Global Vision International
2010 Report Series No. 001
GVI Ecuador
Rainforest Conservation and Community
Development
Phase Report 101 Friday 8th January – Friday 19th March
GVI Ecuador/Rainforest Conservation and Community Development Expedition Report 101
` Submitted in whole to
Global Vision International Yachana Foundation
Museo Ecuatoriano de Ciencias Naturales (MECN)
Produced by Chris Beirne – Field Manager Oliver Burdikin – Field Staff Simon Mitchell –Field Staff
and
Craig Herbert Scholar Katherine Parker Volunteer
Jill Robinson Scholar Skylar Senti Volunteer
Jasmine Rowe Scholar Rachel Smith Volunteer
Laura Jones Intern Hugo Sykes Volunteer
Thomas Smith Intern Amelia Wheeler Volunteer
Rachel Adler Volunteer Roberth Alvarado High school student
Bianca Amato Volunteer Christian Andi High school student
Stef DuFresne Volunteer Javier Andy High school student
Anna Flanagan Volunteer Marianna Conforme High school student
Alistair Gorden Volunteer Richard Dahua High school student
James Mallard Volunteer Abel Kunchicuy High school student
Benny Mansfield Volunteer Christian Vega High school student
Robert McCann Volunteer Mauricio Andi High school graduate
Valerie Mills Volunteer
Prashant Mistry Volunteer
Edited by
Karina Berg – Country Director
GVI Ecuador/Rainforest Conservation and Community Development Address: Casilla Postal 17-07-8832
Quito, Ecuador Email: [email protected]
Web page: http://www.gvi.co.uk and http://www.gviusa.com
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Executive Summary
This report documents the work of Global Vision International’s (GVI) Rainforest
Conservation and Community Development Expedition in Ecuador’s Amazon region
and run in partnership with the Yachana Foundation, based at the Yachana Reserve in
the province of Napo. During the first phase of 2010 from Friday 8th January to Friday
19th March, GVI has:
• Added three new species to the reserve list; Ornate Hawk-eagle (Spizaetus
ornatus), Hog-nosed Pitviper (Bothrops hyoprora), and the Neotropical marbled
Frog (Hyla maromaratus).
• Continued assesseing the effect of habitat change in understory bird communities.
• Continued to collect data on the effect of structural habitat change on the
amphibian and reptile communities, using pitfall trapping and visual encounter surveys.
• Continued with a project investigating the effects of disturbance from the road upon
butterfly communities.
• Continued to sample dung beetles within different habitats around the reserve.
• Continued with English lessons for local school children in Puerto Rico twice a
week.
• Continued giving English classes at Puerto Salazar whenever possible.
• Welcomed four pasantias (work experience students) from the Yachana Technical
High School to join the expedition, in order to exchange language skills, knowledge and
experience.
• Visited Yasuní National Park and Sumak Allpa, an island reserve and school run by
a local conservationist.
• Continued helping the local organisation Amanecer Campisino with their projects in
the local region.
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Contents
List of Figures ................................................................................................................. 5
1 Introduction ................................................................................................................ 6
2 Avian Research ......................................................................................................... 9
2.1 Avian Mistnetting ................................................................................... 9
3 Mammal Incidentals ................................................................................................. 15
4 Herpetological Research .......................................................................................... 15
4.1 The Effect of Structural Habitat Change on Herpetofaunal Communities ................................................................................................ 15
5 Butterfly Research ................................................................................................... 20
5.1 Assessment of Antropogenic Disturbance on Butterfly Communities... 20
6 Dung Beetle Research ............................................................................................. 25
6.1 Assessment of the Impact of Structural Habitat Change on Dung Beetle Assemblages .................................................................................... 25
7 Community Development Projects ........................................................................... 34
7.1 Colegio Técnico Yachana (Yachana Technical High School) .............. 34
7.2 TEFL at Puerto Rico ............................................................................ 34
7.3 English Classes at Puerto Salazar ...................................................... 35
8 Future Expedition Aims ............................................................................................ 35
9 References .............................................................................................................. 36
9.1 General References ............................................................................ 36
9.2 Field Use References .......................................................................... 37
9.3 Dung Beetle References ..................................................................... 38
9.4 Amphibian References ........................................................................ 39
9.5 Butterfly References ............................................................................ 42
10 Appendix A - GVI Species List ................................................................................. 43
10.1 Class Aves .......................................................................................... 43
10.2 Class Mammalia .................................................................................. 46
10.3 Class Sauropsida ................................................................................ 47
10.4 Class Amphibia ................................................................................... 48
10.5 Class Arachnida .................................................................................. 49
10.6 Class Insecta ...................................................................................... 49
11 Appendix B – GVI Yachana Reserve Map ............................................................... 53
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List of Figures
Figure 2.1.1 Map showing the location of each mistnetting site Figure 2.1.2 Summary information regarding vegetation mapping of each mist-netting
site Fig. 2.1.3 Summary Mist-netting Information for Phase 101 Fig. 2.1.4 Summary Mist-netting Information for Phase 094 Figure 4.1.1 Number of individuals found in pitfalls in 101 Figure 4.1.2 Number of individuals found on visual encounter surveys in 101 Figure 4.1.3 Number of individuals found in pitfall traps in total in the project so far Figure 4.1.4 Number of individuals found in total for visual encounter surveys in the
project so far Figure 5.1.1 New standardised dot codes introduced in week 6 of Phase 101 Figure 5.1.2 Number of species and individuals trapped at each trap site
Figure 5.1.3 Average number of species and individuals encountered at each site
Figure 5.1.4 Number of species recorded at each trap in the forest and trail areas Figure 6.1.1 Habitat type of each dung beetle sampling site Figure 6.1.2 Trap layouts at each site Figure 6.1.3 Habitat compared to individuals captured Figure 6.1.4 Individuals identified to species Figure 6.1.5 Comparison of habitat to species richness
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1 Introduction
The Rainforest Conservation and Community Development Expedition operated by
Global Vision International (GVI) is located in the Yachana Reserve in the Napo
province (0° 50' 45.47"S/ -77° 13' 43.65"W; 300-350m altitude), Amazonian region of
Ecuador. The reserve is legally-designated a Bosque Protector (Protected Forest)
consisting of approximately 1000 hectares of predominantly primary lowland rainforest,
as well as abandoned plantations, grassland, riparian forest, regenerating forest and a
road. The Yachana Reserve is owned and managed by the Yachana Foundation. It is
surrounded by large areas of pasture land, small active cacao farms and currently un-
mapped disturbed primary forest. The road within the Yachana Reserve is a large
Fig. 1.1
GVI Amazon
Rio Napo, Napo Province
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stone and gravel based road which dissects the primary forest to the north and the
abandoned cacao plantations and grassland areas to the south.
The Yachana Foundation is dedicated to finding sustainable solutions to the problems
facing the Ecuadorian Amazon region. The foundation works with rainforest
communities to improve education, develop community-based medical care, establish
sustainable agricultural practices, provide environmentally sustainable economic
alternatives, and conserve the rainforest. The Yachana Reserve is the result of the
foundation’s efforts to purchase blocks of land for the purpose of conservation. The
Yachana Foundation has a long-term plan of sustainable management for the reserve
according to International Union for the Conservation of Nature (IUCN) protected forest
guidelines and guidelines laid out by the Ministerio del Ambiente (Ecuadorian Ministry
of the Environment). One of GVI’s main roles at the reserve is to provide support
where deemed necessary for the development of the management plan. This includes
reserve boundary determination, baseline biodiversity assessments, visitor information
support, and research centre development.
GVI also works closely with the Yachana Technical High School, a unique educational
facility for students from the surrounding region. The high school provides students with
meaningful education and practical experience in sustainable agriculture, animal
husbandry, conservation, eco-tourism, and small business operations. As part of their
experiential learning program, students use the Yachana Reserve and GVI’s presence
as a valuable educational tool. As part of their conservation curriculum, the students
visit the reserve to receive hands on training in some of GVI’s research methodology,
as well as familiarization with ecological systems. On a rotational basis, students spend
time at the reserve where they participate in the current research activities, and receive
conversational English classes from GVI volunteers.
GVI additionally conducts TEFL classes (Teaching English as a Foreign Language) at
the nearby village of Puerto Rico, twice a week. Classes are prepared the day before
and last for one hour. Groups of two or three volunteers conduct the classes, covering
relevant topics to the local school children. This allows GVI to integrate with the local
community, whilst giving volunteers the opportunity to experience firsthand involvement
in community development through teaching English. This is also currently laying the
foundation to introduce environmental education programmes to the Puerto Rico
community in the future.
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GVI also works with local research institutions. The Museo Ecuatoriano de Ciencias
Naturales, MECN, (Ecuadorian Museum for Natural Sciences) provides technical
assistance with field research and project development. The museum is a government
research institution which houses information and conducts research on the presence
and distribution of floral and faunal species throughout Ecuador. GVI obtains their
investigation permit with the support of MECN for the collection of specimens. The data
and specimens collected by GVI are being lodged with the MECN in order to make this
information nationally and internationally available, and to provide verification of the
field data. MECN technicians are continuously invited to the Yachana Reserve to
conduct in-field training and education for GVI and Yachana students, as well as
explore research opportunities otherwise unavailable.
A major goal for GVI’s research is to shift focus from identifying species in the reserve
to collecting data for management concerns and publication. In collaboration with all
local and international partners, GVI focuses its research on answering ecological
questions related to conservation. With this in mind, several key goals have been
identified:
• Cataloguing species diversity in the Yachana Reserve in relation to regional
diversity.
• Conducting long-term biological and conservation based research projects.
• Monitoring of biological integrity within the Yachana Reserve and the immediate
surrounding area.
• Publication of research findings in primary scientific literature.
• Solicitation of visiting researchers and academic collaborators.
• Identification of regional or bio-geographic endemic species or sub-species.
• Identification of species that are included within IUCN or Convention on
International Trade in Endangered Species of Wild Fauna and Flora (CITES)
appendices.
• Identification of keystone species important for ecosystem function.
• Identification of new species, sub-species, and range extensions.
• Identification of charismatic species that could add value in promoting the
Yachana Reserve to visitors.
In order to achieve the key goals, volunteers participate in five or ten weeks of each
phase and are trained by GVI personnel to conduct research on behalf of the local
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partners in support of their ongoing work. This report summarises the scientific
research and community-based programmes conducted during the ten-week
expedition from Friday 8th January to Friday 19th March 2010, at the Yachana
Reserve.
2 Avian Research
2.1 Avian Mistnetting
Introduction
As human populations grow, an understanding of anthropogenic change is essential to
understand the conservation of the natural world. Habitat loss is undoubtedly one of the
greatest threats facing tropical forest diversity (Hawes et al. 2008), with over half the
potential tropical closed-canopy forest, defined as tree crown coverage exceeding
60%, having already been removed and put to other use (Wright 2005). However,
there is hope. Despite deforestation reaching alarming levels, 15% of the land
deforested in the 1990s has been reclaimed by natural secondary succession (Wright
2005). This large scale expansion of secondary landscapes may have important
implications for long-term conservation of wildlife (Faria et al, 2007). The total
coverage of non-native and native regeneration will most probably rise further in the
near future due to private investment in carbon-sequestration projects in the tropics
and increased interest in bio fuels and timber (Barlow et al. 2006).
