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The contribution of epiphytes to the abundance and species richness of canopy insects in a Mexican coffee plantation

Published online by Cambridge University Press:  01 September 2009

Andrea Cruz-Angón ,
Martha L. Baena  and
Russell Greenberg
Andrea Cruz-Angón
Affiliation:
Instituto de Ecología, A.C. Departamento de Ecología Funcional. Km 2.5 antigua carretera a Coatepec, No. 315. 91070, Xalapa, Veracruz, México
Martha L. Baena
Affiliation:
Instituto de Ecología, A.C. Departamento de Ecología Funcional. Km 2.5 antigua carretera a Coatepec, No. 315. 91070, Xalapa, Veracruz, México
Russell Greenberg*
Affiliation:
Smithsonian Migratory Bird Center, National Zoological Park, Washington, DC 20008, USA
*
2Corresponding author. Email: greenbergr@si.edu
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Abstract:

The abundance of epiphytes has been assumed to be important in explaining the high diversity of tropical canopy arthropods. In this study we assessed the possible role that the presence of epiphytes may have on the diversity and abundance of canopy insects in an experimental study conducted in a coffee plantation in Coatepec, Veracruz, Mexico. Epiphytes were removed from trees in one of two plots in two sites of the coffee plantation. In each plot we collected insects from three Inga jinicuil trees by knockdown insecticide fogging. Insects were sorted to morphospecies, counted and measured. Trees with epiphytes had significantly higher numbers of species and individuals and insects larger than 5 mm were also more species-rich and abundant in trees with epiphytes. The magnitude of the enhancement was surprisingly large with the epiphyte plot samples having on average 90% more individuals and 22% more species than plots without epiphytes. These differences were even greater for large (>5 mm) insects (184% and 113% respectively). Our results support the tenet that epiphytes provide valuable resources to arthropods, which we have illustrated for canopy insects in shade trees of coffee plantations.

Keywords

bromeliadscanopy insectscommunity structureInga jinicuilMexicorichnessshade coffeevascular epiphytes

Information

Type
Research Article
Information
Journal of Tropical Ecology , Volume 25 , Issue 5 , September 2009 , pp. 453 - 463
Copyright
Copyright © Cambridge University Press 2009

INTRODUCTION

The canopy of a tropical forest supports a remarkably high diversity of arthropods (Basset et al. Reference BASSET, SAMUELSON, ALLISON and MILLER1996, Reference BASSET, NOVOTNY, MILLER, KITCHING, Basset, Novotny, Miller and Kitching2003; Erwin Reference ERWIN1982, Lucky et al. Reference LUCKY, ERWIN and WITMAN2002, Novotný & Basset Reference NOVOTNÝ and BASSET2000, Stork Reference STORK1987). This phenomenon has also been documented for agroforestry systems, such as coffee and cocoa (Bos et al. Reference BOS, STEFFAN-DEWENTER and TSCHARNTKE2007, Perfecto et al. Reference PERFECTO, VANDERMEER, HANSON and CARTÍN1997). So substantial is canopy arthropod species richness that Erwin's publications (Erwin Reference ERWIN1982, Reference ERWIN1983) on beetle diversity of the tree Luehua seemannii in Panama spawned new estimates on the number of total species thought to inhabit the earth's ecosystems. Although the debate on the overall estimates of species numbers still continues (Erwin Reference ERWIN1991, Gaston Reference GASTON1991), investigations of proximate and ultimate mechanisms responsible for the high diversity of tropical canopy fauna have only just begun (Basset et al. Reference BASSET, NOVOTNY, MILLER, KITCHING, Basset, Novotny, Miller and Kitching2003, Ellwood et al. Reference ELLWOOD, JONES and FOSTER2002, Stuntz et al. Reference STUNTZ, ZIEGLER, SIMON and STOTZ2002a). In general, complex vegetation structure and floristic diversity is thought to support high insect diversity. Epiphytes comprise a highly diverse group of plants that improve the structural complexity of the canopy and provide resources in addition to those provided by tree hosts (Benzing Reference BENZING1990, Gentry & Dodson Reference GENTRY and DODSON1987, Kress Reference KRESS1986, Nadkarni Reference NADKARNI1994, Nadkarni & Matelson Reference NADKARNI and MATELSON1989). It is therefore important to consider the role of epiphytes in supporting diversity in the forest canopy (Ellwood et al. Reference ELLWOOD, JONES and FOSTER2002, Kitching et al. Reference KITCHING, MITCHEL, MORSE, THEBAUD, Stork, Adis and Didham1997, Ødegaard Reference ØDEGAARD2000, Stork Reference STORK1987). It has already been established that epiphytes provide important resources for canopy vertebrates (Chan Reference CHAN2003, Cruz-Angón & Greenberg Reference CRUZ-ANGÓN and GREENBERG2005, Cruz-Angón et al. Reference CRUZ-ANGÓN, SILLETT and GREENBERG2008, Nadkarni & Matelson Reference NADKARNI and MATELSON1989, Raboy et al. Reference RABOY, CHRISTMAN and DIETZ2004, Sillett Reference SILLETT1996). Although several authors have specifically assessed arthropod diversity within the epiphyte microcosm (Armbruster et al. Reference ARMBRUSTER, HUTCHINSON and COTGREAVE2002, Cotgrave et al. Reference COTGRAVE, HILL and MIDDLETOWN1993, Paoletti et al. Reference PAOLETTI, TAYLOR, STINNER, STINNER and BENZING1991, Richardson Reference RICHARDSON1999, Richardson et al. Reference RICHARDSON, RICHARDSON, SCATENA and MCDOWELL2000, Stuntz Reference STUNTZ2001, Wittman Reference WITTMAN2000, Yanoviak et al. Reference YANOVIAK, NADKARNI and SOLANO2006), very few studies have established the overall contribution of epiphytes to an entire tree crown's arthropod diversity (Ellwood et al. Reference ELLWOOD, JONES and FOSTER2002, Stuntz et al. Reference STUNTZ, SIMON, ZOTZ, Basset, Novotny, Miller and Kitching2003).

Epiphytes may be important for canopy arthropods in several distinct ways. Epiphytes, particularly long-lived bromeliads (Benzing Reference BENZING1994), provide important microhabitats protected from the often harsh conditions of a tropical forest canopy (Ellwood et al. Reference ELLWOOD, JONES and FOSTER2002, Stuntz et al. Reference STUNTZ, ZIEGLER, SIMON and STOTZ2002a). Epiphytes may also enhance arthropod diversity through the production of soil and litter environment and the provision of foliage that is consumed by herbivorous insects (Schmidt & Zotz Reference SCHMIDT and ZOTZ2000). Epiphytes also attract predators and parasites of herbivorous insects as well as pollinators of epiphytic angiosperms (Wittman Reference WITTMAN2000). All these arthropods may only spend a portion of their life in the bromeliads and thus contribute to the overall abundance of arthropods throughout the canopy (Richardson et al. Reference RICHARDSON, RICHARDSON, SCATENA and MCDOWELL2000, Stork Reference STORK1987, Wittman Reference WITTMAN2000).

