Legacy patterns in the abundance of epigaeic mountain beetles after the eruption of the Puyehue-Cordón Caulle volcanic complex ( NW Patagonia , Argentina )

Organisms that survive a volcanic eruption are part of the biological legacies that are fundamental to subsequent succession and ecosystem development. In January 2012, the summer immediately after the eruption of the Puyehue-Cordón Caulle volcanic complex, we evaluated the short-term response of epigaeic beetle abundance to ash deposition. We focused on three mountains (La Mona, Bayo, Challhuaco) in northwestern Patagonia (Argentina) that were differentially affected by ash deposition. We re-established 32, 100 m2 sampling plots of nine pitfall traps, every 100 m of altitude from the base to the summit of each peak, which we had previously sampled in January 2005 and 2006. We compared the shape of preand posteruptive abundance-elevation relationship (AER), and assessed whether the relative importance of environmental predictors of AER (ambient energy, vegetation cover, plant species richness and soil attributes) changed after the eruption. La Mona and Bayo were most affected by ash deposition; Challhuaco was considerable less affected. Yearly fluctuations in abundance levels were significant in Bayo; here, the shape of AER changed significantly after the eruption. In La Mona, abundance was similar among sampled years, and the shape of AER departed weakly from the overall trend after the eruption. In Challhuaco, abundance tended to increase weakly with time, and the shape of AER did not change after the eruption. Gravel percentage and tree canopy cover were the two most important predictors of pre-eruptive AER, but only tree canopy cover remained as important after the eruption. We conclude that short-term effects of ash deposition on epigaeic mountain beetles were subtle and suggest that the presence of a gradient of ash deposition may lead to associated patterns in biological legacies. Long-term monitoring is essential to fully understand the structural and functional recovery of these mountain ecosystems. [


INTRODUCTION
Volcanic activity is a powerful driver of environmental change at multiple geographical and temporal scales (Simkin 1993).Although, from a human-lifetime perspective, volcanic eruptions may appear as rather infrequent events they actually are not so rare at global or regional scale (Simkin 1993), and whenever they occur they can

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Ecología  modify entire landscapes through a diversity of geophysical disturbances, including the precipitation of volcanic ash or tephra that may blanket extensive areas (e.g., Mount St Helens, >100000 ha: Dale et al. 2005; Puyehue-Cordón Caulle, > 23 million hectares: Gaitán et al. 2011).The precipitation of volcanic ash is susceptible to be translated into an ecological response (Turner et al. 1997;Dale et al. 2005;Kitzberger 2013).However, the ecological response may vary considerably among different environments, and the natural capacity of organisms to tolerate (or not) ash deposition (Dale et al. 2005).
Organisms that survive a volcanic catastrophe (e.g., animals, plants, fungal, microbial) have been increasingly recognized as biological legacies that are fundamental to the ecological response, as they can have significant influences on the path and rates of subsequent succession and ecosystem redevelopment (Franklin 1990;Franklin et al. 2000;Dale et al. 2005).It has been suggested that the level of biological legacies (i.e., the number and kind of surviving organisms and levels of organic debris) is the most important variable influencing ecosystem recovery (Franklin 1990), and several examples suggest they indeed played a significant role in the restoration of plant and animal communities after severe volcanic eruptions (e.g., Mount St. Helens: Dale et al. 2005;Kasatochi Island: Talbot et al. 2010).The presence of a continuum of disturbance intensities may lead to similar gradients in biological legacies (Franklin 1990).
However, legacy patterns may be not so easy to quantify because of the relative unpredictable nature of volcanic activity coupled with the rather infrequent availability of data from pre-disturbance communities.
The goal of the present study was to quantify legacy patterns in the abundance of epigaeic mountain beetles using three mountains differentially affected by the eruption of the Puyehue-Cordón Caulle volcanic complex, and where detailed analyses of preeruptive abundance patterns were available (Werenkraut 2010;Werenkraut & Ruggiero 2014).We compared the post-and pre-eruptive abundance-elevation relationship (AER) along a gradient of ash deposition.Ash deposition is known to produce lethal effects on many insect species and to significantly decline arthropod populations (Wille & Fuentes 1975;Marske et al. 2007;Buteler et al. 2011).In pre-eruptive conditions, AER predominantly followed a hump-shaped pattern within our study area.Also, the abundance of epigaeic beetles increased with tree canopy cover and herb cover, and decreased with the increase in litter accumulation and proportion of gravel (Werenkraut 2010;Werenkraut & Ruggiero 2014).We evaluated whether 1) the shape of AER in the summer immediately after the eruption differed from pre-eruptive reports, and 2) the relative importance of different environmental predictors of abundance variation (temperature at ground level, vegetation and soil attributes) was modified after the eruption.The short-term response of epigaeic beetles to ash fall may result in legacy patterns that can be considered as useful baseline for future long-term monitoring of ecosystem development and recovery.

