 100 (Floyd and Anderson
1987). Richness (count of species encountered [S]) and Shannon diversity
indices for herbaceous plant species were calculated for each site in areas
with and without M. vimineum, which was excluded from the diversity index
calculations (n = 8). Percent canopy cover was measured 1 m above the
center of each sampling location with a CI-110 Digital Canopy Imager (CID
Inc., Camas, WA) on 7 and 9 June 2006 (n = 80). Air temperature and relative
humidity were measured at the time of insect sampling at five sampling
locations in each of the two treatment areas, with and without M. vimineum,
using a Kestrel 3000 Pocket Weather Meter (Nielsen-Kellerman, Boothwyn,
PA) (n = 120).
Sampling locations and dates were considered independent samples for
statistical analysis. One-tailed t-tests were performed to identify directional
2009 J.M. Marshall and D.S. Buckley 519
differences in treatments with and without M. vimineum for canopy cover, air
temperature, and relative humidity, as well as plant species richness and diversity
and insect family richness and diversity. Families that accounted for at
least 3 percent of the total abundance in each treatment area, with and without
M. vimineum, were used to test for differences of individual family abundances
between those treatment areas. Simple linear regression was used to test for
relationships between insect family diversity and plant species diversity. All
statistical analyses were performed using NCSS (v. 2004).
The ocular estimate of 75% M. vimineum cover was similar to the actual
mean cover (± SD) of 79.49% ± 8.82 for this species. Percent forest canopy
cover was significantly greater in areas without M. vimineum than in areas
with M. vimineum (mean ± SD: 79.43% ± 4.56 vs. 75.81% ± 5.54, respectively;
t = 3.19, df = 78, P = 0.002). Air temperature did not differ between areas
with and without M. vimineum (mean ± SD: 27.26 °C ± 3.48 vs. 27.32 °C ±
3.10, respectively; t = 0.11, df = 118, P = 0.913). Also, relative humidity did
not differ between areas with and without M. vimineum (mean ± SD: 49.02%
± 9.34 vs. 49.82% ± 10.17, respectively; t = 0.45, df = 118, P = 0.654).
A total of 2839 insects were captured over the three sampling dates representing
11 orders and 60 families. Total insect family richness (mean ± SD:
15.19 ± 3.55 vs. 15.08 ± 4.25, respectively; t = -0.52, df = 22, P = 0.304)
and diversity (mean ± SD: 1.80 ± 0.44 vs. 1.74 ± 0.40, respectively; t =
-0.32, df = 22, P = 0.752) did not differ significantly between areas with and
without M. vimineum (Table 1). Also, insect abundance did not differ signifi-
cantly between areas with and without M. vimineum (mean ± SD: 138.42 ±
86.94 vs. 98.08 ± 59.90, respectively; t = -1.323, df = 22, P = 0.199). Nine
families each accounted for more than 3 percent of the total insects collected
(Table 1). Formicidae and Entomobryidae were the dominant two families
in both areas with and without M. vimineum, with Formicidae accounting
Table 1. Mean (SD) insect family abundance count, family richness, and family diversity in
areas with (n = 12) and without Microstegium vimineum (n = 12) in central hardwood forests.
120 samples were collected in each treatment.
Mean abundance (count)
Insect Family (Order) With M. vimineum Without M. vimineum
Acrididae (Orthoptera) 7.08 (8.18) 1.42 (1.68)
Blattellidae (Dictyoptera) 0.75 (0.97) 3.83 (3.21)
Chrysomelidae (Coleoptera) 0.83 (0.72) 3.25 (3.33)
Cicadellidae (Hemiptera) 6.42 (5.53) 1.17 (1.53)
Curculionidae (Coleoptera) 1.33 (1.83) 4.25 (6.48)
Entomobryidae (Collembola) 49.42 (76.01) 23.83 (18.86)
Formicidae (Hymenoptera) 39.67 (39.37) 44.08 (46.09)
Gryllidae (Orthoptera) 8.42 (6.29) 1.92 (1.83)
Lygaeidae (Hemiptera) 5.92 (4.93) 3.17 (3.49)
Family richness 15.19 (3.55) 15.08 (4.25)
Family diversity 1.80 (0.44) 1.74 (0.40)
520 Southeastern Naturalist Vol. 8, No. 3
for 35.40% and Entomobryidae accounting for 30.96% of all insects collected.
Of the nine families included in the analyses, only Blattellidae and
Chrysomelidae exhibited reductions in abundance in plots with M. vimineum
(Fig. 2). Families Acrididae, Cicadellidae, and Gryllidae were significantly
more abundant in areas with M. vimineum (Fig. 2). Formicidae, Entomobryidae,
Lygaeidae, and Curculionidae did not differ significantly between areas
with and without M. vimineum.