The development of techniques to access the canopy of tropical trees resulted in a great number of studies conducted within the last two decades (Floren & Linsenmair Reference FLOREN, LINSENMAIR, Stork, Adis and Didham1997). Among these techniques, knockdown insecticide fogging has been one of the most commonly used to collect from the ground big samples of canopy arthropods (Basset & Kitching Reference BASSET and KITCHING1991, Erwin Reference ERWIN1982, Reference ERWIN1983; Perfecto et al. Reference PERFECTO, VANDERMEER, HANSON and CARTÍN1997, Stork Reference STORK1987, Stork & Blackburn Reference STORK and BLACKBURN1993). In most studies of canopy arthropods, authors have failed to report the presence or absence of epiphytic components in the trees they have sampled. Only in very few studies the presence of epiphytes or their influence on canopy arthropods assessed was actually controlled or quantified (Ellwood et al. Reference ELLWOOD, JONES and FOSTER2002, Stork Reference STORK1987, Stuntz Reference STUNTZ2001). Thus, although epiphytes are an important resource for other canopy fauna, such as birds, in human-managed ecosystems such as agroforests (Cruz-Angón & Greenberg Reference CRUZ-ANGÓN and GREENBERG2005), no study has examined the contribution of epiphytic plants to insect diversity in these important tropical habitats. Working in a coffee plantation in Mexico, we determined the impact of the presence of epiphytes on canopy insects, where epiphytes were either experimentally removed from shade trees or left alone, by examining: (1) the richness and abundance of canopy insects; (2) the community similarity; (3) the patterns for large insects which are probably a more important resource for vertebrates. To our knowledge this is the first large-scale experiment where epiphytes have been removed to evaluate their influence on canopy insects in a coffee agro-ecosystem.

METHODS

Study site

Our study site was a 35-y-old, 200-ha shaded coffee plantation located in Coatepec, Veracruz, Mexico (19° 28′03″N, 96° 55′58″W; 1224 m asl). The coffee management system can be described as a commercial polyculture shade type (Moguel & Toledo Reference MOGUEL and TOLEDO1999). We recorded 35 species of tree in the canopy, but the tree assemblage was dominated by Inga jinicuil Schltdl. & Cham. ex G. Don, a nitrogen-fixing, fast-growing legume (Roskoski Reference ROSKOSKI1981, Reference ROSKOSKI1982). Epiphytes were abundant in the plantation where we have recorded up to 40 species of vascular epiphyte in the experimental plots out of 57 total canopy-dwelling species found on the plantation (Cruz-Angón unpubl. data). The most common species include bromeliads such as Tillandsia schiedeana Steud., T. heterophylla E. Morren and T. juncea (Ruiz & Pav.) Poir. The cactus Rhipsalis baccifera (Mill.) Stearn and the aroid Anthurium scandens (Aubl.) Engl. are also common.

Experimental design

We established two experimental sites located on opposite sides (hereafter site: N = North, S = South) of the coffee plantation, and separated by a distance of approximately 1 km. Each site was divided into two 3-ha plots surrounded by a matrix of shaded coffee with epiphytes. During the dry seasons of 1999 and 2000 plantation workers removed all the epiphytes from the shade trees of one of the two plots in both the north and south sites (hereafter plots: NE+ = North with epiphytes, NE− = North without epiphytes; SE+ = South with epiphytes, SE− = South without epiphytes). In each plot we established a grid of 625-m2 (25 × 25 m) quadrats identified by alphanumeric coordinates. We took several vegetation measurements to establish plot differences. An extended description of the study site and experimental plots can be seen in Cruz-Angón & Greenberg (Reference CRUZ-ANGÓN and GREENBERG2005). Mean epiphyte richness per tree among plots did not differ (F(2, 42) = 0.88, P = 0.42) (Cruz-Angón & Greenberg Reference CRUZ-ANGÓN and GREENBERG2005). As a result of the treatment applied, plots without epiphytes (NE− and SE−) had significantly more open canopy than their respective counterparts (NE+ and SE+). This was the only significantly different variable between control and treatment plots and is primarily the direct result of the loss of cover from the removal of epiphytes.

Tree selection

We restricted our samplings to I. jinicuil, the dominant shade-tree species which represented 48–77% of the total trees. In our study site these trees supported an abundant epiphytic flora, averaging (mean ± SE) 15.5 ± 0.4 epiphyte species per tree.

In each plot we randomly selected three grid points and located the nearest I. jinicuil tree. Trees were selected to be similar in crown diameter (≈ 8 m), height (8–11 m), dbh (30–60 cm), and epiphyte loads (50–60% branch covered with vascular epiphytes, primarily bromeliads). One advantage of working in a coffee plantation with commercial polyculture shade management is that most shade trees are planted at the same time, thus epiphyte colonization probably also started at the same time. Also, in commercial polycultures trees are usually pruned within the same year, and tree crowns do not overlap, thus facilitating fogging and collecting insects from a single tree crown.

Canopy fogging and insect collection

Insects were sampled by knock-down insecticide fogging, where a warm fog containing a pyrethrine-based non-persistent insecticide is generated by a thermal pulse-jet engine, which rises into a tree canopy (Stork Reference STORK1991). Insects coming into contact with the chemical are either killed or immobilized, and fall to the plastic sheets set up previously.

A day before we conducted the fogging, we set up two 4 × 4-m plastic sheets at each tree side, just above of the coffee shrubs (>2 m height), in order to cover most of the tree canopy (Figure 1) (Majer & Delabie Reference MAJER and DELABIE1993). Plastic sheets were kept folded until the fogging day when they were unfolded and extended. To collect insects dropping from the canopy, we placed a 1.89-litre plastic container with alcohol (70%) at the centre of each plastic sheet. A total surface area of 384 m2 was sampled overall.

Figure 1.

Trap setting for a knockdown insecticide fogging of an Inga jinicuil tree with epiphytes in a coffee plantation, Coatepec, Veracruz, Mexico. Inga jinicuil trees experimentally depleted of epiphytes were also fogged and insects collected.