Study Area
The study was conducted in north-western Patagonia (41.08° S, 71.02° W, Figure 1) within the Nahuel Huapi National Park (Argentina).The region is characterized by an average temperature <18 °C during the summer season, and during winter, it is <4 °C (Rudloff 1981).More than 70% of the annual precipitation is concentrated during fall and winter (Jobbágy et al. 1995); mean annual precipitation strongly decreases along a west-east gradient from more than 3000 mm to ~300 mm (Barros et al. 1983).Subantarctic forests dominate the landscapes towards the west, and the Patagonian steppes are found towards the east (Paruelo et al. 1998)

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Abril de 2014 biogeographical transition occurs with altitude and, at about 1600 m.a.s.l., it is the transition from the Subantarctic forests and shrublands of semi-arid scrub vegetation that grow downslope to the highaltitude Andean steppes composed of xerophytic shrubs and herbs that often present adaptations to cold and windy conditions (Ferreyra et al. 1998).
The study area is within the Southern Volcanic Zone, a region of high current volcanic activity that begins just south of the Aconcagua massif and extends along the Andes for 1400 km up to Hudson volcano in southern Chile (Clapperton 1993).In northern Patagonia, the Nahuel Huapi area has been affected by several explosive pulses of the Puyehue-Cordón Caulle volcanic complex during the last 10000 years (Villarosa et al. 2006).The last eruption, started on June 4 th 2011, which sent out 950 million tons of ash, sand and pumice stone that covered more than 23 million of hectares over the Neuquén and Río Negro Provinces in Argentina (Gaitán et al. 2011; daily reports available at http: //www.sernageomin.cl. We selected three mountains situated at different locations along the west-east transition (Figure 1) that were differentially affected by ash deposition: 1) La Mona (40.34° S, 71.42° W, annual precipitation: 1950 pmm) and 2) Bayo (40.45° S, 71.36° W, 1650 pmm) are about 40-50 km apart from the eruption, and 3) Challhuaco is about 120 km apart (41.13° S, 71.19° W, 1100 pmm); according to Gaitan et al. (2011) ash deposition in La Mona and Bayo respectively reached 7.5-10 and 10-15 cm, whereas in Challhuaco total ash deposition was less than 2 cm.

Beetle sampling
A suitable field comparative design to infer a causal effect of ash fall on the abundance of beetles would require to fully control for both the temporal change (before-after) in the studied system and spatial impact (control-impact) of the ash fall (Hulbert 1984); actually, sampling multiple impacted and control sites, before and after a disturbance (BACI sampling design), has been recommended as an optimal design for environmental impact assessment (e.g., Underwood 1992).Although we relied on pre-eruptive (January 2005(January -2006) ) abundance data for the three mountains studied, we lack pre-eruptive data from a mountain not affected by ash deposition.The impossibility of having before-after data for a control mountain represented a drawback of our study; however, it was minimized by the location of the three studied mountains along a gradient of ash deposition.This feature in the design of our study makes it to approach a before-after gradient (BAG) sampling design that has been considered as a powerful alternative to BACI design for environmental impact assessment (Elis & Schneider 1997).
We used GPS to find the exact location of the 32 sampling plots that had been previously sampled in 2005-2006 and thus, 9-12 plots were re-established at about 100 m of altitude away from each other, from the base to the top of each mountain.We collected beetles using 288 plastic pitfall traps (diameter, 9 cm; depth, 12 cm), arranged in thirtytwo 100-m 2 grid plots of nine traps.Traps were filled with diluted propylene glycol (40%) and a drop of soap.Pitfall traps were operative as soon as established in the field and were opened over 7 days during January 2012.We pooled the contents from the nine pitfalls to one sample for each plot.All samples were preserved in 80% ethyl alcohol.All the collected material was carried to Ecotono Laboratory, Universidad Nacional del Comahue, Bariloche, Argentina to complete the individuals count.
The abundance of individuals was the total number of individuals caught at each plot; "abundance" should be interpreted with caution here because pitfall trapping allows suitable estimations of relative activity-density rather than absolute abundance (Baars 1979).Nonetheless, our sampling effort (= 9 pitfall traps per sampling plot with seven days of activation during each sampling period) approaches Cheli & Corley's (2010) recommendation of using five traps per experimental unit with ten days of activation, to obtain reliable measures of species richness in the most extreme arid Patagonian steppes.Hence, we are confident that our estimations reflect a reliable picture of the epigaeic beetle community structure and thus they are valid to compare pre-and posteruptive spatial patterns.