Forty-four herbaceous plant species were present in this study. Fifteen
herbaceous plant species occurred only in areas with M. vimineum, whereas
sixteen occurred only in areas without M. vimineum. Plant species richness
(mean ± SD: 11.75 ± 4.27 vs. 15.50 ± 6.45, respectively; t = 0.97, df = 6, P =
0.185) and diversity (mean ± SD: 1.76 ± 0.28 vs. 1.99 ± 0.43, respectively;
t = 0.92, df = 6, P = 0.197) were not significantly different between areas
with and without M. vimineum (Table 2). In addition, herbaceous plant diversity
was not related to M. vimineum percent cover. However, mean percent
cover of herbaceous plant species other than M. vimineum was significantly
higher in areas without M. vimineum than in areas with M. vimineum (mean
± SD: 30.41% ± 16.12 vs. 11.99% ± 4.33, respectively; t = 2.21, df = 6, P =
0.034). By adding M. vimineum to the herbaceous cover, percent herbaceous
plant cover was significantly greater in plots with M. vimineum than without
Figure 2. Mean (± SE) Acrididae (Orthoptera), Blattellidae (Dictyoptera),
Chrysomelidae (Coleoptera), Cicadellidae (Hemiptera), and Gryllidae (Orthoptera)
abundance (counts) with (n = 12) and without (n = 12) Microstegium vimineum in
central hardwood forests. Note: One-tailed t-tests between treatments within families
were significant (P < 0.05) for all families.
2009 J.M. Marshall and D.S. Buckley 521
(mean ± SD: 91.48% ± 7.27 vs. 30.41% ± 16.12, respectively; t = -6.91,
df = 6, P < 0.001). The presence of tree seedlings in plots was independent
on the presence of M. vimineum (X
2 = 2.58, df = 1, P = 0.108).
Table 2. Mean (SD) herbaceous plant species percent cover, species richness, and species diversity
in areas with (n = 4) and without Microstegium vimineum (n = 4) in central hardwood
Mean percent cover
Plant species With M. vimineum Without M. vimineum
Agrimonia pubescens Wallr. 0.00 1.53 (3.06)
Ambrosia artemisiifolia L. 0.00 1.53 (3.06)
Calystegia sepium (L.) R. Br. 0.51 (1.02) 0.00
Campsis radicans (L.) Seem. ex Bureau 1.53 (3.06) 0.00
Carex sp. L. 0.51 (1.02) 0.00
Daucus carota L. 0.51 (1.02) 0.00
Desmodium canescens (L.) DC. 0.51 (1.02) 0.51 (1.02)
Dichanthelium clandestinum (L.) Gould 0.51 (1.02) 0.00
Duschesnea indica (Andr.) Focke 2.19 (3.16) 7.87 (15.74)
Elaeagnus umbellata Thunb. 0.51 (1.02) 6.12 (12.24)
Erechtites hieraciifolia (L.) Raf. ex DC. 0.00 0.51 (1.02)
Euonymus americana L. 0.89 (1.79) 2.30 (1.74)
Euonymus fortunei (Turcz.) Hand.-Maz. 0.00 9.01 (18.03)
Galium concinnum Torr. & Gray 1.02 (2.04) 0.00
Geum canadense Jacq. 2.04 (2.89) 0.51 (1.02)
Impatiens capensis Meerb. 2.24 (4.49) 0.00
Lespedeza repens (L.) W. Bartram 0.00 0.51 (1.02)
Lonicera japonica Thunb. 8.79 (7.24) 2.37 (2.74)
Maianthemum racemosum (L.) Link 0.51 (1.02) 2.30 (2.68)
Microstegium vimineum (Trin.) A. Camus 79.49 (8.82) 0.00
Mitchella repens L. 0.00 8.06 (16.12)
Ophioglossum vulgatum L. 1.02 (1.02) 0.00
Osmorhiza claytonii (Michx.) C.B. Clarke 0.00 1.22 (2.45)
Oxalis stricta L. 0.00 0.51 (1.02)
Parthenocissus quinquefolia (L.) Planch. 4.17 (3.73) 5.83 (5.15)
Polygonum pensylvanicum L. 1.36 (2.72) 0.00
Polygonum persicaria L. 1.02 (2.04) 0.00
Polystichum acrostichoides (Michx.) Schott 0.00 7.65 (15.31)
Potentilla recta L. 1.53 (3.06) 0.00
Ranunculus sp. L. 3.16 (4.09) 0.00
Rosa multifl ora Thunb. 0.00 1.53 (3.06)
Rubus sp. L. 3.06 (3.53) 2.55 (5.10)
Smilax rotundifolia L. 0.00 2.55 (3.06)
Solanum carolinense L. 1.02 (1.18) 0.00
Solidago sp. L. 1.02 (2.04) 0.00
Toxicodendron radicans (L.) Kuntze 1.02 (2.04) 5.47 (5.31)
Tradescantia subaspera Ker Gawl. 0.51 (1.02) 0.00
Uvularia perfoliata L. 0.00 0.51(1.02)
Vaccinium sp. L. 0.00 2.55 (5.10)
Viburnum acerifolium L. 0.00 5.27 (10.54)
Viola sp. L. 2.04 (2.89) 0.51 (1.02)
Vitis rotundifolia Michx. 0.51 (1.02) 11.73 (20.77)
Wisteria fl oribunda (Willd.) DC. 0.00 2.38 (4.76)
Plant species richness 11.75 (4.27) 15.50 (6.45)
Plant species diversity 1.76 (0.28) 1.99 (0.43)
522 Southeastern Naturalist Vol. 8, No. 3
Insect family diversity was inversely related to plant species diversity