Fogging was conducted at 6h30–8h30 on 14–16 December 2000, when wind speeds were low, which allowed the fog to go up slowly, covering the entire tree before dispersing. The 15-min fogging process was followed by a 2-h drop-out period; plastic sheets were then screened very carefully and all insects in them were collected and placed in the containers. Insect containers were sealed and transported to the Entomology Laboratory of the Instituto de Ecología for further examination. Although we collected all invertebrates from fogged trees, we restricted our analysis to adult insect stages, because it was not possible with nymphs and larvae to accurately assign most to a given species. With the exception of Lepidoptera (which we were unable to sort), all adult individuals were counted, measured (length and width) and sorted to species based on external morphology. Immature stages were sorted only to family, measured and counted. All animals were cross-referenced with a voucher collection to ensure singularity of assigned species. The order Lepidoptera was excluded from all analyses regarding species richness and composition, but was included for the abundance analyses.

All of the specimens collected were checked and identified by one of the authors (M. L. Baena) to avoid taxonomic bias. Specimens were deposited at the Entomology Department of Instituto de Ecología, A.C. in Xalapa, Mexico.

Data analysis

Insect diversity and abundance. To assess the completeness of our sampling, we constructed smoothed species accumulation curves (Gotelli & Colwell Reference GOTELLI and COLWELL2001) by randomizing samples by plot 100 times. We then compared the observed values with the mean expected number of species using Chao1 estimator (Colwell & Coddington Reference COLWELL and CODDINGTON1994). We used EstimateS 7.5.0 (http://viceroy.eeb.uconn.edu/EstimateS7Pages/EstimateS7Support.htm) to randomize samples and to obtain the expected number of species. We conducted GLMs for a split-plot design where the whole plot was the sites (site: north and south) that contained the partial–experimental plots (treatment: E+ and E–). Trees were nested into the smaller plots. This allowed us to search for differences in abundance and species richness between treatments (E+ vs. E–) for all insects collected and for insects larger than 5 mm. This permitted us to maximize the power of tests for the factor (treatment) in which we were most interested (Sahai & Ageel Reference SAHAI and AGEEL2000). Following tests for normality and homoscedasticity we used a square-root transformation on the data (Zar Reference ZAR1999).

Composition and similarities of assemblages. To quantify the similarity in the composition of assemblages among trees in plots, we generated a similarity matrix that was used for all multivariate analysis described below. The similarity matrix consisted of pairwise comparisons between samples, based on the Bray–Curtis similarity index from observed species abundances transformed to the fourth root. This transformation reduces the influence of the most common taxa and focuses attention on patterns across the whole assemblage (Clarke Reference CLARKE1993). Subsequently, we performed a two-way crossed ANOSIM (analysis of similarity) using PRIMER 5 program (Clarke Reference CLARKE1993, Clarke & Gorley Reference CLARKE and GORLEY2001) to test for significant differences in community composition between site groups (North and South) and between treatment groups (E+ and E–). Finally, we conducted a Multidimensional scaling (MDS) using the MDS program in PRIMER, to graphically ordinate differences in species assemblages between treatment plots onto two dimensional charts.

RESULTS

Insect diversity and abundance

We collected 23 199 arthropods. Non-insect arthropods accounted for 30% of the collected items. Insect adults (61% of the collected individuals) comprised 12 orders, 168 families and 602 species (see Appendix 1 for list of orders and families collected). Of collected insect adults, 90% were < 5 mm long. Hymenoptera and Diptera were the most abundant insect orders, representing 39.8% and 31.2% of the adult individuals, respectively. The most species-rich orders were Coleoptera with 248 species in 48 families and Diptera with 144 species in 67 families (Table 1).

Table 1.

Number of insect morphospecies by order or suborder and number of families (in parentheses) captured during the canopy fogging of 12 Inga jinicuil trees in an experimental setting in a shade coffee plantation where six trees (three per plot) had epiphytes removed while the other six trees remain with epiphytes, in Coatepec, Veracruz, Mexico. Sites: North, South, Treatments: E+ = with epiphytes, E− = without epiphytes. Total columns show total number of families and species per site. Expected number of species was obtained using Chao 1 estimator. Completeness represents the percentage of observed versus estimated species richness. Within dissimilarity represents the mean percentage dissimilarity between samples within plots. In bold are the groups that showed a consistent pattern of higher diversity in E+ plots.

In general, 75.4% (454 species) of the species were represented by less than 10 individuals, contributing to less than 10% (1484 individuals) of the total catch. Indeed, 34% were represented by a single individual (singletons). Only 6% of the species (41) were represented by at least 50 individuals. These common species represented 72% of the collected individuals.

Response to epiphyte removal

The orders that showed a consistent pattern of higher diversity in E+ plots than in E– plots were Coleoptera, Diptera, Hymenoptera and Orthoptera (Table 1). In order Hymenoptera, ants (Formicidae) were three times more abundant in E+ than in E– plots (F(1,12) = 19.0, P > 0.001; Mean ± SE: E+ = 245 ± 76.8; E− = 69.6 ± 25.9).

Randomized species accumulation curves show that plots in the South site had significantly more species than plots in the North site. None of the plots showed an asymptotic curve. Plots with epiphytes (NE+ and SE+) had significantly more species than their E– counterparts (Figure 2). Expected number of species showed a consistent pattern of species accumulation by treatment and sites (Figure 3). Richness estimates for E– plots indicate that inventory levels were above 70%, whereas for E+ plots inventory completeness were below 70% (Table 1). This indicates that in order to achieve more complete sampling, E+ plots would require a greater sampling effort than E– plots.

Figure 2.

Mean species accumulation curves for insect species collected by knockdown fogging of three trees per plot (two samples per tree) in an experimental setting in a coffee plantation in Central Veracruz, Mexico. Experimental plots: North with epiphytes (♦), North without epiphytes (□), South with epiphytes (▲), and South without epiphytes (○). Error bars represent 95% Confidence Intervals.

Figure 3.

Mean expected number of insect species by experimental plot in a coffee plantation in Central Veracruz, Mexico. Mean expected number of species were based on Chao 1 estimator form the 100 iterations. Experimental plots: NE+ = North with epiphytes, NE− = North without epiphytes, SE+ = South with epiphytes, SE− = South without epiphytes. Error bars represent 95% confidence intervals.