Ash deposition
At each plot, we dug a plastic test-tube (5 cm diameter and 35 cm height) into the ground to carefully remove a core from the soil whereby to measure the height of ash deposition in cm.

Environmental variables
During January 2012, we measured a total of 19 environmental variables on each sampling plot, that were known to be associated with the spatial variation in abundance at pre-eruptive times, as reported in Werenkraut (2010), and Werenkraut & Ruggiero (2014).These previous works should be consulted for details of the field measurements and lab protocols.Here, we mention that we measured variables representing 1) ambient energy, 2) vegetation, and 3) soils, as follows: Ambient energy: we mounted one HOBO H8 logger (Onset Computer Corporation, Bourne, MA, USA) on a pole fixed at the centre of each 10 x 10 m sampling plot to measure minimum daily temperature (TMIN), and daily temperature range (TVAR) at ground level from data recorded every 2 h during the week that pitfall traps were active.Differences in sun exposure between slopes at these temperate latitudes were represented by a qualitative variable (SUN=N>NW>NE>W>E>SW>SE>S).
Vegetation: we sampled the vegetation in each of the 10x10-m sampling plots and classified all plants

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Ecología Austral 24:31-41 recorded according to their growth forms: i) herbs, ii) shrubs, and iii) trees, as proposed by Ezcurra & Brion (2005).We counted the total number of species of herbs (HERBSP), shrubs (SHRUBSP) and trees (TREESP) recorded on each sampling plot to estimate species richness.We made four readings of canopy cover using a spherical densitometer facing each of the four cardinal directions, and averaged the cover values to estimate an overall estimation of tree canopy cover for each plot (TREECOV).The proportion of each sampling plot covered by shrubs (SHRUBCOV) was estimated visually.We estimated the herb cover for each 10×10-m plot by haphazardly throwing four times a 0.50×0.50-mwooden frame subdivided into a 25-celled nylon string grid.In each placement, we estimated the proportion of cells covered by herbs.We averaged these four values to estimate herbaceous cover (HERBCOV).We removed as much litter as was necessary to dig in the pitfall trap to obtain equivalent samples of litter biomass at each plot.Samples were stored in paper bags, oven-dried to constant mass at 60 °C and weighed to estimate dry litter biomass (LITTER).

Soil characteristics:
for each plot-sample, we extracted samples from the top 10-cm of soil at three randomly selected points to determine water pH (PHH2O; potentiometric determination, Thomas 1996), volcanic pH (PHVOLC), which is a likely indicator of volcanic influence in soil formation (potentiometric determination, Blakemore et al. 1987 a,b), proportion of silt, sand, and clay (SILT, SAND and CLAY) (Klute 1986), proportion of organic matter (OM) (Pipette Method, Klute 1986) and soil humidity (HUM=[(wet weightdry weight)/wet weight]x100).We haphazardly extracted three additional samples from each plot using a cylinder of known volume (96.21 cm 3 ).These samples were dried at 105 °C for 24 h and sieved to 2 mm.From particles less than 2 mm, we determined bulk density (BULDEN)=dry weight/ cylinder volume.Higher values of BULDEN are related to more compacted soils.From samples with larger particles, we estimated the proportion of gravel (GRAVEL=gravel weight/total weight).We averaged BULDEN and GRAVEL estimations over the three samples.