(Fig. 3). Insect family diversity was not significantly related to mean air
temperature, relative humidity, or canopy cover. Also, the abundance of insects
was not significantly related to mean air temperature, relative humidity,
canopy cover, percent herbaceous plant cover, M. vimineum percent cover,
or plant species diversity.
The most obvious difference, as well as statistically significant difference,
was the increase in percent plant cover as a result of the inclusion of
M. vimineum. Herbaceous plant cover was over 3 times higher in areas with
M. vimineum than in those without, because of the addition of this species.
Other research provides little evidence that M. vimineum alters hardwood
forest communities, but this species still remains a species of management
concern. While Cole (2006) illustrated that some hardwood tree species had
lower germination in M. vimineum and Oswalt et al. (2004, 2007) found
decreases in abundance of woody stems and growth of out-planted oak
seedlings with increases in M. vimineum, there have been no assessments
of overall changes in forest plant and insect communities with M. vimineum
establishment. In addition, other arthropods, such as I. scapularis, may exhibit
very little change, in terms of distribution and abundance, as a result
of M. vimineum invasion (Carroll 2003). Based on the results of this study,
Figure 3. Linear relationship between plant species diversity and insect family diversity
in central hardwood forests.
2009 J.M. Marshall and D.S. Buckley 523
it appears that the overall plant community diversity, and not the abundance
of M. vimineum, affects the diversity of insects. This finding differs from
results for other invasive species which have changed insect communities
associated with the invaded forest plant communities, resulting in decreased
insect abundance and richness (Standish 2004).
Without studies quantifying the feeding habits of insects on M. vimineum,
there is no clear explanation for the increases in the abundances of Acrididae,
Cicadellidae, and Gryllidae and reductions in the abundances of Blattellidae
and Chrysomelidae with the presence of M. vimineum. However, general
family characteristics may provide some information regarding the observed
changes. Acrididae are usually generalist herbivores and respond to the increased
overall plant cover and structure (Lawton 1983). Also, increases in
Acrididae food quality has resulted in measurable increases in population size
(Oedekoven and Joern 2000). Increases in abundances of Acrididae in areas
with M. vimineum may have been associated with changes in plant structure
due to the addition of M. vimineum to the community; however, further investigations
are necessary to clarify this relationship.
The reductions in abundance of Blattellidae in areas with M. vimineum
may result from the changes that occur in the decomposition of litter under
M. vimineum compared to native litter layers (Kourtev et al. 2002). In contrast,
increases in Gryllidae individuals may also have been a result of the
decomposition of litter under M. vimineum, selecting for the increased litter
layer nitrogen content under M. vimineum stands (Ehrenfeld et al. 2001,
Schädler et al 2003).
The reduced herbaceous plant cover other than M. vimineum in areas
where this species occurred may explain the reduced abundance of Chrysomelidae;
there may have been fewer plants acceptable for feeding by
individuals in this family. Typically, species within this family are specific
to their food plant; oftentimes these species are monophagous or oligophagous
(Arnett et al. 2002). In addition, species within the family Cicadellidae
are also food-plant specific (Triplehorn and Johnson 2005) and were more
abundant in areas with M. vimineum. Differences in the responses of these
two host-specific taxa may be due to the differences of native plants in areas
with and without M. vimineum. Plant species occurring only with or without
M. vimineum may have played an important role in the distribution of insects
from these two families.