The ANOVA showed that sites differed significantly in both mean number of species and individuals (species: F (1,12) = 36.8, P < 0.001; individuals: F (1,12) = 79.7, P < 0.001). Mean (± SE) species richness and abundance by tree were significantly greater in South plots (species: 103 ± 10.9; individuals: 661 ± 126) than in the North plots (species: 58.6 ± 7.3; individuals: 338 ± 96.9). The treatment factor was significant for both mean number of species and individuals (species: F (1,12) = 8.9, P = 0.01; individuals: F (1,12) = 23.1, P < 0.001). The mean number of species and individuals was significantly greater in plots with epiphytes (species: 89.2 ± 13.4; individuals: 655 ± 143) than in plots without epiphytes (species: 72.7 ± 8.6; individuals: 344 ± 71.3). Site by treatment effects for either number of species or individuals were not significant (species: F (1,12) = 1.3, P < 0.27; individuals: F (1,1) = 0.02, P < 0.90). Treatment effects for abundance and richness of insects larger than 5 mm were also significant (species: F (1,12) = 9.6, P = 0.009; individuals: F (1,12) = 9.9, P = 0.008). Mean number of species and individuals for this group size was significantly greater in plots with epiphytes (species: 23.8 ± 6.09; individuals: 136 ± 56.1) than in plots without epiphytes (species: 11.2 ± 1.22; individuals: 47.7 ± 9.62).

Community structure and similarities

Community structure varied greatly among sites and treatments. Mean dissimilarity within plots was almost as great as dissimilarity among plots (Table 2). ANOSIM showed that all plots significantly differed in community composition. Averaged dissimilarity among plots was about 80%. Despite the high species turnover and community structure differences, the nMDS generated a well-defined ordination in which dimension 1 separated samples by site, whereas dimension 2 separated samples by treatment (Figure 4).

Table 2.

Results from two-way crossed ANOSIM test, based on Bray–Curtis dissimilarities in fourth-root-transformed insect abundances from four experimental plots in a coffee plantation, Central Veracruz, Mexico. Pairwise ANOSIM tests for differences between plots. Experimental plots: NE+ = North with epiphytes, NE− = North without epiphytes, SE+ = South with epiphytes, SE− = South without epiphytes.

Figure 4.

Ordination of two matched pairs of experimental plots, based on a multidimensional scaling analysis used to compare the similarities of the studied plots (Stress = 0.17). Experiment consisted in removing epiphytes from all trees in one of two plots in two sites. Two samples per trees, three trees per site were fogged and insects were collected. Experimental Plots: North with epiphytes (♦), North without epiphytes (□), South with epiphytes (▲), and South without epiphytes (○). Stress = 0.16.

DISCUSSION

Insect richness, abundance and size distribution

Our results show that in the focal shade coffee plantation, epiphytes contributed to a high abundance and richness of insects. In our study the main difference between plots within a site (North and South) was the presence or absence of epiphytes. Trees with epiphytes had an average of 22% more species and 90% more individuals than trees without epiphytes. The percentage increase with epiphytes is even greater for insects > 5 mm in length (113% and 184%, respectively). Differences among sites may be explained by the difference in canopy cover which was greater in the South sites. Sites in the South had significantly more species and individuals than plots in the North. This indicates that the amount of tree foliage (canopy cover) may also be an important factor for canopy insect faunas (Wilkens et al. Reference WILKENS, VANDERKLEIN and LEMKE2005).

The relatively small number (10%) of insects larger than 5 mm was expected since, in general, average adult insect body length is in the order of 4–5 mm, and body size distributions more generally are skewed toward smaller sizes (Dudley Reference DUDLEY2000, May Reference MAY, Mound and Waloff1978). Moreover, it has been suggested that insecticide fogging may not be a good method to collect large canopy insects (Basset et al. Reference BASSET, SPRINGATE, ABERLENC, DELVARE, Stork, Adis and Didham1997, Ellwood et al. Reference ELLWOOD, JONES and FOSTER2002). This bias is mostly due to the fact that large insects get stuck in the canopy before dropping down. Nevertheless, a significantly greater number of large insects (> 5 mm), which are the most important food items for insectivorous vertebrates, were collected in trees with epiphytes than in trees without them. Experimental studies conducted in coffee plantations have shown that when birds are excluded from plants, insects within the exclosures tend to be larger and more abundant than insects outside the exclosure (Greenberg et al. Reference GREENBERG, BICHIER, CRUZ-ANGON, MACVEAN, PEREZ and CANO2000). Epiphytes may provide large insects with a hiding place from potential predators such as such as lizards or birds (Dial & Roughgarden Reference DIAL and ROUGHGARDEN1995, Greenberg et al. Reference GREENBERG, BICHIER, CRUZ-ANGON, MACVEAN, PEREZ and CANO2000). This may explain the significantly greater abundance of large insects in the E+ plots.

In terms of the effects of epiphytes on specific groups, only Hymenoptera (predominantly ants) showed significantly greater abundance in plots with epiphytes; ants have previously been reported to be the dominant insect species in epiphytes (Dejean et al. Reference DEJEAN, OLMSTED and SNELLING1995, Ellwood et al. Reference ELLWOOD, JONES and FOSTER2002, Longino & Nadkarni Reference LONGINO and NADKARNI1990, Stuntz et al. Reference STUNTZ, ZIEGLER, SIMON and STOTZ2002b, Wittman Reference WITTMAN2000). In addition to Hymenoptera three other orders (Coleoptera, Diptera and Orthoptera) showed a higher species richness in plots with epiphytes. Bromeliads can be used by different insect groups according to their own requirements. Some bromeliad species form cavities between their leaves and house insects like ants, which in turn can bring organic matter to the bromeliad cavities to fertilize their living domiciles. In such cases, the ants gain a place to live, but little or no food from their hosts (Janzen Reference JANZEN1974, Huxley Reference HUXLEY1980, Thompson Reference THOMPSON1981). Other insects can benefit from bromeliads, especially from trophic action, for example the particularly high relative abundance of Collembola (70%) probably reflects the high amount of decaying material retained within the epiphytes as this insect group is mainly comprised of detritivores (Rusek Reference RUSEK1998). Dermaptera species, some Coleoptera, especially from the Coccinellidae family and some ant species from the genera Pachicondyla, Odontomachus (Ponerinae) and Crematogaster (Myrmicinae) are predators and may help to protect epiphytes from herbivores.

In our study a large number of insect species (454) were represented by less than 10 individuals, a general pattern for tropical canopy (Basset & Kitching Reference BASSET and KITCHING1991, Floren & Linsenmair Reference FLOREN and LINSENMAIR1998, Lucky et al. Reference LUCKY, ERWIN and WITMAN2002, Morse et al. Reference MORSE, STORK and LAWTON1988, Novotný & Basset Reference NOVOTNÝ and BASSET2000). Given the large number of species found with fewer than 10 individuals it is possible that a portion of these species are tourist species that have no long-lasting relationship with the plant, but which may be attracted to trees for short-term use, such as for shelter and sustenance (honeydew and other substances), or as a site for sunbasking and sexual display (Gaston et al. Reference GASTON, BLACKBURN, HAMMOND and STORK1993). So our true canopy insect species richness may have been overestimated by the presence of tourist species, which we were not able to identify and exclude from the analysis. However, the presence of tourist species should not contribute to a systematic bias towards higher richness estimates for the epiphyte versus non-epiphyte plots. Furthermore, the influence of tourist species upon our estimate of faunal similarities should be low, since the index used is less sensitive to rare species.