Several studies have optimistically concluded that this expansion of secondary forest
will offset the loss of worldwide biodiversity through destruction of primary habitat
(Wright 2005; Wright and Muller–Landau 2006). Stating that, the observed time lags
between habitat destruction and species extinctions are of sufficient length to allow
secondary forest to mature and regenerate into suitable habitat (Brooks et al; 2002).
Dunn (2004) states that; regenerating tropical secondary forests recover sufficiently in
20-40 years to recover faunal species diversity, but support lesser tree diversities than
old growth forests. Species compositions of flora and fauna communities often differ
between secondary and primary habitats (Blake and Loiselle 2000). The value of
regenerating secondary forest will be context and species dependant. There is a
growing consensus that there is currently a lack of empirical evidence to support the
theories that regenerating disturbed habitats will be sufficient to conserve most forest
species in the future (Gardner et al. 2007). Undoubtedly, further research needs to be
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performed before the true value of secondary regenerating forest can be unequivocally
determined.
There is currently a lack of consensus between many studies examining the impacts of
habitat change on bird communities. Despite birds being the most studied and
understood taxa in the Neotropics, a recent review of literature found that, pre-2008;
only 17 studies examined the value of secondary forest for tropical birds (Barlow et al.
2006). The majority of studies conducted to date have concluded that secondary
forests can support equivalent or high levels of species richness compared to primary
or relatively undisturbed forest (Barlow et al, 2006). Despite these encouraging results,
there are a whole host of problems with the existing studies which make a strong
conclusion of the value of secondary forest for Neotropical birds impossible to
determine (Gardner et al. 2006). For example, several of the studies attribute the high
species richness to the close proximity of primary habitat, resulting in primary species
being transiently recorded in secondary habitat. Several studies also lacked a good
primary forest baseline with which to compare their results (Barlow et al. 2006). This
aims to address the problems highlighted by Gardner et al (2007), to compare
understory bird communities in the disturbed secondary patches of the Yachana
Reserve with the relatively undisturbed patches.
Method
Study Plots
Four net locations were established around the reserve; two in relatively disturbed
areas, two in relatively undisturbed areas (see fig. 2.1.1). The net locations were no
closer than 500m apart at their nearest point as Barlow and Peres (2004) concluded,
based on recaptures of marked individuals, that plots 500m apart were spatially
independent. The net locations are restricted to trails within the reserve, as the hilly
topography makes establishing nets in other locations impossible without destroying
large areas of native vegetation. Plots are random with respect to tree fall gaps,
fruiting trees or other factors which may influence capture rates.
Mistnetting
Understory mistnetting was used to examine the avifauna at each of the four sites
within the reserve. Each site was sampled for 66 to 69 hours between the 18th of
January 2010 and the 10th March 2010. Four 12x2.5m mist nets with 10-40m spacing
(to allow for difficult topography) were established at each site. All nets could be
checked within a 10-15min period. Captured birds were then released away from the
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net locations from an established banding station. Nets were opened between 6.30am
and 11.10am for four successive days, allowing extra hours or days to account for
periods of persistent wind or heavy rain. Nets were checked every 30 minutes. All
captures were placed in a bird bag and returned to the banding station where they
were be identified to species, banded, weighed, measured and sexed whenever
possible. All birds were banded to identify recaptures, except hummingbirds, which
have extremely delicate legs.
Vegetation Mapping
Around each mist-netting site six 100m transects were assessed. Each transect started
250m away from the mist-netting center point and ended 150m away from the center
point, and were spaced evenly to avoid psuedoreplication. The transects were stratified
and placed randomly with regard to topography and habitat. Along each transect, five
canopy coverage estimations were made by two independent observers and the
dominant type of canopy was noted (Absent, Low, Middle and High). All
Melostomatacae and Heliconidae within 5m either side of the transect line were
Figure. 2.1.1 Map showing the location of each mist netting site
Represents the locations of each mist-netting site within the Yachana Reserve. The pink
dots represent the ‘less disturbed’ sites of Laguna and Frontier, whilst the green dots
represent the ‘more disturbed’ sites of Cascada and Ficus. The blue circles represent
required site separation outlined by Barlow and Perez (2004) to ensure the sites are
independent.
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counted. All trees >30cm Diameter at Breast Height (DBH) were measured within 5m
either side of the transect line. The presence or absence of trees of the genus
Theobroma and coffee plants were also noted.
Results
Vegetation Profiling
Vegetation profiling was performed in the week immediately following each mist netting
session (see Fig. 2.1.2). The numbers of Melostomacae varied from 156 (Cascada) to
1393 (Ficus). Number of flowing Heliconidae varied from 20 (Laguna) to 124
(Cascada). Coffee showed the most marked difference between the sites from two
(Laguna) to 3230 individuals (Ficus). Cascada and Laguna were dominated by high
canopy (63.3-90%) whereas Ficus and Frontier sites were predominantly mid-canopy.
However, only Cascada and Ficus were found to have gaps in their canopies. The
canopy cover measurement is inconclusive; with all sites spread from 42-53%. The
largest tree located was on the Cascada site; however Frontier had the largest average
DBH measurement. Finally, twelve freshly cut tree trunks were found at the Ficus site,
indicating strong human disturbance.
Fig. 2.1.2
Location Number of Plants Canopy Class (%)
Canopy
Cover
(%) Five largest trees DBH Notes
Melo Heli. Coffee High Mid Low Gap 1 2 3 4 5
Cascada 156 124 924 63.3 26.7 3.3 6.7 42 143 92 82 80 79
Ficus 1393 15 3230 23.3 56.6 13.3 6.7 51 96 90 90 86 76
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Stumps
Laguna 664 20 2 90 10 0 0 53 105 96 81 79 76
Frontier 812 30 6 40 53.3 6.7 0 50 128 111 106 99 89
Figure 2.1.2 Summary information regarding vegetation mapping of each mist-netting site.
The strongest differences observed between the sites were the presence of >900
individuals of coffee at Cascada and Ficus with canopy gap compositions of 6.7%. In
comparision Laguna and Frontier contained <7 individual coffee plants and had a 0%
canopy gap composition. On the basis of these results Cascada and Ficus are
classified as ‘more disturbed’ and Laguna and Frontier are classified as ‘less
disturbed’.
Avifaunal Sampling
In Phase 101 (Fig. 2.1.3) 127 birds were captured in 269 hours of mist-netting between
the dates of 18th of January 2010 and the 10th March 2010. Individuals caught at each
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site varied from eleven individuals to 35. Each site was subjected to between 66 hours
and 68.3 net hours of sampling. The total number of individuals captured in the ‘more
disturbed’ areas was 23, whereas the total number of individuals captured in the ‘less
disturbed’ areas was 57. The number of species captured at the ‘less disturbed’ sites
was also lower that captured in the ‘more disturbed’ sites (see Fig. 2.1.3). The
understory birds caught at each of the ‘more disturbed’ areas represented only five
different bird families, where as birds caught at the ‘less disturbed’ areas each
represented by eleven and nine different bird families. Capture efficiencies,
represented by number of individuals per mist net hour, where also higher in the ‘less
disturbed’ sites (0.32 and 0.52 indiv.h-1) in comparison to the ‘more disturbed’ sites
(0.18 and 0.17 indiv.h-1).
Fig. 2.1.3 Summary mist-nettingiInformation for Phase 101
More disturbed Less Disturbed
Total Cascada Ficus Laguna Frontier
Net Hours 67.28 66.28 68.30 67.10 269
Number of Individuals 12 11 22 35 80
Individuals per net hour 0.18 0.17 0.32 0.52 0.30
Total Num. of species 8 7 15 20 30
Species per net hour 0.12 0.11 0.22 0.30 0.11
Total Num. of famillies 6 4 10 11 16
Fig. 2.1.4 Summary mist-nettingiInformation for Phase 094
More disturbed Less Disturbed
Total Cascada Ficus Laguna Frontier
Net Hours 69.16 68.88 69.20 64.00 271
Number of Individuals 27 13 39 48 127
Individuals per net
hour 0.39 0.19 0.56 0.75 0.47
Total Num. of species 14 8 17 20 33
Species per net hour 0.20 0.12 0.25 0.31 0.12
Total Num. of famillies 5 5 11 9 16
Direct comparison of summary mist-netting information from Phases 094 (Fig. 2.1.4)
and 101 (Fig. 2.1.3) shows that the total numbers of individuals caught per phase has
decreased from 127 in phase 094 to 80 in phase 101. Previously noted trends that
there is lower species diversity and fewer individuals in the ‘more disturbed’ locations
are consistent between phase 094 and phase 101.
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Discussion
Vegetation Profiling
Using the vegetation mapping methods, in-field observation and map consultation;
Laguna and Frontier have been classified as ‘less disturbed’ whereas Cascada and
Ficus have been classified as ‘more disturbed’. The crucial differences appear to be
absence/presence of coffee plants and canopy gaps, however, more data must be
collected before these results can be confirmed.
Understory Mist-netting
Several differences between the ‘less disturbed’ and ‘more disturbed’ sites have been
observed. These include: number of species caught, number of individuals caught,
number of families represented, and percentage of individuals of a given family caught
at each site. However, the current sample size of 207 birds is completely prohibitive of
any statistically relevant analysis. The differences observed could be due to but not
limited to: genuine differences in understory bird community richness and structure in
each area, seasonal variations in bird foraging patterns, different weather conditions, or
simply a function of the low number of birds in the data set. The only way to begin to
address these potential factors is to increase the size of data set through repeated
sampling at each study site until enough data is obtained. Until that point, any
conclusions will be simply speculation.
The comparison of phase data from Phase 094 to Phase 101 is interesting. There was
a clear drop in the number of individuals caught at all sites. This could be due to
seasonal fluctuations in weather, local food availability effects or the disturbance
caused by the mist-netting method itself. It will be interesting to see if this trend
continues as this project moves into its next phase. The number of different species
caught at each site remained consistent, which would indicate that the observed drop is
in the number of individuals only – not a decrease in diversity.
Future Work
Both the understory mist-netting and vegetation mapping will be continued in their
current forms as they appear to be functioning effectively.
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3 Mammal Incidentals
Introduction
GVI continues to document mammal species activity in the reserve predominately
through incidental mammal and track sightings. This is confined to incidental
recordings due to the low occurrence of conspicuous diurnal mammals. Excessive
mammal surveying has proved to not be sufficiently productive.
Methods
All mammal species encountered outside of specific mammal surveys were recorded.
Incidental sightings can take place during any of the other survey or project work within
the reserve, or during long walks into the forest. At the occurence of each incidence,
the time, location, date, species, and any other key characteristics or notes are taken
and later entered into a database in camp.
Sightings
During this phase various mammal species were recorded incidentally, whilst groups
were participating in other survey work or walks in the forest. Incidental sightings
included encounters with the Amazon Red Squirrel (Sciurus sp.), Black Agouti
(Dasyprocta fuliginosa), Black-mantled Tamarins (Saguinus nigricollis), Coatis (Nasua
nasua), Kinkajou (Potos flavus), Night Monkeys (Aotus sp.), Common Opossum
(Didelphis marsupialis), Water Opossum (Chironectes minimus) and Water Rat
(Nectomys squamipes), Paca (Agouti paca). Also recorded were various unidentified
small rodents found in the amphibian pitfall traps.