The negative relationship in insect family and plant species diversities
in this study also concurred with several arthropod functional groups
presented by Koricheva et al. (2004). This relationship between insect and
plant diversities suggests that the overall plant community may be a more
influential driver in the distribution of insects rather than the invasion of
M. vimineum. The invasion of M. vimineum may alter decomposition rates
and soil functionality (Ehrenfeld et al. 2001; Kourtev et al. 2002, 2003),
but the presence of this species appeared to have little effect on the plant
species richness or diversity. Other factors may have attributed to the
524 Southeastern Naturalist Vol. 8, No. 3
invasion by M. vimineum, such as forest management (Marshall and Buckley
2008). Such factors may have been the overarching cause of changes in
plant species diversity, ultimately altering the insect community (Maskell
et al. 2006, Palmer et al. 2004).
The authors thank Jason Corsberg, Richard M. Evans, Brien Ostby, Martin R.
Schubert, and J. Mark Young for assistance in the planning and implementation of
this study. The authors are also grateful to Dr. Craig Harper and John Gruchy for
loaning the vacuum sampler used in this work, and to Dr. Jerome F. Grant for his
review of an earlier version of this manuscript.
Arnett, R.H. Jr., M.C. Thomas, P.E. Kelley, and J.H. Frank. 2002. American Beetles,
Volume II: Polyphaga: Scarabaeoidea through Curculionoidea. CRC Press LLC,
Boca Raton, FL. 880 pp.
Carroll, J.F. 2003. Survival of larvae and nymphs of Ixodes scapularis Say (Acari:
Ixodidae) in four habitats in Maryland. Proceedings of the Entomological Society
of Washington 105:120–126.
Cole, P. 2006. The non-native grass, Microstegium vimineum, suppresses woody
seedling recruitment in understory habitat. Southeastern Biologist 53:171.
Daly, H.V., J.T. Doyen, and A.H. Purcell III. 1998. Introduction to Insect Biology and
Diversity. Oxford University Press, Oxford, UK. 688 pp.
Ehrenfeld, J.G., K. Kourtev, and W. Huang. 2001. Changes in soil functions following
invasions of exotic understory plants in deciduous forests. Ecological
Fairbrothers, D.E., and J.R. Gray. 1972. Microstegium vimineum (Trin.) A. Camus
(Gramineae) in the United States. Bulletin of the Torrey Botanical Club
Floyd, D.A., and J.E. Anderson. 1987. A comparison of three methods for estimating
plant cover. Journal of Ecology 75:221–228.
Fralish, J.S. 2003. The Central Hardwood forest: Its boundaries and physiographic
provinces. Pp. 1–20, In J.W. Van Sambeek, J.O. Dawson, F. Ponder Jr., E.F.
Loewenstein, and J.S. Fralish (Eds.). Proceedings of the 13th Central Hardwood
Forest Conference. General Technical Report NC-234. USDA Forest Service,
North Central Research Station, St. Paul, MN.
Harper, C.A., and D.C. Guynn Jr. 1998. A terrestrial vacuum sampler for macroinvertebrates.
Wildlife Society Bulletin 26:302–306.
Hayek, L.C., and M.A. Buzas, M.A. 1997. Surveying Natural Populations. Columbia
University Press, New York, NY. 563 pp.
Hunt, D.M., and R.E. Zaremba. 1992. The northeastward spread of Microstegium
vimineum (Poaceae) into New York and adjacent states. Rhodora 94:167–170.
Integrated Taxonomic Information System (ITIS). 2007. ITIS home page. Available
online at http://www.itis.gov. Accessed 12 March 2007.
James, P. 2003. 2002–2003 Annual Report. Ijams Nature Center, Knoxville, TN. 16 pp.
Johnson, K. 1997. Tennessee Exotic Plant Management Manual. Great Smoky
Mountain National Park, Gatlinburg, TN, and Tennessee Exotic Pest Plant Council,
2009 J.M. Marshall and D.S. Buckley 525
Koricheva, J., C.P.H. Mulder, B. Schmid, J. Joshi, and K. Huss-Danell. 2004. Numerical
responses of different trophic groups of invertebrates to manipulations
of plant diversity in grasslands. Oecologia 125:271–282.
Kourtev, P.S., J.G. Ehrenfeld, and W.Z. Huang. 2002. Enzyme activities during litter
decomposition of two exotic and two native plant species in hardwood forests of
New Jersey. Soil Biology and Biochemistry 34:1207–1218.