Previous studies examining the role of epiphytes in arthropod communities are equivocal. Although very few studies have been based on an experimental removal of epiphytes (Ellwood et al. Reference ELLWOOD, JONES and FOSTER2002), the overall contribution of epiphytes to canopy insect abundance and composition at an ordinal level has been reported to be low (Stuntz et al. Reference STUNTZ, SIMON, ZOTZ, Basset, Novotny, Miller and Kitching2003). Stuntz et al. (Reference STUNTZ, SIMON, ZOTZ, Basset, Novotny, Miller and Kitching2003) studied the contribution of epiphytes to the overall arthropod richness of the small tropical tree Annona glabra (Annonaceae). In this study the authors collected the arthropods from A. glabra trees that had different species of epiphyte and no epiphytes at all. The authors found no significant differences in the abundance or community composition of arthropods between trees with and without epiphytes. However, their results may not be applicable to all tropical forest types, because they worked with a rather small tree (6 m) in an inundated area, and epiphytes were apparently not abundant in this tree. On the other hand, Ellwood et al. (Reference ELLWOOD, JONES and FOSTER2002) found that a single large bird's nest fern (Asplenium nidus) an epiphytic species that occurs throughout the forest of South-East Asia, may contain from 7–93% of the total number of invertebrates in the tree crown. These observations are more consistent with our results.

How appropriate is the canopy fogging technique for answering the questions posed in this study? Although insecticide knockdown fogging has proven not to be a good method for collecting the fauna of non-vascular epiphyte fauna (Yanoviak et al. Reference YANOVIAK, NADKARNI and GERING2003), the method has been reported to work well for vascular epiphytes (Stork & Hammond Reference STORK, HAMMOND, Stork, Adis and Didham1997). Furthermore, any underestimation of the abundance of arthropods in epiphytes due to the collection method would bias the results away from supporting the hypothesis of greater arthropod abundance on the epiphyte control plots. Therefore, we consider canopy fogging an appropriate approach to assessing the overall contribution of epiphytes to arthropod abundance and richness that should be followed up with more fine-tuned sampling and observational techniques to further assess guild composition, and proportion of rare species versus tourist.

Community structure and similarities

Our results showed great species dissimilarities between treatment and control plots, as well as trees within a plot. Such high spatial turnover between trees has been a consistent result of all tropical canopy arthropod studies (Davies et al. Reference DAVIES, STORK, BRENDELL, HINE, Stork, Adis and Didham1997, Erwin & Scott Reference ERWIN and SCOTT1980, Floren & Linsenmair Reference FLOREN and LINSENMAIR1998, Lucky et al. Reference LUCKY, ERWIN and WITMAN2002). Furthermore, high insect species turnover between epiphyte species has also been documented (Richardson et al. Reference RICHARDSON, BURGIN, AZARBAYJANI, LUTUBULA, Stork, Adis and Didham1997, Stuntz et al. Reference STUNTZ, ZIEGLER, SIMON and STOTZ2002b). For example, Stuntz et al. (Reference STUNTZ, ZIEGLER, SIMON and STOTZ2002b) found very little overlap in insect species composition for three species of epiphyte studied in an inundated forest in Panama. Despite the high levels of between-tree turnover in our study, we were able to document a pattern of faunal similarity within treatment groups based on multi-dimensional scaling, which indicates that regardless of the great species turnover, trees with epiphytes had a similar insect community structure when compared with trees without them. Our results are consistent with those of Stork (Reference STORK1987) who found that the amount of climbers and epiphytes was more important for faunal similarity in particular insect groups (i.e. Homoptera, Grulllidae, Anthicidae, Chrysomelidae and scavengers) than taxonomic relatedness of the trees, in a study conducted in Borneo.

Conservation implications of epiphyte removal

Over the last few decades several coffee-producing countries have simplified the shade of coffee plantations by reducing the richness and abundance of shade trees (Romero-Alvarado et al. Reference ROMERO-ALVARADO, SOTO-PINTO, GARCÍA-BARRIOS and BARRERA-GAYTAN2002). In Mexico, it has been estimated that over 49% of the producing area has been transformed from highly diverse shade systems to legume-dominated systems (Santoyo-Cortés et al. Reference SANTOYO-CORTÉS, DÍAZ-CÁRDENAS and RODRÍGUEZ-PADRÓN1994). In the latter systems, epiphyte removal from shade trees is a relatively common management practice (Cruz-Angón & Greenberg Reference CRUZ-ANGÓN and GREENBERG2005). The elimination of epiphytes and mistletoes from the canopy results in simplification of the vertical structure and richness of the coffee plantations that in fact are already simplified compared with pristine forests. Experimental evidence indicates that epiphyte removal may have negative effects in bird communities of coffee plantations (Cruz-Angón & Greenberg Reference CRUZ-ANGÓN and GREENBERG2005), even in species that do not have a direct relationship with epiphytes (do not use epiphytes as nesting sites or feeding substrate). In particular, insectivorous species that do not feed or nest in epiphytes were significantly less abundant in sites without epiphytes than in sites with epiphytes; the reduction of non-epiphyte-related bird species may be explained by the overall reduction in the number of insects observed in plots without epiphytes. Our results confirm that epiphytes might represent a keystone resource in coffee plantations, just as they do in other tropical forests because of their important role in controlling major functional characteristics of these ecosystems (Nadkarni Reference NADKARNI1994).

ACKNOWLEDGEMENTS

We thank A. Martínez-Fernández for assistance with fieldwork. The Martínez family and plantation manager R. Monge provided access to their coffee plantation and permission to tree fogging. F. Becerril drew the Inga jinicuil with epiphytes and trap setting for Figure 1. M. Ordano, R. Munguía and C. Tejeda, gave statistical advice; J.G. García-Franco, Federico Escobar, S. Philpott, V. Rico-Gray, and M. Coro-Arizmendi improved the manuscript with their comments and corrections. Funding to ACA was provided by CONACYT (scholarship 128767), Smithsonian Institution Fellowship 2002–2003, Departamento de Ecología Funcional and Laboratorio de Bioacústica of the Instituto de Ecología and grants from the National Geographic Society and Scholarly Studies Fund of the Smithsonian Institution to RSG.