4 Herpetological Research
4.1 The Effect of Structural Habitat Change on Herpetofaunal Communities
Introduction
One of the key drivers of worldwide species loss is habitat change; defined as habitat
deforestation, fragmentation and deterioration (Urbina-Cardona, 2008). The rapid rate
of forest conversion in the Neotropics has been offset by large-scale expansion of
secondary forest, plantation and pastureland (Wright SJ, 2005; Gardner et al. 2007b).
Despite the increasingly dominant role of these degraded habitats in the tropical
landscape, there is little consensus within the scientific community about the extent of
its conservation value (Gardner et al. 2007c, Lo-Man-Hung1, et al. 2008). Wright &
Muller-Landau (2006) predict that the future loss of primary forest will be offset by
regenerating secondary forest and consequently suggest that the predicted loss of
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species due to habitat change may be premature. However, there is currently a lack of
empirical evidence to support the theory that regenerating forests can fully support
native forest species (Gardner 2007c).
Two recent multiple taxa assessments, conducted on the cubraca cacao plantations of
Bahia, Brazil (Pardini et al. IN PRESS) and eucalyptus plantations of the Jari forestry
project, Brazil (Barlow et al. 2007), found that responses to structural habitat change
were taxon specific. Barlow et al. (2007) found that four of the fifteen taxa analysed
(trees and lianas, birds, fruit feeding butterflies, and leaf litter amphibians) were found
to decrease in species richness with increasing habitat disturbance. However, five taxa
(large mammals, epigiec arachnids, lizards, dung beetles and bats) exhibit idiosyncratic
responses to habitat change (Barlow et al. 2007). Both studies concluded that
responses to structural habitat change will be species specific, not simply taxon
specific. Analysis of a generalised taxon response is likely to hide a higher level of
species specific disturbance responses which are important when designing
conservation strategies (Barlow et al 2007; Pardini et al. 2009). These studies highlight
the importance of performing multiple taxa assessments that are species specific
relating to the conservation value of secondary and plantation forests.
Problem Statement
The Neotropics are estimated to contain nearly 50% of the worlds amphibians (IUCN,
2007) and 32% of the worlds reptiles (Young et al. 2004), this equates to over 3000
species of each taxon. Within the continental Neotropics, the 17 countries in Central
and South America, there are 1685 species of amphibian and 296 species of reptiles
considered endangered. Amphibians and reptiles are considered to be the most
threatened groups of terrestrial vertebrates (J. Gardner 2007b). There have been many
factors implicated in threatening populations of amphibians and reptiles, including
habitat loss and change, the virulent Batrachochytrium dendrobatidis pathogen, climate
change (Whitfield et al. 2007), ultraviolet-B radiation (Broomhall et al. 2000), and
agrochemical contaminants (Bridges et al. 2000).
Current State of Amphibian and Reptile Research
Amphibians and reptiles are important primary, mid-level and top consumers in
Neotropical ecosystems; therefore, it is important to understand the responses of these
organisms to structural habitat change (Bell et al. 2006). Despite its apparent severity,
the amount of research time given to studying the impacts of habitat change on
amphibian and reptile populations is relatively low. This is especially true in the
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Neotropics which, despite an estimated 89% of threatened species being affected by
habitat loss, has only been the subject of 10% of the world’s herpetological studies
(Gardner et al 2007a). There is a general consensus amongst herpetologists that the
effect of structural habitat change on determining amphibian and reptiles and
distributions is limited (Pearman, 1997; Krishnamurthy, 2003; Urbina-Cardona, 2006;
Gardner et al, 2007b).
A recent global scale review of the state of amphibian and reptile research regarding
structural habitat change highlighted several serious deficiencies: i) There is currently a
strong study bias away from the Neotropics towards North America and Australia. ii)
Published studies report contradictory responses of amphibian and reptile populations
to habitat change. iii) There are several common limitations in study methodology and
analysis (Gardner et al. 2007a).
Aims of the Research
• Assess the ability of secondary forest (abandoned cacao plantation) to preserve
leaflitter herpetofaunal richness, distribution and abundance in comparison to
primary forest habitat.
• Understand the effects of structural habitat change within the Neotropics.
• Identify the responses of different herpetofaunal groups/species to structural
habitat change.
Methods
In Phase 101, data was collected between 16th January to10th March 2010.
Nocturnal and Diurnal Visual Encounter Surveys
Twelve 75m transects in both the primary and secondary locations were established.
Care was taken to space transects sufficiently to avoid psuedoreplication. Transects
were marked with coloured transect tape to avoid unnecessary habitat modification.
Where possible, the transects were located at least 10m from streams and 100m from
forest edges to avoid biases resulting from increases in species richness and
abundance, which could result in confusion about the true effect of structural habitat
change on amphibian and reptile diversity.
Visual encounter surveys have been shown to be one of the most effective methods for
sampling tropical herpetofaunas (Bell et al, 2006). They have been repeatedly shown
to yield greater numbers of individuals per effort than other sampling methods in recent
18
publications (Ernst and Rodel, 2004; Donnelly et al 2005) and GVI’s own preliminary
investigations. Each transect was searched by six observers (strip width = 6m, duration
= 1h 30m).
Pitfall Trapping
Twelve pitfall arrays were also established in both primary and secondary forest. Each
array consists of four 25L buckets with 8m long by 50cm high plastic drift fence
connecting them in linear shaped design. When open, the pitfalls were checked at once
a day.
Particular care was taken to ensure that sampling effort is equal for both primary and
secondary habitats. This ensures maximum comparability in the resultant data sets.
Any amphibians or reptiles encountered through either method were identified in the
field using available literature and released. Any individual which could not be identified
was taken back to the GVI base camp for further analysis. A small proportion of the
captured individuals, including those that could not be identified, were anaesthetised
with Lidocaine and fixed with 10% formalin. All preseserved specimens are stored at
the Museo Ecuatoriano de Ciencias Naturales (MECN).
Surveying primary rainforest habitat is a privileged opportunity; however there is the
potential to negatively affect the ecosystem by passing infections between sites and
species. Good practices are strictly adhered to so as to ensure transmissions are not
possible. This is achieved by systematic cleaning of tools, equipment, and sterile bags
are changed when handling different individuals. Under no circumstances did
amphibians or reptiles come in contact with exposed human skin tissue.
Results
Species Encountered in 101
During this phase, 284 identified reptile and amphibian individuals were encountered,
comprising 19 species of amphibian and 16 species of reptile.
Pitfalls in Phase 101
Figure 4.1.1 Number of individuals found in pitfalls in Phase 101
Amphibians and
reptiles
Amphibians Reptiles
Total 163 132 31
19
Visual Encounter Surveys in Phase 101
Figure 4.1.2 Number of individuals found on visual encounter surveys in Phase 101
Amphibians and
reptiles
Amphibians Reptiles
Total
(approx 1080 mins survey
time with 5/6 searchers)
121 109 12
Species Encountered Overall in the Project So Far:
During the whole project to date, 1479 identified reptile and amphibian individuals have
been encountered.
Pitfalls
Figure 4.1.3 Number of individuals found in pitfall traps in total in the project so far
Amphibians and
reptiles
Amphibians Reptiles
Total 701 589 122
Visual Encounter Surveys
Figure 4.1.4: Number of individuals found in total for visual encounter surveys in the
project so far
Amphibians and
reptiles
Amphibians Reptiles
Total
(approx 5760 mins survey
time with 5/6 searchers)
778 719 59
Discussion
The amphibian and reptile work continues to provide a wealth of species which are
continuing to show that some species are more prevalent than others and there are
certainly some differences in the numbers and types of species found within different
areas of the reserve. The amphibians Ameerga bilinguis, Pristimantis kichwarum,
Pristimantis lanthanites, Bolitoglossa peruvianus (Dwarf-climbing Salamander) and the
lizard Lepsoma parietale are still found in greater numbers than other species at
various habitat types around the reserve.
20
It should be noted that Pristimantis ockendeni has recently been identified as three
different species and the species found within this reserve has been identified as
Pristimantis kichwarum. This identification has been made by observations of
morphological features and verification of photographs by specialists working on the
initial identification of these species.
The methods used within the past ten weeks will continue into the next phase so that
changes in species assemblages can be observed over an annual period of time.
The resultant analysis which will be used when a greater amount of data has been
gathered will involve multivariate analysis such as principal component analysis and
also decision tree analysis that may be applied to the development of a model used to
determine the types of amphibians and reptiles found in specific habitat types.
5 Butterfly Research
5.1 Assessment of Antropogenic Disturbance on Butterfly Communities
Introduction
Butterflies are widely regarded as important ecological indicators due to dependence of
the larval stage on a specific host plant, combined with adult pollinating roles (Ehrlich
and Raven, 1965). Herbivorous species are considered to indicate the diversity and
health of their habitats as they may closely reflect patterns of diversity in, as well as
disturbances to, plant species (DeVries and Walla, 1999; Sparrow et al. 1993). Due to
this, they may be used to predict patterns in other taxonomic groups.
Road systems sharply define and fragment forest ecosystems, resulting in changes to
plant species composition and structure from road edges to the surrounding interior
(Bennett, 1991). The presence of roads and trails opens up the forest canopy, creating
light gaps, modifying plant communities and resources available for other species.
Butterfly communities have been shown to be sensitive to environmental variables,
such as sunlight, gaps and edges (Ramos, 2000). Sparrow et al. (1994) found 74%
more butterfly species along a road transect than in undisturbed forest.
The Yachana Reserve comprises approximately 1000 hectares of predominantly
primary lowland rainforest in addition to a matrix of abandoned plantations, grassland,
21
riparian and regenerating forest. A road 15m wide runs through the middle of the
reserve, connecting it to the surrounding agricultural landscape. In addition to this,
there are a number of trails on either side of the road which are walked regularly by
individuals and groups of up to eight volunteers. This presents an excellent opportunity
to investigate the effects of disturbance from the road, in addition to making paired
comparisons between disturbed trails and nearby undisturbed forest transects.
Sparrow et al. (1994) recommend including both disturbed and undisturbed habitat
types in monitoring programs investigating butterfly community variation.
Method
Data collection continued on the established series of 200m transects on the Columbia
and Frontier Trails. The same sampling sites located every 50m continued to be
monitored. The Columbia and Frontier Trails run roughly perpendicular to the road and
receive heavy usage from GVI volunteers, Yachana tourtists and locals. Each sampling
site was paired with an undisturbed site located 75m perpendicular to the trail in the
forest to assess the impact of the trails on fruit-feeding nymphalid butterfly
communities. Traps 1-10 were located on Frontier while traps 11-20 were on Columbia.
Odd numbered traps were on the trails while the even numbered traps were in the
forest.
As in the previous phases of the study, two baited traps were suspended with the base
hanging approximately 1.5 meters above the ground at each sampling site. The traps
were baited and maintained for 14 consecutive days and checked daily in the
afternoon. New bait was added to the traps on the third day of sampling. The bait,
consisting of mashed, fermented bananas, was prepared following the methods of
DeVries and Walla (1999).
Captured butterflies were identified in the field by GVI volunteers and staff. When
identification in the field was not possible, photos of the specimen where taken and/or
the specimen was brought back to camp for further study. During previous phases of
study butterflies had been marked on the hindwing with non-toxic permanent marker
and replaced in the traps in order to measure escape rates.