Analyses of data
The shape of the AER relationship: we used the mgcv package in R (Wood 2001; R Development Core Team 2011) to fit a generalized additive model (GAM) to the AER data to test for significant differences in the mean abundance of beetles caught among years, and to test whether a smoother function of elevation accounted for a significant proportion of the shape of the AER in each site, using the data from the three sampling periods (January 2005(January , 2006(January and 2012)).
where Log 10 (Abundance i ) was the number of individuals (log-transformed) modeled as a smoothing function (f) of "elevation" and "year", being a nominal variable with three levels (January 2005, January 2006 and January 2012); we log-transformed abundance data to satisfy the assumptions of a normal distribution (N) of errors (εi) with mean zero (0) and variance (σ2) (Zuur et al. 2009).In a second run, we required the interaction term between "elevation" and "year 2012 " to test whether the shape of AER changed after the eruption (January 2012).
The interaction term in a GAM is different from one in linear regression, and it allows testing the deviation of AER in January 2012 (AER 2012 ) smoother from an overall smoother fit on all data points (= overall elevation effects on all years).If AER 2012 is significant it means that the shape of the AER changed after the eruption.The command gam.check in the mcgv package was used to assess normality, homogeneity and model fit, using logtransformed abundance data (Zuur et al. 2009).
The association of abundance with environmental factors: we used a multi-model selection approach of inference and the modelaveraging procedure implemented in the glmulti package (Calcagno & Mazancourt 2010) to estimate the relative importance of each predictor variable to account for mean abundance variation by using the Akaike weight (wi), which measures the relative likelihood of a model to be the best given a dataset; the importance of a given variable arose from the sum of the w i of all the models in which the variable participated (Burnham & Anderson 2002).We classified the environmental variables into groups to represent ambient energy, vegetation cover, plant species richness, physical composition of soils, and chemical properties and organic matter of soils.We first generated multiple models that included all possible combinations of the given "m" explanatory variables in each environmental group.Then, we generated a composite model that combined the most single important variable in each environmental group, and compare their relative importance to account for abundance variation between pre-and post-eruptive conditions.For January 2012, the composite model also included the effect of ash.

Ash deposition and AER patterns
We confirmed that La Mona and Bayo were the two altitudinal gradients most affected by the ash deposition (Figure 2); the highest level of ash deposition (>10 cm between 900-1600

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Abril de 2014 m.a.s.l.) was found in Bayo, followed by La Mona with ~8 cm between 800-1600 m.a.s.l., and considerably lower levels of ash deposition (≤2cm) were recorded in Challhuaco (Figure 2).Thus, our measurements of ash deposition at local scale, on 32 field sampling plots, were in agreement with those of Gaitán et al (2011).
We collected a total of 6483 individuals of beetles in January 2012, which exceeded the total number of individuals collected in January 2005 (4569 individuals) and 2006 (4285 individuals).The GAM applied to the AER data adequately described the elevational variation in abundance (Table 1a, Figure 3).This analysis revealed yearly fluctuations in the level of abundance, mostly in Bayo (Table 1a, Figure 3).Here, there was a significant effect of time (year) on the mean number of individuals caught (Table 1a); actually, the mean number of individuals caught per plot (n) decreased from n=180 in 2005 to n=30.4 in 2006, and then, in January 2012, it increased to a similar level to those recorded in 2005 (n=180.4).In La Mona, the mean abundance of individuals caught did not differ significantly across years, and in Challhuaco there was a tendency for the abundance of individuals caught to increase with time, although the overall effect of time was marginally significant (Table 1a).
The shape of the AER was accounted significantly by the smoother function fit to the abundance data (Table 1a).In January 2012, the shape of the AER in Bayo departed significantly from the overall trend; in La Mona there was a weaker tendency for the shape of AER to be different from the overall trend (P=0.09), and the shape of AER in Challhuaco did not change after the eruption (Table 1b, Figure 3).