Appendix 1.

List of families by order collected in shade trees of a coffee plantation in Central Veracruz, Mexico. Unidentified families are listed as unknown and numbered consecutively within the order they belong to.

References

LITERATURE CITED

ARMBRUSTER, P., HUTCHINSON, R. A. & COTGREAVE, P. 2002. Factors influencing community structure in a South American tank bromeliad fauna. Oikos 96:225–234.CrossRefGoogle Scholar
BASSET, Y. & KITCHING, R. L. 1991. Species number, species abundance and body length of arboreal arthropods associated with an Australian rainforest tree. Ecological Entomology 16:391–402.CrossRefGoogle Scholar
BASSET, Y., SAMUELSON, G. A., ALLISON, A. & MILLER, S. E. 1996. How many species of host-specific insects feed on a species of tropical tree. Biological Journal of the Linnean Society 59:201–216.CrossRefGoogle Scholar
BASSET, Y., SPRINGATE, N. D., ABERLENC, H. P. & DELVARE, G. 1997. A review of methods for the sampling arthropods in the tree canopies. Pp. 27–52 in Stork, N. E., Adis, J. & Didham, R. K. (eds.). Canopy arthropods. Chapman & Hall, London.Google Scholar
BASSET, Y., NOVOTNY, V., MILLER, S. E. & KITCHING, R. L. 2003. Canopy entomology, and expanding field of natural science. Pp. 4–6 in Basset, Y., Novotny, V., Miller, S. E. & Kitching, R. L. (eds.) Arthropods of tropical forests. Cambridge University Press, Cambridge.Google Scholar
BENZING, D. H. 1990. Vascular epiphytes. Cambridge University Press, Cambridge. 354 pp.CrossRefGoogle Scholar
BENZING, D. H. 1994. How much is known about Bromeliaceae in 1994? Selbyana 15:1–7.Google Scholar
BOS, M. M., STEFFAN-DEWENTER, I. & TSCHARNTKE, T. 2007. The contribution of cacao agroforests to the conservation of lower canopy ant and beetle diversity in Indonesia. Biodiversity and Conservation 16:2429–2444.CrossRefGoogle Scholar
CHAN, L. M. 2003. Seasonality, microhabitat and cryptic variation in tropical salamander reproductive cycles. Biological Journal of the Linnean Society 78:489–496.CrossRefGoogle Scholar
CLARKE, K. R. 1993. Non-parametric multivariate analyses of changes in community structure. Australian Journal of Ecology 18:117–143.CrossRefGoogle Scholar
CLARKE, K. R. & GORLEY, R. N. 2001. Primer v5: user manual/tutorial. Primer-E Ltd. Plymouth. 91 pp.Google Scholar
COLWELL, R. K. & CODDINGTON, J. A. 1994. Estimating the extent of terrestrial biodiversity through extrapolation. Philosophical Transactions of the Royal Society of London, Series B 345:101–118.Google Scholar
COTGRAVE, P., HILL, M. J. & MIDDLETOWN, D. A. 1993. The relationship between body size and population size in bromeliad tank faunas. Biological Journal of the Linnean Society 49:367–380.CrossRefGoogle Scholar
CRUZ-ANGÓN, A. & GREENBERG, R. 2005. Are epiphytes important for birds in coffee plantations? An experimental assessment. Journal of Applied Ecology 42:150–159.CrossRefGoogle Scholar
CRUZ-ANGÓN, A., SILLETT, T. S. & GREENBERG, R. 2008. An experimental study of habitat selection by birds in a coffee plantation. Ecology 89:921–927.CrossRefGoogle Scholar
DAVIES, J. G., STORK, N. E., BRENDELL, M. J. D. & HINE, S. J. 1997. Beetle species diversity and faunal similarity in Venezuelan rainforest tree canopies. Pp. 85–103 in Stork, N. E., Adis, J. & Didham, R. K. (eds.). Canopy arthropods. Chapman & Hall, London.Google Scholar
DEJEAN, A., OLMSTED, I. & SNELLING, R. R. 1995. Tree-epiphyte-ants relationship in the low inundated forest of Sian Ka'an biosphere reserve, Quintana Roo, Mexico. Biotropica 27:57–70.CrossRefGoogle Scholar
DIAL, R. & ROUGHGARDEN, J. 1995. Experimental removal of insectivores from rain forest canopy: direct and indirect effects. Ecology 76:1821–1834.CrossRefGoogle Scholar
DUDLEY, R. 2000. The biomechanics of insect flight: form, function, evolution. Princeton University Press, Princeton. 476 pp.CrossRefGoogle Scholar
ELLWOOD, M. D. F., JONES, D. T. & FOSTER, W. A. 2002. Canopy ferns in lowland dipterocarp rainforest support a prolific abundance of ants, termites and other invertebrates. Biotropica 34:575–583.CrossRefGoogle Scholar
ERWIN, T. L. 1982. Tropical forests: their richness in Coleoptera and other arthropod species. The Coleopterists Bulletin 36:74–75.Google Scholar
ERWIN, T. L. 1983. Tropical forests canopies: the last biotic. Bulletin of the Entomological Society of America 11:14–19.CrossRefGoogle Scholar
ERWIN, T. L. 1991. How many species are there?: revisited. Conservation Biology 5:330–333.CrossRefGoogle Scholar
ERWIN, T. L. & SCOTT, J. C. 1980. Seasonal and size patterns, trophic structure, and richness of Coleoptera in the tropical arboreal ecosystem: the fauna of the tree Luehua seemannii (Triana and Planch) trees sampled in the canal zone of Panama. The Coleopterists Bulletin 34:305–322.Google Scholar
FLOREN, A. & LINSENMAIR, K. E. 1997. Diversity and recolonization dynamics of selected arthropod groups on different tree species in lowland rainforest in Sabah, Malaysia with special reference to Formicidae. Pp. 245–381 in Stork, N. E., Adis, J. & Didham, R. K. (eds.). Canopy arthropods. Chapman & Hall, London.Google Scholar
FLOREN, A. & LINSENMAIR, K. E. 1998. Non-equilibrium communities of Coleoptera in trees in a lowland rain forest of Borneo. Ecotropica 4:55–67.Google Scholar
GASTON, K. J. 1991. Estimates of the near-imponderable: a reply to Erwin. Conservation Biology 5:564–566.CrossRefGoogle Scholar
GASTON, K. J., BLACKBURN, T. M., HAMMOND, P. M. & STORK, N. E. 1993. Relationships between abundance and body size: where do tourists fit? Ecological Entomology 18:310–314.CrossRefGoogle Scholar
GENTRY, A. H. & DODSON, C. H. 1987. Diversity and biogeography of neotropical vascular epiphytes. Annals of the Missouri Botanical Garden 74:205–233.CrossRefGoogle Scholar
GOTELLI, N. J. & COLWELL, R. K. 2001. Quantifying biodiversity: procedures and pitfalls in measurement and comparison of species richness. Ecology Letters 4:379–391CrossRefGoogle Scholar
GREENBERG, R., BICHIER, P., CRUZ-ANGON, A., MACVEAN, C., PEREZ, R. & CANO, E. 2000. The impact of avian insectivory on arthropods and leaf damage in some Guatemalan coffee plantations. Ecology 81:1750–1755.CrossRefGoogle Scholar
HUXLEY, C. 1980. Symbiosis between ants and epiphytes. Biological Reviews 55:321–340.CrossRefGoogle Scholar
JANZEN, D. H. 1974. Epiphytic myrmecophytes in Sarawak: mutualism through the feeding of plants by ants. Biotropica 6:237–259.CrossRefGoogle Scholar
KITCHING, R. L., MITCHEL, H., MORSE, G. & THEBAUD, C. 1997. Determinants of species richness in assemblages of canopy arthropods in rainforest. Pp. 131–150 in Stork, N. E., Adis, J. & Didham, R. K. (eds.). Canopy arthropods. Chapman & Hall, London.Google Scholar
KRESS, W. J. 1986. The systematic distribution of vascular epiphytes: an update. Selbyana 9:2–22.Google Scholar
LONGINO, J. T. & NADKARNI, N. M. 1990. A comparison of ground and canopy leaf litter ants (Hymenoptera: Formicidae) in a Neotropical montane forest. Psyche 97:81–93.CrossRefGoogle Scholar