Although marking in order to measure recapture rates has continued since the initiation
of the project, the dot codes used to refer to different traps have been inconsistent,
rendering a long period of recapture data unusable. This resulted from unexpected
22
changes in staff members running the project in phase 101. The dot code used during
the first six weeks of phase 101 was not standardised between observers and
recaptures of butterflies initially caught during this period show inconsistent dot code
markings. During the latter part of Phase 101 a standardised dot code was introduced
(Fig.5.1.1). Since nymphalidae and other detritivorous tribes can have a life span of
three to six months (Florida Museum Of Natural History, 2010; Turner 1971) recapture
data should be considered unsafe for the next phase and carefully monitored until no
further discrepancies from the new dot codes are noted.
Figure 5.1.1The new standardised dot codes introduced in week six of Phase 101.
It is worth noting that although specific dot-code data is unreliable all butterflies caught
continued to be marked before release. Therefore it will continue to be possible to
differentiate between recaptures and newly-caught individuals and hence avoid any
pseudo-replication.
Since data collection to explore escape rates and the nymphalid-vegetation relationship
had both been undertaken at the outset of the project it was not necessary to
undertake further vegetation mapping or escape experiments.
Results
Overall 187 individuals of at least 36 different species were captured over the two 14-
day periods with an additional twelve species still awaiting identification confirmation.
Only one new species was confirmed for the Yachana Reserve species list – Caligo
23
euphorbas, however, several of the specimens awaiting identification were also
suspected to be new to the reserve species list.
Some preliminary analysis all the data collected since the initiation of the project was
attempted, with the aim of elucidating some of the original trends sought in the initial
project proposal, namely the difference in the butterfly communities in areas of varying
levels of disturbance. Figure 5.1.2 displays the number of species and number of
individuals caught in each trap since the beginning of the project.
Fig. 5.1.2 Number of species and individuals trapped at each trap site.
Locations Number of
Species
Number of Individuals
Forest Average 15.8 27.7
Forest Standard
Deviation
3.5 7.7
Trail Average 13.7 29.1
Trail Standard
Deviation
3.3 8.5
Fig 5.1.3 Average number of species and individuals encountered at each site.
Trap Type Trap
Number
Total Number of
Species Trapped
Total Number of Individuals
Trapped
Trail 3 13 18
Trail 5 16 31
Trail 7 13 31
Trail 9 15 39
Trail 11 17 38
Trail 13 9 17
Trail 15 13 28
Trail 17 19 38
Trail 19 9 22
Forest 4 10 18
Forest 6 21 41
Forest 8 19 28
Forest 10 17 35
Forest 12 19 35
Forest 14 15 27
Forest 16 16 23
Forest 18 14 23
Forest 20 12 20
24
A greater diversity of butterflies was found in the undisturbed forest locations. However,
the number of individuals averaged marginally higher in traps on the disturbed trails.
The averages for both undisturbed forest and disturbed trails are displayed in the table
and graph below (Fig 5.1.3, Fig. 5.1.4).
Figure 5.1.4 Number of species recorded at each trap in the forest and trail areas.
Discussion
The two two-week periods of capture were marked by significantly lower capture levels
than in previous phases (187 individuals over the 28 days in comparison with 184
individuals in only 14 days during 094b). This was thought to be mainly due to changes
in the weather linked with a change into the wet season (more periods of heavy
rainfall), since it is know that butterflies alter their levels of activity according to climatic
conditions (Clench, 1966) with rainfall also reducing population (Hamer et al., 2003). It
was also speculated that slight changes in the practice of banana bait preparation may
have affected the attractiveness of the bait used. The methodology devised by Devries
& Walla (1999) will be followed exactly from this point forward in order to rule out any
bias from quality of bait.
More species were recorded in undisturbed forest sites that disturbed trail sites
although this is not currently a strong enough trend to be statistically significant.
Several studies have found the opposite of this; that more disturbed habitats tend to
hold great diversity of butterflies (Hamer et al. 2003). However, anthropological
Number of Species Recorded in Each Trap in Forest and Trail Areas
0
5
10
15
20
25
Trail
Trail
Trail
Trail
Trail
Trail
Trail
Trail
Trail
Fores
t
Fores
t
Fores
t
Fores
t
Fores
t
Fores
t
Fores
t
Fores
t
Fores
t
Number of Species
25
disturbance (rather than natural disturbance) has been shown to be negatively
correlated with butterfly diversity in certain forest habitats (Brown & Frietas, 2000).
Further data and more statistically robust analysis are required before the trends
tentatively identified by the analysis here can be confirmed, it will also be necessary to
check the data fit a normal or log-normal distribution. On average marginally more
individuals have been recorded from trail-base traps than undisturbed forest, although
this was such a minimal difference that it seems unlikely to be significant even once
further data are collected. .
This project will continue using the same methods as initially set out in the project
proposal (Brimble, 2009) next phase to acquire a larger sample size. Specimens and
photos of the unidentified species have been retained for future identification.
6 Dung Beetle Research
6.1 Assessment of the Impact of Structural Habitat Change on Dung Beetle
Assemblages
Introduction
Dung beetles (Order Coleoptera, Family Scarabaeidae, Subfamily Scarabaeinae) are
particularly vulnerable to habitat fragmentation and changes in habitat and fauna, this
sensitivity allows them to be extremely useful as indicators of ecosystem health
(Halffter et al. 1992; Klein 1989). For these reasons their use as indicator species for
Neotropical habitat disturbance research has increased in recent years.
An omnipresent component of tropical biotas, dung beetles perform constructive
ecosystem functions. Dung beetles are primarily associated with mammals; they are
indicators of mammalian abundance and possibly diversity. Nevertheless, dung
beetles’ functions in ecological systems go far beyond the status of an indicator. By
burying dung on which adults and larvae feed upon, dung beetles act as secondary
seed dispersers, accelerate nutrient recycling rates, increase plant yield and regulate
vertebrate parasites (Mittal, 1993; Andresen, 1999). (Hanski & Cambefort 1991;
Halffter & Matthews 1966; Estrada et al. 1991). Due to their influence, the decline in
dung beetle abundance and diversity may have cascading effects on the environment.
Habitat fragmentation is one of the most widespread and pervasive human activities
impacting upon the earth’s dwindling tropical rainforest habitats. Fragmentation
26
reduces total habitat area and creates subpopulations of species which are isolated
from one another, in turn disrupting individual and population behaviour (Hanski et al.,
1995). In addition, exchange of genes between populations, species interactions and
subsequently ecological processes are reduced (Aizen & Feinsinger, 1994; Saunders
et al., 1991). Fragmentation also modifies physical conditions, creating habitat edges
that are different from habitat interiors (Diamond, 1975). It has been estimated that the
area of Amazonian rainforest modified by such edge effects exceeds the area that has
been cleared by felling (Skole & Tucker, 1994).
Regeneration and restoration of forests through conservation efforts may mitigate
some current deforestation; however, a number of major obstacles still constrain
rainforest regeneration. According to several studies, the most significant factor in
regeneration is the transport of seeds to deforested sites (Young et al.1987, Pannell
1989, Nepstad et al. 1991, Buschbacher et al. 1992, Chapman & Chapman 1999, Holl
1999). Monitoring dung beetle assemblages in their associated habitats is essential in
conservation projects that aim to maintain the regeneration ability of forest fragments,
and ecosystem health (Andresen, 2003).
This study aims to survey dung beetles in tropical rainforest forest fragments located in
the Ecuadorian Amazon at the Yachana Reserve, to examine the effects of habitat
fragmentation on species diversity and abundance of these beetles.
This research addresses two main questions in the study at the reserve: (1) Does
habitat, isolation, or the density of trees of a fragment affect species richness, and
abundance? (2) Does fragmentation, isolation, or tree density affect the abundance of
the dominant species?
Methods
Study Site
All research was performed directly on, or in the area immediately surrounding, the
Yachana Reserve (see Appendix B). The road within the Yachana reserve is a large
stone and gravel based road which dissects the primary forest to the north and the
abandoned cacao plantations to the south. A growing body of research suggests that
roads can have a negative impact on species diversity (Cushman et al. 2006). Roads
can decrease dispersal, reduce genetic diversity and increase mortality. These affects
were considered when interpreting any data obtained.
27
Nine sites were chosen at random and marked throughout the Yachana Reserve
during Phase 092, 2009. Each site contained four baited pitfall traps, each positioned
on the corner of a 50m x 50m grid (refer to Figure 6.1.2), in order to minimize trap
interference and the effect of wind upon trap detectability (Larsen and Forsyth, 2005).
Five sites were placed within primary rainforest and four within the secondary matrix.
This allowed direct comparisons to be made between these two habitat types (refer to
Fig 6.1.1). Individual trap catches were pooled together for each site. Two sites were
exposed at one time (a trapping station from the primary forest and a trapping station
from the secondary matrix), in random combinations, so as to minimize the effect of
weather variability upon overall catch data. During the Phase 101 each trapping site
was sampled for 48 hours (apart from DB5 and DB9, sampled for only 24 hours), at
trapping stations spread throughout the habitat matrices. Traps were emptied every 24
hours. Each 24-hour sample from a trap was considered a single trap day. Trapping
periods lasted 48 hours in most cases. Beetles were identified by the author and
confirmed with assistance of specialists from the Museo Ecuatoriano de Ciencias
Naturales (MECN) in Quito. Beetles measuring ≥ 13 mm were considered as large.
Voucher specimens are temporarily held at GVI’s workstation within the Yachana
Reserve.
Site Habitat Type
DB1 Primary rainforest/Less disturbed
DB2 Primary rainforest/Less disturbed
DB3 Primary rainforest/Less disturbed
DB4 Primary rainforest/Less disturbed
DB5 Primary rainforest/Less disturbed
DB6 Secondary rainforest
DB7 Grassland with intermittent trees, bordered by secondary forest
DB8 Grassland with intermittent trees, bordered by secondary forest
DB9 Recovering Cacao plantation
Figure 6.1.1 Habitat type of each dung beetle sampling site
28
Figure 6.1.2 Trap layouts at each site
Each pitfall trap is constructed of a 16oz plastic container, baited with a dung ball
suspended above it. Containers were placed in a hole dug in the ground so that the top
was flush with the surrounding soil, allowing beetles to fall into the trap. All leaf litter
and vegetation was removed in a 25cm radius around each trap, as this was found
during preliminary investigations to affect trap efficiency (See Phase Report 091).
Traps were filled with an inch of water containing scent-free liquid detergent in order to
increase viscosity, to prevent beetles from escaping. Fresh dung, used as bait, was
collected from a horse on the morning of baiting the traps. 50cc of bait was suspended
in muslin netting 5cm above the lip of each trap, held in place by string and suspended
at the end of an angled stick placed in the ground. A plate was positioned 5cm above
the top of the bait ball using three upright sticks, in order to prevent rain and beetles
from landing directly on the dung bait.
Habitat Feature Mapping
Species occupy a particular habitat for breeding because the habitat contains certain
environmental factors that allow a species to carry out its life history (Hilden 1965,
James et al. 1984). Vegetation structure is of considerable importance to dung beetle
species habitat (MacArthur and MacArthur 1961, Hilden 1965, James 1971, Cody
1981, 1985). Some dung beetle species are specifically adapted to a vegetation
structure that meets their foraging requirements (Hilden 1965, Robinson and Holmes
29
1982, Cody 1985). To accurately assess dung beetle behavior, a thorough knowledge
of the vegetation structure of the habitats that they occupy is critical.