Environmental factors associated with beetles' abundance at pre-and post-eruptive conditions
In January 2012, there was a significant decrease in above ground plant cover and plant species richness on our sampling plots, mainly in HERBSP, HERBCOV, SHRUBCOV and LITTER (Table 2).We often found that

DISCUSION
We confirmed that epigaeic mountain beetles are one important component of the biological legacy after the eruption of the Puyehue-Cordón Caulle volcanic complex.The high number of beetles captured during the first summer immediately after the eruption suggests that a great number of species were able to survive within our study area, thus maintaining (in La Mona) or rather increasing (in Bayo and Challuaco) the number of individuals caught after the eruption.This suggests that, at least in La Mona, Bayo and Challhuaco, total abundance of epigaeic beetles seems not to have been seriously affected by ash deposition; however, the shape of the AER did suggest a differential

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Ecología Austral 24:31-41 ecological response along the gradient of ash deposition.The shape of the AER changed significantly after the eruption in Bayo where ash deposition was higher; in La Mona, ash deposition was comparatively lower and there was a weak tendency for the shape of AER to change.In Challhuaco, there were the lowest levels of ash deposition and no alteration of AER shape after the eruption.These findings support the idea that the presence of a continuum of disturbance intensities (i.e., here, in the level of ash deposition) may lead to associated patterns in biological legacies (Franklin 1990).
The abundance levels we observed shortly after the eruption could be associated with the seasonal timing of the eruption, which is often important to account for different post-eruptive landscapes (Foster et al. 1998).The eruption of the Puyehue -Cordón Caulle volcanic complex on June 4 th , occurred in late autumn, a few weeks before the beginning of the austral winter; it is possible that many beetle species were already in a dormant stage (i.e., pupae) tucked away in soil, or within the tissues of plants and so were not exposed at the time of eruption.In temperate climates, the pupa is often the best equipped insect stage to carry the individual beetle through the winter, until day length, temperatures and moisture in spring and summer become appropriate for adult beetles to emerge (Evans & Bellamy 2000;Topp 1994).
After the eruption of Mt.Saint Helens in May 1980, the selective death of organisms in the areas subjected only to tephra deposition left the structure and function of the affected ecosystems relatively intact (Foster et al. 1998).This was explained by the fact that by the time of the eruption, the mountain was covered with snow, and the presence of snow packs might had cushioned the blow, resulting in that a few months later, in late summer, almost the entire ecosystems showed evidence of resilience (del Moral 1981).Although we could not confirm the presence and extent of snow on our sampling plots by the time of eruption, we think that small shrubs that remained alive under the ash (e.g., Gaultheria spp.) were also part of the biological legacy that might have also favored the survival of beetles.We speculate that they possible might have acted as refuges for some insect species after they emerged from dormant stages, providing food for herbivores and suitable micro-habitats within the intricate structure of their branches.
The tendency for ash deposition to increase soil humidity could be another factor favoring beetle survival; in general, the higher the layer of ash deposited, the higher the water content we estimated at each sampling plot, (b=0.79,P<0.0001, R 2 =0.64).This may be associated with a short term mulching action associated with ash that could increase soil water retention through lowering soil temperatures and decreasing direct evaporation from soil (Black & Mack 1986).Probably because of the high ambient humidity typical of winter conditions at these temperate latitudes the ash deposited became quickly saturated and this may have protected insects from dehydration.This may explain why although laboratory assays suggested that Puyehue-Cordón Caulle volcanic ash could act as insecticide killing insects by dehydration (Buteler et al. 2011), we did not find evidence to suggest this effect on native beetles in their natural habitats.However, in the long term, ash deposition could result in other effects (e.