LUCKY, A., ERWIN, T. L. & WITMAN, J. D. 2002. Temporal and spatial diversity and the distribution of arboreal Carabidae (Coleoptera) in a Western Amazonian rain forest. Biotropica 34:376–386.CrossRefGoogle Scholar
MAJER, J. D. & DELABIE, J. H. C. 1993. An evaluation of Brazilian cocoa farm ants as potential biological control. Journal of Plant Protection in the Tropics 10:43–49.Google Scholar
MAY, R. M. 1978. The dynamics and diversity of insect faunas. Pp. 188–204 in Mound, L. A. & Waloff, N. (eds.). Diversity of insect faunas. Blackwell Scientific, Oxford.Google Scholar
MOGUEL, P. & TOLEDO, V. M. 1999. Biodiversity conservation in traditional coffee systems in Mexico. Conservation Biology 13:1–12.CrossRefGoogle Scholar
MORSE, D. R., STORK, N. E. & LAWTON, J. H. 1988. Species number, species abundance and body length relationships of arboreal beetles in Bornean lowland rain forest trees. Ecological Entomology 13:25–37.CrossRefGoogle Scholar
NADKARNI, N. M. 1994. Diversity of species and interactions in the upper tree canopy of forest ecosystems. American Zoologist 34:70–78.CrossRefGoogle Scholar
NADKARNI, N. M. & MATELSON, T. J. 1989. Bird use of epiphyte resources in Neotropical trees. Condor 91:891–907.CrossRefGoogle Scholar
NOVOTNÝ, V. & BASSET, Y. 2000. Rare species in communities of tropical insect herbivores: pondering the mystery of singletons. Oikos 89:564–572.CrossRefGoogle Scholar
ØDEGAARD, F. 2000. The relative importance of trees versus lianas as hosts for phytophagous beetles (Coleoptera) in tropical forests. Journal of Biogeography 27:283–296.CrossRefGoogle Scholar
PAOLETTI, M. G., TAYLOR, R. A. J., STINNER, D. H., STINNER, B. R. & BENZING, D. H. 1991. Diversity of soil fauna in the canopy and forest floor of Venezuelan cloud forest. Journal of Tropical Ecology 7:373–383.CrossRefGoogle Scholar
PERFECTO, I., VANDERMEER, J., HANSON, P. & CARTÍN, V. 1997. Arthropod biodiversity loss and the transformation of a tropical agro-ecosystem. Biodiversity and Conservation 6:935–945.CrossRefGoogle Scholar
RABOY, B. E., CHRISTMAN, M. C. & DIETZ, J. M. 2004. The use of degraded and shade cocoa forest by endangered golden-headed lion tamarins Leontopithecus chrysomelas. Oryx 138:75–83.Google Scholar
RICHARDSON, B. A. 1999. The bromeliad microcosm and the assessment of faunal diversity in a Neotropical forest. Biotropica 31:321–336.CrossRefGoogle Scholar
RICHARDSON, B. J., BURGIN, S., AZARBAYJANI, F. F. & LUTUBULA, S. 1997. Distinguishing the woods from the trees. Pp. 497–509 in Stork, N. E., Adis, J. & Didham, R. K. (eds.). Canopy arthropods. Chapman & Hall, London.Google Scholar
RICHARDSON, B. A., RICHARDSON, M. J, SCATENA, F. N. & MCDOWELL, W. H. 2000. Effects of nutrient availability and other elevational changes on bromeliad populations and their invertebrate communities in a humid tropical forest in Puerto Rico. Journal of Tropical Ecology 16:167–188.CrossRefGoogle Scholar
ROMERO-ALVARADO, Y., SOTO-PINTO, L., GARCÍA-BARRIOS, L. E. & BARRERA-GAYTAN, J. K. 2002. Coffee yields and soil nutrients under the shades of Inga sp. vs. multiple species in Chiapas México. Agroforestry Systems 54:215–224.CrossRefGoogle Scholar
ROSKOSKI, J. P. 1981. Nodulation and nitrogen fixation by Inga jinicuil, a woody legume in coffee plantations. I. Measurements of nodule biomass and field acetylene reduction rates. Plant Soil 59:201–206.CrossRefGoogle Scholar
ROSKOSKI, J. P. 1982. Nitrogen fixation in a Mexican coffee plantation (Inga jinicuil). Plant and Soil 67:283–291.CrossRefGoogle Scholar
RUSEK, J. 1998. Biodiversity of Collembola and their functional role in the ecosystem. Biodiversity and Conservation 7:1207–1219.CrossRefGoogle Scholar
SAHAI, H. & AGEEL, M. I. 2000. The Analysis of Variance: fixed random and mixed models. Birkhäuser, Boston. 742 pp.CrossRefGoogle Scholar
SANTOYO-CORTÉS, V. H., DÍAZ-CÁRDENAS, S. & RODRÍGUEZ-PADRÓN, B. 1994. Sistema agroindustrial café en México. Universidad Autónoma Chapingo, México. 176 pp.Google Scholar
SCHMIDT, G. & ZOTZ, G. 2000. Herbivory in the epiphyte, Vriesea sanguinolenta Cogn. & Marchal (Bromeliaceae). Journal of Tropical Ecology 16:829–839.CrossRefGoogle Scholar
SILLETT, T. S. 1996. Foraging ecology of epiphyte-searching insectivorous birds in Costa Rica. Condor 96:866–877.Google Scholar
STORK, N. E. 1987. Arthropod faunal similarity of Bornean rain forest trees. Ecological Entomology 12:219–226.CrossRefGoogle Scholar
STORK, N. E. 1991. The composition of the arthropod fauna of Bornean lowland forest trees. Journal of Tropical Ecology 7:161–180.CrossRefGoogle Scholar
STORK, N. E. & BLACKBURN, T. M. 1993. Abundance, body size and biomass of arthropods in tropical forest. Oikos 67: 487–489.CrossRefGoogle Scholar
STORK, N. E. & HAMMOND, P. M. 1997. Sampling arthropods from tree-crowns by fogging with knockdown insecticides: lessons from studies of oak tree beetle assemblages in Richmond Park (UK). Pp. 3–26 in Stork, N. E., Adis, J. & Didham, R. K. (eds.). Canopy arthropods. Chapman & Hall, London.Google Scholar
STUNTZ, S. 2001. The influence of epiphytes on arthropods in the tropical forest canopy. PhD Dissertation. Würzburg University, Germany. 111 pp.Google Scholar
STUNTZ, S., ZIEGLER, C., SIMON, U. & STOTZ, G. 2002a. Rainforest air-conditioning: the moderating influence of epiphytes on the microclimate in tropical tree crowns. International Journal of Biometeorology 46:53–59.CrossRefGoogle ScholarPubMed
STUNTZ, S., ZIEGLER, C., SIMON, U. & STOTZ, G. 2002b. Diversity and structure of the arthropod fauna within three canopy epiphyte species in Central Panama. Journal of Tropical Ecology 18:161–176.CrossRefGoogle Scholar
STUNTZ, S., SIMON, U. & ZOTZ, G. 2003. Arthropods seasonality in tree crowns with different epiphyte loads. Pp. 176–185 in Basset, Y., Novotny, V., Miller, S. E. & Kitching, R. L. (eds.). Arthropods of tropical forests. Cambridge University Press, Cambridge.Google Scholar
THOMPSON, J. N. 1981. Reversed animal-plan interactions: the evolution of insectivorous and ant-fed plants. Biological Journal of the Linnean Society 16:147–155.CrossRefGoogle Scholar
WILKENS, R. T., VANDERKLEIN, D. W. & LEMKE, R. W. 2005. Plant architecture and leaf damage in bear oak: insect usage patterns. Northeastern Naturalist 12:153–168.CrossRefGoogle Scholar
WITTMAN, P. K. 2000. The animal community associated with canopy bromeliads of the lowland Peruvian Amazon rain forest. Selbyana 21:48–51.Google Scholar
YANOVIAK, S. P., NADKARNI, N. M. & GERING, J. 2003. Arthropods in epiphytes: a diversity component that is not effectively sampled by canopy fogging. Biodiversity and Conservation 12:731–741.CrossRefGoogle Scholar
YANOVIAK, S. P., NADKARNI, N. M. & SOLANO, J. R. 2006. Arthropod assemblages in epiphyte mats of Costa Rican cloud forests. Biotropica 36:202–210.Google Scholar
ZAR, J. H. 1999. Biostatistical analysis. Prentice Hall, Inc. Upper Saddle River. 662 pp.Google Scholar
Figure 0