In most studies of habitat selection, the vegetation structure of occupied sites is
compared to unoccupied sites and sampling is usually done in one general location
within a species range (e.g., Haggerty 1986, 1998, Dunning and Watts 1990,
Plentovich et al. 1998). Although this method may indicate the major features that
determine occupancy, it does not necessarily indicate those features that may be the
most critical for occupancy.
An alternative approach, and the one used in this study, is to compare the vegetation
structure of occupied sites from a broad geographic perspective (James et al. 1984). If
it is assumed that a species have similar foraging and nest-site selection behaviors
throughout its range, then we can expect to see similarities in the vegetation structure
of different localities, even though other variables (e.g., floristics, tree age,
management practices) may be different. Similarities and differences in the vegetation
structure from different localities may help identify structural features that are more or
less critical for occupancy, respectively. Further, this approach may give a better
understanding of the vegetation structure that may constrain the distribution of a
species (James et al. 1984, Parrish 1995).
Vegetation profiling of nine sites within the Yachana Reserve was performed in
October 2009. Vegetation mapping was performed at each pitfall trap on a transect
station. To ensure an appropriate level of independence, data from sample circles for
each site were pooled and the site was used as the sample unit in all statistical
analyses.
Seven variables were measured at each trapping location using the methods of James
and Shugart (1970) and Wiens (1973) (Table 1). A sample grid was created, placed
directly over the desired pitfall trap location. Grid lines were extended 15 feet, in each
of the four cardinal directions. Quadrants (I-IV) were established to ensure the most
accurate data recording. Tree (dbh [greater than] 15 cm) density was determined by
counting and measuring the number of live and dead trees within the sample plot.
Percent canopy and understory canopy coverage were determined by estimation.
Vegetation density was measured by counting the number of vegetation hits along the
quadrant tape markers placed on the ground. Percent woody, shrub, grass, and litter
30
covers were estimated by noting if these vegetation types came in contact with a
vertically held rod that was placed at ten equally spaced points. Litter depth was
measured within 6 cm of the base of a vertically held measurement tool. Soil samples
were taken at four different locations within the established quadrants and were then
characterized and classified using the USCS (Unified Soil Classification System).
Results and Discussion
Habitat Structure
Currently the disturbance status of each site has been estimated through on-site
observation and examination of the reserve map, however this simply is not reliable
enough. The importance of vegetation structure in determining patterns of species
diversity and abundance is well established (Hawes et al. 2008). Vegetation mapping
of each trapping station has been completed but is not incorporated in this report.
Pitfall Trap Sampling
During Phase 101 the baited pitfall traps captured a total of 2121 individuals comprised
of 18 identifiable species and eight genera within 384 hours of trapping. Sampling
occurred from January 8, 2010 to March 19, 2010. Two of the sites (DB5 and DB9)
were sampled for only 24 hours due to a limitation of resources. In order to make
these sites comparable, the average percentage decline in the number of trapped
beetles between 24 and 48 hours was calculated for each habitat type using the
available data. This average percentage decline was then applied to the number of
trapped individuals within 24 hours to extrapolate how many may have been caught
had the traps been open for 48 hours.
The highest catch yielded 706 individuals comprised of ten different identifiable species
within a 48 hour trapping period, located within the primary forest (DB4). The lowest
catch yielded four individuals, comprised of two different identifiable species after a 48
hour trapping period (DB3) within the primary undisturbed forest (Figure 6.1.3).
31
Primary Undisturbed Individuals
Secondary
Disturbed Individuals
DB1- Ficus 18 DB6- Ridge 179
DB2- Upper B-loop 363 DB7- Buena Vista 234
DB3- Inca 4 DB8 -Buena Vista 124
DB4- Upper Frontier 706 DB9 -Cacao Grove 349 (534)*
DB5- Ficus (road) 144 (167*)
Total 1235 Total 886
*Trap open for 24 hours, extrapolated total for 48 hours given in brackets
Figure 6.1.3: Habitat compared to individuals captured
The primary, undisturbed habitat shows a greater variance in the number of individuals
caught at each site from the lowest number of individuals caught (4) to the highest
(706).
In order to draw conclusions from the data it is necessary to identify beetles to species
level. This was not possible in all cases due to the complexity of the field of dung
beetle taxonomy. However, Figure 6.1.4 below presents the data regarding only those
individuals identified to species.
The most commonly found species across both habitat types was Eurysternus
caribaeus. Overall, more identifiable beetles were found in the primary habitats, yet the
number of individuals trapped in secondary habitats was greater than that of primary
habitats. This may suggest greater species diversity within secondary habitats.
However, seven of the identifiable species found within primary habitats were not found
in secondary habitats. These included Onthophagus pubresas, Deltochilum
granulatum and Eurysternus hypocrita.
32
Fig
ure
6.1
.4 Indiv
iduals
identified t
o s
pecie
s
H
ab
ita
t P
rim
ary
– U
nd
istu
rbe
d
Se
con
da
ry -
Dis
turb
ed
T
ota
ls
T
rap
Nu
mb
er
DB
1
DB
2
DB
3
DB
4
DB
5
DB
6
DB
7
DB
8
DB
9
Pri
ma
ry
Se
con
da
ry
Identified to Species
Ca
nth
idiu
m s
p.
Aff
. H
istr
io
0
0
0
2
0
0
0
0
0
2
0
Ca
nth
on
lu
teic
ollis
2
8
0
1
4
1
3
3
0
2
28
8
De
lto
chilu
m g
ran
ula
tum
0
0
0
8
0
0
0
0
0
8
0
Dic
ho
tom
ius
ah
au
s 0
0
0
0
0
1
0
0
0
1
1
Dic
ho
tom
ius
con
cico
llis
0
0
0
1
0
0
0
0
0
1
0
Dic
ho
tom
ius
pre
ito
i 1
3
0
5
2
1
0
0
0
1
2
1
Eu
ryst
ern
us
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ba
eu
s 4
2
8
0
11
5
76
3
7
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44
2
60
8
5
Eu
ryst
ern
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fusu
s 0
1
5
0
1
33
0
4
2
7
4
9
13
Eu
ryst
ern
us
foe
du
s 0
6
0
7
2
4
3
2
1
1
9
10
Eu
ryst
ern
us
hyp
ocr
ita
0
0
0
1
0
0
0
0
0
1
0
Eu
ryst
ern
us
infl
exu
s 1
2
6
1
53
9
1
1
3
6
5
10
1
25
Eu
ryst
ern
us
ple
be
jus
1
1
1
0
0
1
22
1
2
0
4
35
On
tho
ph
ag
us
acu
min
ate
s 0
0
0
0
0
0
1
0
0
0
1
On
tho
ph
ag
us
ha
em
ato
pu
s 0
1
1
0
0
0
7
0
0
0
18
7
On
tho
ph
ag
us
nyc
top
us
1
31
0
0
5
2
1
0
0
54
5
8
75
On
tho
ph
ag
us
oe
re
0
0
0
0
6
0
0
0
0
6
0
On
tho
ph
ag
us
on
are
o
0
5
0
0
0
0
0
0
0
5
0
On
tho
ph
ag
us
pu
bre
sas
0
5
0
0
0
0
0
0
0
5
0
33
Site
Number of Species
Identified
Primary- Undisturbed
Ficus 6
Upper Bloop 11
Inca 2
Upper Frontier 10
Ficus (road) 8
Mean number of Species 7.4
Secondary –Disturbed
Ridge 9
Buena Vista 7
Buena Vista 5
Cacao Grove 6
Mean number of Species 6.75
Figure 6.1.5 Comparison of habitat to species richness
Habitat Specificity and Assemblage Similarity
Early results of this study offer an interesting comparison with the effects of primary -
undisturbed forest and disturbed – secondary forests on Neotropical dung beetle assemblages.
In contrast to what was predicted, primary – undisturbed rainforest and secondary – disturbed
rainforest habitats are representing large zones of mixing or gradation of dung beetle
assemblages, unlike the assumption of an abrupt assemblage turnover between habitats.
When averaging the total number of species captured in each habitat, the primary - undisturbed
habitat held 7.4 identifiable species while the secondary - more disturbed habitat averaged at
6.75 identifiable species per location. There appears to be little difference between species
richness when comparing the two habitats. However, there are differences in species richness
in trapping stations within the same habitat type (refer to Figure 6.1.5).
Habitat crossover in the associated beetle fauna may suggest that most dung beetles in the
community not completely habitat specialists and possibly host specialists. Local variation in
34
abiotic factors such as soil texture, moisture, and forest structure do influence the occurrence
and relative abundance of scarabaeines (Howden & Nealis 1975, 1978; Halffter & Edmonds
1982); however thus far data suggests the former. It is understood that conclusions are
qualitative due to missing data and the problem of identifying beetles to species level. Owing to
problems identifying dung beetles down to the species level, this project will now be post-poned
until further field guides become available.
7 Community Development Projects
7.1 Colegio Técnico Yachana (Yachana Technical High School)
GVI continues to work closely with the Yachana Technical High School. Seven current students
from the Yachana Technical High School joined the expedition for a period of five weeks each.
They participated in all aspects of the expedition, including survey work, camp duty and satellite
camps. Conversation sessions for language exchange were also arranged between the
students and GVI volunteers and/or staff. The students are of great assistance during field work,
sharing their knowledge about local uses for plants as well as helping with the scheduled project
work. They share their culture with volunteers and allow a greater insight into their background,
teaching traditional basket-weaving, traditional achiote-painting. The benefits to the students
are large, as they learn about the realities of conserving and managing a reserve first-hand,
along with the techniques used for monitoring different speices. They also get to practise and
improve their conversational English language skills for an extended period of time, during the
field work, but also around base camp. This sort of shared practical learning experience is
invaluable in the developing world and those students who have the opportunity and interest to
join GVI for a period of time (whether it be two weeks of longer periods), make great progress in
their English language as well as having the opportunity to experience inter-cultural exchange
with native English speakers from different parts of the globe. It is hoped that these exchanges
will continue in the future as they are beneficial to GVI volunteers, staff and of course to the
students themselves.
7.2 TEFL at Puerto Rico
Fifteen English classes were given at Puero Rico this phase. This resulted in 60 ‘volunteer
hours’ of teaching, to 22 older students (7-13 years old) and 14 younger students (4-7 years
old). The next expedition will see the continuation of these lessons, augamneted by an
occasional tropical ecology class given at the end of each five weeks. The English lessons and
35
interaction with the Puerto Rico community has had the long term aim of developing and
encorporating environmental education for the children at the school. This part of the interaction
will begin in Phase 102, but due to the level of understanding of English, this part of the
teaching will need to be presented in Spanish.
7.3 English Classes at Puerto Salazar
Two informal English classes were given at Puerto Salazar on Saturday afternoons. The
feedback from both the children and the volunteers was fantastic. We hope to continue and
expand on these classes in the future, however are somewhat tied to time and resources given
that Puerto Salazar is approximately 45 minutes walk away from GVI base camp in the Yachana
Reserve. GVI is aiming to support the communities around the reserve as much as possible,
but also very aware of the limitations due to fluctuations in numbers of volunteers and therefore
do not want to over-commit to programmes with the communities when there are high numbers
of volunteers on base, to then find that if the numbers drop GVI is unable to maintain the local
commitments. For this reason the work with Puerto Salazar will continue on the occasions
when it is convenient to both the local community and the GVI Amazon schedule, with a view to
continuing the work in the future.