Kourtev, P.S., J.G. Ehrenfeld, and M. Haggblom. 2003. Experimental analysis of
the effect of exotic and native plant species on the structure and function of soil
microbial communities. Soil Biology and Biochemistry 35:895–905.
Lawton, J.H. 1983. Plant architecture and the diversity of phytophagous insects. Annual
Review of Entomology 28:23–39.
Leicht, S.A., J.A. Silander, Jr., and K. Greenwood. 2005. Assessing the competitive
ability of Japanese Stiltgrass, Microstegium vimineum (Trin.) A. Camus. Journal
of the Torrey Botanical Society 132:573–580.
Mack, R.N., D. Simberloff, W.M. Lonsdale, H. Evans, M. Clout, and F.A. Bazzaz.
2000. Biotic invasions: Causes, epidemiology, global consequences, and control.
Ecological Applications 10:689–710.
Mandryk, A.M., and R.W. Wein. 2006. Exotic vascular plant invasiveness and forest
invasibility in urban boreal forest types. Biological Invasions 8:1651–1662.
Marshall, J.M., and D.S. Buckley. 2008. Infl uence of litter removal and mineral soil
disturbance on the spread of an invasive grass in a Central Hardwood forest.
Biological Invasions 10:531–538.
Maskell, L.C., L.G. Firbank, K. Thompson, J.M. Bullock, and S.M. Smart. 2006.
Interactions between non-native plant species and the fl oristic composition of
common habitats. Journal of Ecology 94:1052–1060.
Meiners, S.J., S.T.A. Pickett, and M.L. Cadenasso. 2002. Exotic plant invasions
over 40 years of old-field successions: Community patterns and associations.
National Climatic Data Center (NCDC). 2007. NCDC home page. Available online
at http://www.ncdc.noaa.gov/oa/ncdc.html. Accessed 15 May, 2007.
Oedekoven, M.A., and A. Joern. 2000. Plant quality and spider predation affects
grasshoppers (Acrididae): Food-quality-dependent compensatory mortality.
Oswalt, C.M., W.K. Clatterbuck, S.N. Oswalt, A.E. Houston, and S.E. Schlarbaum.
2004. First-year effects of Microstegium vimineum and early growing season
herbivory on planted high-quality oak (Quercus spp.) seedlings in Tennessee.
Pp. 1–9, In D.A. Yaussy, D.M. Hix, R.P. Long, and P.C. Goebel (Eds.). Proceedings
of the 14th Central Hardwood Forest Conference. General Technical
Report NE-316. USDA, Forest Service, Northeastern Research Station, Newton
Oswalt, C.M., S.N. Oswalt, and W.K. Clatterbuck. 2007. Effects of Microstegium
vimineum (Trin.) A. Camus on native woody species diversity in a productive
mixed-hardwood forest in Tennessee. Forest Ecology and Management
Palmer, M., M. Linde, and G.X. Pons. 2004. Correlational patterns between invertebrate
species composition and the presence of an invasive plant. Acta Oecologica
Redman, D.E. 1995. Distribution and habitat types for Nepal Microstegium (Microstegium
vimineum (Trin.) Camus) in Maryland and the District of Columbia.
526 Southeastern Naturalist Vol. 8, No. 3
Schädler, M., G. Jung, H. Auge, and R. Brandl. 2003. Palatability, decomposition,
and insect herbivory: Patterns in a successional old-field plant community. Oikos
Siemann, E., and W.E. Rogers. 2006. Recruitment limitation, seedling performance,
and persistence of exotic tree monocultures. Biological Invasions 8:979–991.
Standish, R.J. 2004. Impact of an invasive clonal herb on epigaeic invertebrates in
forest remnants in New Zealand. Biological Conservation 116:49–58.
Steele, J., R.S. Chandran, W.N. Grafton, C.D. Huebner, and D.W. McGill. 2006.
Awareness and management of invasive plants among West Virginia woodland
owners. Journal of Forestry 104:248–253.
Triplehorn, C.A., and N.F. Johnson. 2005. Borror and DeLong's Introduction to the
Study of Insects. Brooks Cole, Belmont, CA. 864 pp.
Tscharntke, T., A.M. Klein, A. Kruess, I. Steffan-Dewenter, and C. Thies. 2005.
Landscape perspectives on agricultural intensification and biodiversity: Ecosystem
service management. Ecology Letters 8:857–874.
US Department of Agriculture Natural Resource Conservation Service (USDA
NRCS). 2007. The PLANTS Database. Available online at http://plants.usda.gov.
Accessed March 12, 2007.