Figure 1. Trap setting for a knockdown insecticide fogging of an Inga jinicuil tree with epiphytes in a coffee plantation, Coatepec, Veracruz, Mexico. Inga jinicuil trees experimentally depleted of epiphytes were also fogged and insects collected.

Figure 1

Table 1. Number of insect morphospecies by order or suborder and number of families (in parentheses) captured during the canopy fogging of 12 Inga jinicuil trees in an experimental setting in a shade coffee plantation where six trees (three per plot) had epiphytes removed while the other six trees remain with epiphytes, in Coatepec, Veracruz, Mexico. Sites: North, South, Treatments: E+ = with epiphytes, E− = without epiphytes. Total columns show total number of families and species per site. Expected number of species was obtained using Chao 1 estimator. Completeness represents the percentage of observed versus estimated species richness. Within dissimilarity represents the mean percentage dissimilarity between samples within plots. In bold are the groups that showed a consistent pattern of higher diversity in E+ plots.

Figure 2

Figure 2. Mean species accumulation curves for insect species collected by knockdown fogging of three trees per plot (two samples per tree) in an experimental setting in a coffee plantation in Central Veracruz, Mexico. Experimental plots: North with epiphytes (♦), North without epiphytes (□), South with epiphytes (▲), and South without epiphytes (○). Error bars represent 95% Confidence Intervals.

Figure 3

Figure 3. Mean expected number of insect species by experimental plot in a coffee plantation in Central Veracruz, Mexico. Mean expected number of species were based on Chao 1 estimator form the 100 iterations. Experimental plots: NE+ = North with epiphytes, NE− = North without epiphytes, SE+ = South with epiphytes, SE− = South without epiphytes. Error bars represent 95% confidence intervals.

Figure 4

Table 2. Results from two-way crossed ANOSIM test, based on Bray–Curtis dissimilarities in fourth-root-transformed insect abundances from four experimental plots in a coffee plantation, Central Veracruz, Mexico. Pairwise ANOSIM tests for differences between plots. Experimental plots: NE+ = North with epiphytes, NE− = North without epiphytes, SE+ = South with epiphytes, SE− = South without epiphytes.

Figure 5

Figure 4. Ordination of two matched pairs of experimental plots, based on a multidimensional scaling analysis used to compare the similarities of the studied plots (Stress = 0.17). Experiment consisted in removing epiphytes from all trees in one of two plots in two sites. Two samples per trees, three trees per site were fogged and insects were collected. Experimental Plots: North with epiphytes (♦), North without epiphytes (□), South with epiphytes (▲), and South without epiphytes (○). Stress = 0.16.

Figure 6

Appendix 1. List of families by order collected in shade trees of a coffee plantation in Central Veracruz, Mexico. Unidentified families are listed as unknown and numbered consecutively within the order they belong to.