8 Future Expedition Aims
� The biodiversity programme will be continued, opportunistically re-surveying sites, and
expanding the survey areas within the reserve.
� Avian research will continue, focusing on mist netting.
� Herpetological research will continue, repeating pitfall trapping and visual encounter
surveys, and incorporating the collection of environmental data (temperature, humidity, air
flow and light levels) at each of the surveying sites, so that specific climatic conditions can
be compared.
� The butterfly project will continue, examining the effects of road and trail disturbance upon
fruit feeding species, in relation to changes in vegetation.
� GVI will continue to participate in exchanges with the Yachana Technical High School.
� TEFL at Puerto Rico will continue with a defined focus for each ten week block, for each age
group and the aim is to encourage students to put their learning into practise and get them
conversing in English.
� Simple environmental lesson will begin at the school in Puerto Rico (to be given in Spanish).
36
� An expansion of teaching will branch out with weekend lessons at the local community
called of Puerto Salazar. These lessons will be the basis for a future opportunity of more
structured teaching times within this community.
9 References
9.1 General References
Allen, T., Ginkbeiner, S.L., and Johnson, D.H., 2004. Comparison of detection rates of breeding
marsh birds in passive and playback surveys at Lacreek National Wildlife refuge, South Dakota.
Waterbirds 27, 277-281.
Bennett, A. F., 1991. Roads, roadsides and wildlife conservation: A review. In: Saunders, D. A.,
Hobbs, R. J. (eds.). Nature Conservation 2: The role of corridors. Chipping Norton, NSW,
Australia: Surrey Beatty 99-118.
Daszak, P., Berger, L., Cunningham, A.A., Hyatt, A.D., Green, D.E., Speare. R., 1999.
Emerging infectious diseases and amphibian population declines. Emerging Infectious
Diseases. 5, 735-48.
Ehrlich, P. R., Raven, P. H., 1965. Butterflies and plants: A study in co-evolution. Evolution 18:
586-608.
Gardner T.A., Fitzherbert E.B., Drewes R.C., Howell K.M., Caro T., 2007. Spatial and temporal
patterns of abundance and diversity of an east African leaf litter amphibian fauna. Biotropica
39(1):105-113.
Heyer W.R., Donnelly M.A., McDiarmid R.W., Hayek L.A.C., Foster M.S., 1994. Measuring and
Monitoring Biological Diversity - Standard Methods for Amphibians.
Kroodsma, D.E., 1984. Songs of the Alder Flycatcher (Empidonax alnorum) and Willow
Flycatcher (Empidonax traillii) are innate. Auk 101, 13-24.
37
Lacher, T., 2004. Tropical Ecology, Assessment, and Monitoring (TEAM) Initiative: Avian
Monitoring Protocol version 3. Conservation International, Washington, DC.
www.teaminitiative.org.
Menendez-Guerrero P.A., Ron S.R. and Graham C.H., 2006. Predicting the Distribution and
Spread of Pathogens to Amphibians. Amphibian Conservation 11:127-128.
Ridgely, R.S., Greenfield, P.J., 2001. The birds of Ecuador. Volume I. Status, Distribution, and
Taxonomy. Cornell University Press, New York.
Sutherland, W.J., 1996. Ecological census techniques: a handbook. University press,
Cambridge.
Weldon, C., du Preez, L.H., Hyatt, A.D., Muller, R., Speare, R., 2004. Origin of the amphibian
chytrid fungus. Emerging Infectious Diseases. 10 (Issue 12).
9.2 Field Use References
Bartlett, R.D., Bartlett, P., 2003. Reptiles and amphibians of the Amazon. An ecotourist’s guide.
University Press of Florida, Gainsville.
Bollino, M., Onore G., 2001. Butterflies & moths of Ecuador. Volume 10a. Familia: Papilionidae.
Pontificia Universidad Católica del Ecuador, Quito.
Carrera, C., Fierro, K., 2001. Manual de monitoreo los macroinvertebrados acuáticos.
EcoCiencia, Quito.
Carrillo, E., Aldás, S., Altamirano, M., Ayala, F., Cisneros, D. Endara, A., Márquez, C., Morales,
M., Nogales, F, Salvador, P., Torres, M.L., Valencia, J., Villamarín, F., Yánez, M., Zárate, P.,
2005. Lista roja de los reptiles del Ecuador. Novum Milenium, Quito.
de la Torre, S., 2000. Primates of Amazonian Ecuador. SIMBIOE, Quito.
DeVries, P.J., 1997. The butterflies of Costa Rica and their natural history. Volume II:
Riodinidae. Princeton University Press, Princeton.
38
Duellman, W.E., 1978. The biology of an equatorial herpetofauna in Amazonian Ecuador. The
University of Kansas, Lawrence.
Eisenberg, J.F., Redford, K.H., 1999. Mammals of the Neotropics: The central Neotropics.
Volume 3 Ecuador, Peru, Bolivia, Brazil. The University of Chicago Press, Chicago.
Emmons, L.H., Feer, F., 1997. Neotropical rainforest mammals. A field guide, second edition.
The University of Chicago Press, Chicago.
Moreno E., M., Silva del P., X., Estévez J., G., Marggraff, I., Marggraff, P., 1997. Mariposas del
Ecuador. Occidental Exploration and Production Company, Quito.
Neild, A.F.E., 1996. The butterflies of Venezuela. Meridain Publications. London.
Ridgely, R.S., Greenfield, P.J., 2001. The birds of Ecuador. Volume I. Status, distribution and
taxonomy. Christopher Helm, London.
Ridgely, R.S., Greenfield, P.J., 2001. The birds of Ecuador. Volume II. A field guide. Christopher
Helm, London.
Tirira S., D., 2001. Libro rojo de los mamíferos del Ecuador. SIMBIOE/EcoCiencia, Quito.
9.3 Dung Beetle References
Aizen, M. A. & Feinsinger, P. (1994). Forest fragmentation, pollination and plant reproduction in
Chago dry forest, Argentina. Ecology 75: 330-351.
Andresen, E. (1999). Seed dispersal by monkeys and the fate of dispersed seeds in the
Peruvian rain forest. Biotropica 31: 145-158.
Diamond, J. M. (1975). The island dilemma: lessons of modern biogeographic studies for the
design of natural reserves. Biological Conservation 7: 129-146.
39
Estradsa, A., Coates-Estrada, R., Dadda, A. A. & Cammarano, P. (1998). Dung and carrion
beetles in tropical rainforest fragments and agricultural habitats at Los Tuxtlas, Mexico. Journal
of Tropical Ecology 14: 577-593.
Hanski, I., Pakkala, T., Kuussaari, M. & Lei, G. (1995). Metapopulation persistence of an
endangered butterfly in a fragmented landscape. Oikos 72: 21-28.
Larsen, T. H. and Forsyth, A. (2005). Trap spacing and transect design for dung beetle
biodiversity studies. Biotropica 37: 322-325.
Mittal, I. C. (1993). Natural manuring and soil conditioning by dung beetles. Tropical Ecology 34:
150-159.
Saunders, D. A., Hobbs, R. J. & Margules, C. R. (1991). Biological consequences of ecosystem
fragmentation: a review. Conservation biology 5: 18-32.
Skole, D. L. & Tucker, C. (1994). Tropical deforestation and habitat loss fragmentation in the
Amazon: satellite data from 1978-1988. Science 260: 1905–1910.
Spector, S. & Forsyth, A. B. (1998). Indicator taxa for biodiversity assessment in the vanishing
tropics. Conservation Biology Series 1: 181-209.
9.4 Amphibian References
J. Barlow, T. A. Gardner, I. S. Araujo, T. C. Avila-Pires, A. B. Bonaldo, J. E. Costa, M. C.
Esposito, L. V. Ferreira, J. Hawes, M. I. M. Hernandez, M. S. Hoogmoed, R. N. Leite, N. F. Lo-
Man-Hung, J. R. Malcolm, M. B. Martins, L. A. M. Mestre, R. Miranda-Santos, A. L. Nunes-
Gutjahr, W. L. Overal, L. Parry, S. L. Peters, M. A. Ribeiro-Junior, M. N. F. da Silva, C. da Silva
Motta, and C. A. Peres (2007) Quantifying the biodiversity value of tropical primary, secondary,
and plantation forests PNAS vol. 104 no. 47 18555–18560
Beebee, T.J.C., Griffiths, R.A., (2005). The amphibian decline crisis: A watershed for
conservation biology? Biological Conservation 125, 271–285.
40
K. E. Bell and M. A. Donnelly (2006) Influence of Forest Fragmentation on Community
Structure of Frogs and Lizards in Northeastern Costa Rica Conservation Biology Volume 20,
No. 6, 1750–1760
Bridges, C.M., Semlitsch, R.D., (2000). Variation in pesticide tolerance of tadpoles among and
within species of Ranidae and patterns of amphibian decline. Conservation Biology 14, 1490–
1499.
Broomhall, S.D., Osborne, W.S., Cunningham, R.B. (2000). Comparative effects of ambient
ultraviolet-B radiation on two sympatric species of Australian frogs. Conservation Biology 14,
420–427.
Samuel A. Cushman (2006) Effects of habitat loss and fragmentation on amphibians: A review
and prospectus Biological Conservation 128; 231 –240
Donnelly, M. A., M. H. Chen, and G. C.Watkins. (2005) Sampling amphibians and reptiles in the
Iwokrama Forest ecosystem. Proceedings of the Academy of Natural Sciences of Philadelphia
154:55–69.
Toby A. Gardner*, Jos Barlow, Carlos A. Peres (2007a) Paradox, presumption and pitfalls in
conservation biology: The importance of habitat change for amphibians and reptiles Biological
Conservation 138; 166–179
T. A. Gardner, M.A.Ribeiro-Junior, J. Barlow, T. S. Avila-Pires, M.S. Hoogmeod and C. A. Peres
(2007b) The Value of Primary, Secondary, and Plantation Forests for a Neotropical
Herpetofauna Conservation Biology Vol 21, 3; 775–787
T. A. Gardner, J. Barlow, L. W. Parry, and C. A. Peres (2007c) Predicting the Uncertain Future
of Tropical Forest Species in a Data Vacuum BIOTROPICA 39(1): 25–30 2007
Gibbons, J. W., Scott, D. E., Ryan, T. J., Buhlmann, K. A., Tuberville, T. D., Metts, B. S.,
Greene, J. L., Mills, T., Leiden, Y., Poppy, S. and C. T. Winne. 2000. The global decline of
reptiles, deja-vu amphibians. Bioscience 50: 653–667.