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Abril de 2014 hence long-term research is indispensable to fully understand the consequences of ash deposition on water dynamics that may potentially affect beetle abundances.
We confirmed that the association of the abundance of epigaeic beetles with environmental factors changed in the summer immediately after the eruption, although tree canopy cover continued to be an important variable.In general, the abundance of beetles increased as the tree canopy cover increased.However, the increase in tree canopy cover measured after the eruption should not be necessarily interpreted as an increase in primary production; in January 2012, our densitometer measurements could have been affected by the ash accumulation that pressed the tree branches out of their natural shape thus increasing shadow.The strong positive association of beetle abundance with canopy cover before and after the eruption can reflect the greater diversity and abundance of epigaeic beetles within the forests (as compared to the steppes) but it may also be associated with local effects within the forests, given that canopy cover can influence directly the availability of microhabitats at the ground level (e.g., Coleoptera: Niemelä et al. 1996).
Before the eruption, the abundance of beetles decreased with the increase in gravel percentage, and this factor appeared as the most important to account for their abundance.However, although we recorded no significant changes in the percentage of gravel after the eruption, we observed that gravel percentage was not important for AER in the summer immediately after the eruption (Table 2).Given that many coleopteran immature stages live underground, it would be interesting to follow more in depth, the course and possible alterations of this association to fully understand whether it may show a long term impact on beetle abundance.
Temperature at ground level was of relatively high importance to account for abundance patterns.The fact that minimum daily temperature was important at pre-eruptive times whereas daily temperature range was more important to account for post-eruptive patterns should not be overemphasized given that pre-eruptive temperature data was obtained from longer time series (i.e., dataloggers were established in the field for more than 150 days) than in the post-eruptive sampling period (one week).The remaining variables representing soil attributes and ash deposition were less important.Long term studies are needed to determine the extent to which abundance-environment associations observed in the summer immediately after the eruption are sustained.
The short-term effect of ash deposition on insect populations could have been selective within our study region, leading to differences in mortality among taxa.For instance, ash deposition did seriously affect the abundance of the invasive yellow jackets (Vespula spp), as no wasps were caught where ash deposition levels exceeded 3 cm (Masciochi et al. 2013).Short-term response to ash deposition has been also observed in honeybees (Apis mellifera), through experiments that demonstrated that workers were unable to see the flowers covered by ash, with this meaning extra allocation of energy during nectar foraging (Martínez et al. 2013).Laboratory trials also showed the toxicity of volcanic ash from Puyehue -Cordón Caulle eruption on the native grasshopper Dichroplus vittigerum (Fernández-Arhex et al. 2013).It has been suggested that for non-native species that have evolved in regions with little or no exposition to volcanic activity the effects could be dramatic (Masciochi et al. 2013).
In summary, the AER patterns found for epigaiec mountain beetles in the first summer after the volcanic eruption conforms to the idea that short-term effects of ash deposition may be subtle and that ground dwelling beetle assemblages remain as a significant part of the biological legacy that probably will contribute to ecosystem development and recovery.However, ash deposition could differently affect different stages of development, and we do not know whether beetles that survived in the first summer after the eruption, were able to complete their life cycle or will be able to sustain their populations in the presence of ash.Therefore, a long-term monitoring programme is warranted.This should evaluate the quantitative and qualitative changes in species richness and taxonomic composition in the beetle assemblage that could be associated with long term effects of ash deposition, and modification of other components of the biotic (e.g., the potential effect of removing the exotic Vespula spp on the reassembly of native fauna) and abiotic environments that could be crucial aspects to understand the structural and functional recovery of these mountain ecosystems.

Figura 4 .
Figure 4. Environmental changes observed after the Puyehue-Cordón Caulle eruption.The pictures were taken at one of the sampling plots (Bayo, 1300 m) from about the same standing position to be able to show differences between the environmental conditions before the eruption in 2005 (top) and after the eruption (down).Note that the shrubs in the understory shown in the top figure are buried under the ash in the bottom figure.Figura 4. Cambios ambientales observados luego de la erupción del complejo volcánico Puyehue-Cordón Caulle.Las fotos fueron tomadas en uno de los sitios de muestreo (Bayo, 1300 m) desde aproximadamente la misma posición para poder mostrar las diferencias en las condiciones ambientales entre antes de la erupción en 2005 (arriba) y después de la erupción (abajo).Nótese que los arbustos del sotobosque en la foto superior están enterrados debajo de la ceniza en la foto inferior.

Figure 5 .
Figure5.Ranking of importance of environmental factors that best accounted for the spatial variation in abundance at (a) pre-and (b) post-eruptive conditions, after the application of model averaging procedure (see main text for explanation).Figura 5. Orden de importancia de los factores ambientales que mejor explicaron la variación espacial en la abundancia en condiciones (a) pre-y (b) post-eruptivas, luego de la aplicación del promediado de modelos (ver texto principal para una explicación).

Table 1 .
GAMs model fit to AER data to: a) test for differences in the levels of Log 10 (abundance) and shape of the AER on three altitudinal gradients (Bayo, La Mona and Challhuaco) (model without interaction).

Table 2 .
Overall environmental changes observed on the three mountains studied.