41
S.V. Krishnamurthy (2003) Amphibian assemblages in undisturbed and disturbed areas of
Kudremukh National Park, central Western Ghats, India Environmental Conservation 30 (3):
274–282
P. B. Pearman (1997) Correlates of Amphibian Diversity in an Altered Landscape of Amazonian
Ecuador Conservation Biology, Volume 11, No. 5 Pages 1211–1225
R. Pardini, D. Faria, G. M. Accacio, R. R. Laps, E. Mariano-Neto,
M. L.B. Paciencia, M. Dixo, Julio Baumgarten (2009) The challenge of maintaining Atlantic
forest biodiversity: A multi-taxa conservation assessment of specialist and generalist species in
an agro-forestry mosaic in southern Bahia Biological Conservation 142; 1170-1182
M. Rödel & R. Ernst (2004) MEASURING AND MONITORING AMPHIBIAN DIVERSITY IN
TROPICAL FORESTS. I. AN EVALUATION OF METHODS WITH RECOMMENDATIONS FOR
STANDARDIZATION Ecotropica 10: 1–14,
Sala, O.E., Chapin, F.S.I., Armesto, J.J., Berlow, E., Bloomfield, J., Dirzo, R., Huber-Sanwald,
E., Huenneke, L.F., Jackson, R.B., Kinzig, A., Leemans, R., Lodge, D.M., Mooney, H.A.,
Oesterheld, M., Poff, N.L., Sykes, M.T., Walker, B.H., Walker, M., Wall, D.H., (2000). Global
biodiversity scenarios for the year 2100. Science 287, 1770–1774.
Stuart, S.N., Chanson, J.S., Cox, N.A., Young, B.E., Rodrigues, A.S.L., Fischman, D.L. and
Waller, R.W. (2004). Status and trends of amphibians declines and extinctions worldwide.
Science 306: 1783-1786.
J. N. Urbina-Cardona, M. Olivares-Pe´rez, V. H. Reynoso (2006) Herpetofauna diversity and
microenvironment correlates across a pasture–edge–interior ecotone in tropical rainforest
fragments in the Los Tuxtlas Biosphere Reserve of Veracruz, Mexico Biological Conservation
132; 61–75
J. N. Urbina-Cardona (2008) Conservation of Neotropical Herpetofauna: Research Trends and
Challenges Tropical Conservation Science Vol.1(4):359-375
Wright SJ (2005) Tropical forests in a changing environment Trends Ecol Evol 20:553–560.
42
Whitfield SM, Pierce MSF (2005) Tree buttress microhabitat use by a neotropical leaf-litter
herpetofauna. Journal of Herpetology 39:192-198.
Whitfield SM, Bell KE, Philippi T, Sasa M, Bolanos F, Chaves G, Savage JM, DonnellyMA
(2007) Amphibian and reptile declines over 35 years at La Selva, Costa Rica Proc Natl Acad Sci
104:8352–8356.
Young, B.E., Stuart, S.N., Chanson, J.S., Cox, N.A., Boucher, T.M., 2004. Disappearing Jewels:
The Status of New World Amphibians. Natureserve, Arlington, VA.
9.5 Butterfly References
Bennett, A. F., 1991. Roads, roadsides and wildlife conservation: A review. In: Saunders, D. A.,
Hobbs, R. J. (eds.). Nature Conservation 2: The role of corridors. Chipping Norton, NSW,
Australia: Surrey Beatty pp. 99-118.
Cottam, G., Curtis, J.T., 1956. The use of distance measures in phytosociological sampling.
Ecology 37: 451-460.
DeVries, P. J., Walla, T. R., 1999. Species diversity in spatial and temporal dimensions of fruit-
feeding butterflies from two Ecuadorian rainforests. Biological Journal of the Linnean Society 68:
333-353.
Ehrlich, P. R., Raven, P. H., 1965. Butterflies and plants: A study in co-evolution. Evolution 18:
586-608.
Ramos, A. F., 2000. Nymphalid butterfly communities in an Amazonian forest fragment. Journal
of Research on the Lepidoptera 35:29-41.
Sparrow, H. R., Sisk, T. D., Ehrlich, P. R., Murphy, D. D., 1994. Techniques and guidelines for
monitoring neotropical butterflies. Conservation Biology. 8: 800-809.
43
10 Appendix A - GVI Species List
January 2010
** New additions to the Yachana
Species List in Phase 101
10.1 Class Aves
Tinamiformes
Tinamidae Tinamous
Crypturellus bartletti Bartlett's Tinamou
Crypturellus cinereus Cinereous Tinamou
Crypturellus soui Little Tinamou
Crypturellus undulatus Undulated Tinamou
Crypturellus variegatus Variegated Tinamou
Tinamus major Great Tinamou
Ciconiformes
Ardeidae Herons, Bitterns and Egrets
Ardea cocoi Cocoi Heron
Bubulcus ibis Cattle Egret
Butorides striatus Striated Heron
Egretta caerulea Little Blue Heron
Egretta thula Snowy Egret
Tigrisoma lineatum Rufescent Tiger-Heron
Cathartidae American Vultures
Cathartes aura Turkey Vulture
Cathartes melambrotus Greater Yellow-headed Vulture
Coragyps atractus Black Vulture
Sarcoramphus papa King Vulture
Falconiformes
Accipitridae Kites, Eagles, Hawks etc
**Spizaetus ornatus **Ornate Hawk-eagle
Buteo magnirostris Roadside Hawk
Buteo polyosoma Variable Hawk
Elanoides forficatus Swallow-tailed Kite
Harpagus bidentatus Double-toothed Kite
Ictinia plumbea Plumbeous Kite
Leptodon cayanensis Gray-headed Kite
Leucopternis melanops Black-faced Hawk
Leucopternis albicollis White Hawk
Pandion haliaetus Osprey
Falconidae Falcons and Caracaras
Daptrius ater Black Caracara
Falco rufigularis Bat Falcon
Ibycter americanus Red-throated Caracara
Herpetotheres cachinnans Laughing Falcon
Micrastur gilvicollis Lined Forest-Falcon
Micrastur semitorquatus Collared Forest-Falcon
Milvago chimachima Yellow-headed Caracara
Galliformes
Cracidae Curassows, Guans, and Chachalacas
Nothocrax urumutum Nocturnal Curassow
Ortalis guttata Speckled Chachalaca
Penelope jacquacu Spix's Guan
Odontophoridae New World Quails
Odontophorus gujanensis Marbled Wood-Quail
Charadriiformes
Scolopacidae Sandpipers, Snipes and Phalaropes
Actitis macularia Spotted Sandpiper
Tringa solitaria Solitary Sandpiper
Recurvirostridae Plovers and Lapwings
Hoploxypterus cayanus Pied Plover
Gruiformes
Rallidae Rails, Gallinules, and Coots
Anurolimnatus castaneiceps Chestnut-headed Crake
Aramides cajanea Gray-necked Wood-Rail
Columbiformes
Columbidae Pigeons and Doves
Claravis pretiosa Blue Ground-Dove
Columba plumbea Plumbeous Pigeon
Geotrygon montana Ruddy Quail-Dove
Leptotila rufaxilla Gray-fronted Dove
Psittaciformes
Psittacidae Parrots and Macaws
Amazona farinosa Mealy Amazon
Amazona ochrocephala Yellow-crowned Amazon
Ara severa Chestnut-fronted Macaw
Psittacidae Cont. Parrots and Macaws
Aratinga leucophthalmus White-eyed Parakeet
44
Aratinga weddellii Dusky-headed Parakeet
Pionites melanocephala Black-headed Parrot
Pionopsitta barrabandi Orange-cheeked Parrot
Pionus menstruus Blue-headed Parrot
Pionus chalcopterus Bronze-winged Parrot
Pyrrhura melanura Maroon-tailed Parakeet
Cuculiformes
Cuculidae Cuckoos and Anis
Crotophaga ani Smooth-billed Ani
Crotophaga major Greater Ani
Piaya cayana Squirrel Cockoo
Piaya melanogaster Black-bellied Cuckoo
Opisthocomidae Hoatzin
Opisthocomus hoazin Hoatzin
Strigiformes
Strigidae Typical Owls
Glaucidium brasilianum Ferruginous Pygmy-Owl
Lophostrix cristata Crested owl
Otus choliba Tropical Screech-Owl
Otus watsonii Tawny-bellied Screech-owl
Pulsatrix perspicillata Spectacled owl
Caprimulgiformes
Nyctibiidae Potoos
Nyctibius aethereus Long-tailed Potoo
Nyctibius grandis Great Potoo
Nyctibius griseus Common Potoo
Caprimulgidae Nightjars and Nighthawks
Nyctidromus albicollis Pauraque
Nyctiphrynus ocellatus Ocellated Poorwill
Apodiformes
Apodidae Swifts
Chaetura cinereiventris Grey-rumped Swift
Streptoprocne zonaris White-collared Swift
Piciformes
Galibulidae Jacamars
Jacamerops aureus Great Jacamar
Galbula albirostris Yellow-billed Jacamar
Bucconidae Puffbirds
Chelidoptera tenebrosa Swallow-winged Puffbird
Bucco macrodactylus Chestnut-capped Puffbird
Malacoptila fusca White-chested Puffbird
Monasa flavirostris Yellow-billed Nunbird
Monasa morphoeus White-fronted Nunbird
Monasa nigrifrons Black-fronted Nunbird
Notharchus macrorynchos White-necked Puffbird
Capitonidae New World Barbets
Capita aurovirens Scarlet-crowned Barbet
Capita auratus Gilded Barbet
Eubucco bourcierii Lemon-throated Barbet
Ramphastidae Toucans
Pteroglossus azara Ivory-billed Aracari
Pteroglossus castanotis Chestnut-eared Aracari
Pteroglossus inscriptus Lettered Aracari
Pteroglossus pluricinctus Many-banded Aracari
Ramphastos vitellinus Channel-billed Toucan
Ramphastos tucanus White-throated Toucan
Selenidera reinwardtii Golden-collared Toucanet
Picidae Woodpeckers and Piculets
Campephilus melanoleucos Crimson-crested Woodpecker
Campephilus rubricollis Red-necked Woodpecker
Celeus elegans Chestnut Woodpecker
Celeus flavus Cream-coloured Woodpecker
Celeus grammicus Scale-breasted Woodpecker
Chrysoptilus punctigula Spot-breasted Woodpecker
Dryocopus lineatus Lineated Woodpecker
Melanerpes cruentatus Yellow-tufted Woodpecker
Picumnus lafresnayi Lafresnaye's piculet
Veniliornis fumigates Smoky-brown Woodpecker
Veniliornis passerines Little Woodpecker Trochilidae Hummingbirds
Amazilia franciae cyanocollis Andean Emerald Hummingbird
Amazilia fimbriata Glittering-throated Emerald
Anthracothorax nigricollis Black-throated Mango
Campylopterus largipennis Gray-breasted Sabrewing
Campylopterus villaviscensio Napo Sabrewing
Eriocnemis vestitus Glowing Puffleg
Eutoxeres condamini Buff-tailed Sicklebill
Glaucis hirsute Rufous -breasted Hermit
Heliothryx aurita Black-eared Fairy
Heliodoxa aurescens Gould's Jewelfront
45
Phaethornis bourcieri Straight-billed Hermit
Phaethornis hispidus White-bearded Hermit
Phaethornis malaris Great-billed Hermit
Thalurania furcata Fork-tailed Woodnymph
Trogoniformes
Trogonidae Trogons and Quetzals
Pharomachrus pavoninus Pavonine Quetzal
Trogon melanurus Black-tailed Trogon
Trogon viridis Amazonian White-tailed Trogon
Trogon collaris Collared Trogon
Trogon rufus Black-throated Trogon
Trogon violaceus Amazonian Violaceous Trogon
Trogon curucui Blue-crowned Trogon
Coraciiformes
Alcedinidae Kingfishers
Chloroceryle amazona Amazon Kingfisher
Chloroceryle americana Green Kingfisher
Chloroceryle inda Green and Rufous Kingfisher
Megaceryle torquata Ringed Kingfisher
Momotidae Motmots
Baryphthengus martii Rufous Motmot
Electron platyrhynchum Broad-billed Motmot
Momotus momota Blue-crowned Motmot
Cotingidae Cotinga
Ampelioides tschudii Scaled Fruiteater
Cotinga cayana Spangled Cotinga
Cotinga maynana Plum-throated Cotinga
Gynnoderus foetidus Bare-necked Fruitcrow
Iodopleura isabellae White-browed Purpletuft
Querula purpurata Purple throated Fruitcrow
Pipridae Manakins
Chiroxiphia pareola Blue-backed Manakin
Chloropipo holochlora Green Manakin
Dixiphia pipra White-crowned Manakin
Lepidothrix coronata Blue-crowned Manakin
Machaeropterus regulus Striped Manakin
Manacus manacus White-bearded Manakin
Pipra erythrocephala Golden-headed Manakin
Tyranneutes stolzmanni Dwarf Tyrant Manakin
Corvidae Crows, Jays, and Magpies
Cyanocorax violaceus Violaceous Jay
Vireonidae Vireos
Vireo olivaceus Red-eyed Vireo
Turdidae Thrushes
Catharus ustulatus Swainson's Thrush
Turdus albicollis White-necked Thrush
Turdus lawrencii Lawrence's Thrush
Hirundinidae Swallows and Martins
Atticora fasciata White-banded Swallow
Stelgidopteryx ruficollis Southern rough-winged swallow
Tachycineta albiventer White-winged Swallow
Troglodytidae Wrens
Campylorhynchus turdinus Thrush-like Wren
Donacobius atricapillus Black-capped Donacobius
Henicorhina leucosticta White-breasted Wood-wren
Microcerculus marginatus Southern Nightingale-Wren
Thryothorus coraya Coraya Wren
Polioptilidae Gnatcatchers and Gnatwrens
Microbates cinereiventris Tawny-faced Gnatwren
Parulidae New World Warblers
Dendroica aestiva Yellow Warbler
Basileuterus fulvicauda Buff-rumped Warbler
Dendroica fusca Blackburnian Warbler
Dendroica striata Blackpoll Warbler Thraupidae Tanagers
Chlorophanes spiza Green Honeycreeper
Cissopis leveriana Magpie Tanager
Creugops verticalis Rufous-crested Tanager
Cyanerpes caeruleus Purple Honeycreeper
Dacnis flaviventer Yellow-bellied Dacnis
Euphonia laniirostris Thick-billed Euphonia
Euphonia rufiventris Rufous-bellied Euphonia
Euponia xanthogaster Orange-bellied Euphonia
Euphonia chrysopasta White-lored Euphonia
Habia rubica Red-crowned Ant-Tanager
Hemithraupis flavicollis Yellow-backed Tanager
Piranaga olivacea Scarlet Tanager
Piranaga rubra Summer Tanager
Ramphocelus carbo Silver-beaked Tanager
46
Ramphocelus nigrogularis Masked Crimson Tanager
Tachyphonus cristatus Flame-crested Tanager
Tachyphonus surinamus Fulvous-crested Tanager
Tangara callophrys Opal-crowned Tanager
Tangara chilensis Paradise Tanager
Tangara mexicana Turquoise Tanager
Tangara schrankii Green-and-gold Tanager
Tangara xanthogastra Yellow-bellied Tanager
Tersina viridis Swallow Tanager
Thraupis episcopus Blue-gray Tanager
Thraupis palmarum Palm Tanager
Cardinalidae Saltators, Grosbeaks etc
Cyanocompsa cyanoides Blue-black Grosbeak
Saltator grossus Slate-colored Grosbeak
Saltator maximus Buff-throated Saltator
Emberizidae Emberizine Finches
Ammodramus aurifrons Yellow-browed Sparrow
Oryzoborus angloensis Lesser Seed-Finch
Fringillidae Cardueline Finches
Carduelis psaltria Lesser Goldfinch
Icteridae American Orioles, and Blackbirds
Cacicus cela Yellow-rumped Cacique
Cacicus solitarius Solitary Cacique
Clypicterus oseryi Casqued Oropendola
Gymnomystax mexicanus Oriole Blackbird
Icterus croconotus Orange-backed Troupial
Molothrus oryzivorous Giant Cowbird
Psarocolius angustifrons Russet-backed Oropendola
Psarocolius decumanas Crested Oropendola
Psarocolius viridis Green Oropendola
10.2 Class
Mammalia
Marsupialia
Didelphidae Opossums
Caluromys lanatus Western woolly opposum
Chironectes minimus Water opossum
Didelphis marsupialis Common opossum
Marmosa lepida Little rufous mouse opossum
Micoureus demerarae Long-furred woolly mouse opossum
Philander sp. Four-eyed opossum
Xenarthra
Megalonychidae
Subfamily Choloepinae Two-toed sloths
Choloepus diadactylus Southern two-toed sloth
Dasypodidae Armadillos
Cabassous unicinctus Southern naked-tailed armadillo
Dasypus novemcinctus Nine-banded armadillo
Chiroptera
Carollinae Short-tailed Fruit bats
Carollia brevicauda
Carollia castanea
Carollia perspicullatus Short-tailed fruit bat
Rhinophylla pumilio Little fruit bat
Desmodontinae Vampire bats
Desmodus rotundus Common vampire bat
Emballonuridae Sac-winged/Sheath-tailed Bats
Saccopteryx bilineata White-lined bat
Glossophaginae Long tongued bats
Glossophaga soricina Long tongued bat
Lonchophylla robusta Spear-nosed long-tongued bat
Stenodermatidae Neotropical Fruit bats
Artibeus jamaicensis Large fruit-eating bat
Artibeus lituratus Large fruit bat
Artibeus obscurus Large fruit bat
Artibeus planirostus Large fruit bat
Chiroderma villosum Big-eyed bat
Sturrnia lilium Hairy-legged bat
Sturnria oporaphilum Yellow shouldered fruit bat
Uroderma pilobatum Tent-making bat
Vampyrodes caraccioli Great Stripe-faced bat
Phyllostominae Spear-nosed Bats
Macrophyllum macrophyllum Long-legged bat
Mimon crenulatum Hairy-nosed bat
Phyllostomus hastatus Spear-nosed bat
Vespertilionidae Vespertilionid Bats
Myotis nigricans Little brown bat
47
Primates Monkeys
Callitrichidae
Saguinus nigricollis Black-mantle tamarin
Cebidae
Allouatta seniculus Red howler monkey
Aotus sp. Night monkey
Cebus albifrons White-fronted capuchin
Carnivora Carnivores
Procyonidae Raccoon
Nasua nasua South american coati
Potos flavus Kinkajou
Mustelidae Weasel
Eira Barbara Tayra
Lontra longicaudis Neotropical otter
Felidae Cat
Herpailurus yaguarundi Jaguarundi
Leopardus pardalis Ocelot
Puma concolor Puma
Artidactyla Peccaries and Deer
Mazama Americana Red brocket deer
Tayassu tajacu Collared peccary
Rodentia Rodents
Echimyidae
Dactylomys dactylinus Amazon bamboo rat
Nectomys squamipes Water rat
Proechimys semispinosus Spiny rat
Sciuridae Squirrels
Sciurus sp. Amazon red squirrel
Sciurillus pusillus Neotropical pygmy squirrel
Large Cavylike Rodents
Agouti paca Paca
Coendou bicolour Bi-color spined porcupine
Dasyprocta fuliginosa Black agouti
Hydrochaeirs hydrochaeirs Capybara
Myoprocta pratti Green acouchy
10.3 Class
Sauropsida
Lizards
Gekkonidae
Gonatodes concinnatus Collared forest gecko
Gonatodes humeralis Bridled forest gecko
Pseudogonatodes guianensis Amazon pygmy gecko
Gymnophthalmidae
Alopoglossus striventris Black-bellied forest lizard
Arthrosaura reticulata reticulata Reticulated creek lizard
Cercosaurra argulus
Cercosaura ocellata
Leposoma parietale Common forest lizard
Neusticurus ecpleopus Common streamside lizard
Prionodactylus argulus Elegant-eyed lizard
Prionodactylus oshaughnessyi White-striped eyed lizard
Iguanas
Hoplocercidae
Enyalioides laticeps Amazon forest dragon
Polychrotidae
Anolis fuscoauratus Slender anole
Anolis nitens scypheus Yellow-tongued forest anole
Anolis ortonii Amazon bark anole
Anolis punctata Amazon green anole
Anolis trachyderma Common forest anole
Scincidae
Mabuya nigropunctata Black-spotted skink
Tropiduridae
Tropidurus (Plica) plica Collared tree runner Tropidurus (plica) umbra ochrocollaris Olive tree runner
Teiidae
Kentropyx pelviceps Forest whiptail
Tupinambis teguixin Golden tegu
Snakes
Colubridae
Atractus elaps Earth snake sp3
Atractus major Earth snake
48
Atractus occiptoalbus Earth snake sp2
Chironius fuscus Olive whipsnake
Chironius scurruls Rusty whipsnake
Clelia clelia clelia Musarana
Dendriphidion dendrophis Tawny forest racer
Dipsas catesbyi Ornate snail-eating snake
Dipsas indica Big-headed snail-eating snake
Drepanoides anomalus Amazon egg-eating snake
Drymoluber dichrous Common glossy racer
Helicops angulatus Banded south american water snake
Helicops leopardinus Spotted water snake
Imantodes cenchoa Common blunt-headed tree snake
Imantodes lentiferus Amazon blunt-headed tree snake
Leptodeira annulata annulata Common cat-eyed snake
Leptophis cupreus Brown parrot snake
Liophis miliaris chrysostomus White-lipped swamp snake
Liophis reginae Common swamp snake
Oxyrhopus formosus Yellow-headed calico snake
Oxyrhopus melanogenys Black-headed calico snake
Oxyrhopus petola digitalus Banded calico snake
Pseustes poecilonotus polylepis Common bird snake
Pseustes sulphureus Giant bird snake
Sphlophus compressus Red-vine snake
Spilotes pullatus Tiger rat snake Tantilla melanocephala melanocephala Black-headed snake
Xenedon rabdocephalus Common false viper
Xenedon severos Giant false viper
Xenoxybelis argenteus Green-striped vine snake
Viperidae
Bothriopsis taeniata Speckeled forest pit viper
Bothriopsis bilineata bilineata Western Striped Forest Pit Viper
Bothrops atrox Fer-de-lance
**Bothrops hyoprora **Amazonian Hog-Nosed Viper
Lachesis muta muta Amazon Bushmaster
Boidae
Boa constrictor constrictor Red-tailed boa
Boa constrictor imperator Common boa constrictor
Corallus enydris enydris Amazon tree boa
Epicrates cenchria gaigei Peruvian rainbow boa
Elapidae
Micurus hemprichii ortonii Orange-ringed coral snake
Micrurus langsdorfii Langsdorffs coral snake
Micrurus lemniscatus Eastern ribbon coral snake
Micrurus spixii spixxi Central amazon coral snake
Micurus surinamensis surinamensis Aquatic coral snake
Crocodilians
Alligatoridae
Paleosuchus trigonatus Smooth-fronted caiman
10.4 Class
Amphibia
Caecilians
Typhlonectidae
Caecilia aff. tentaculata
Plethodontidae Lungless Salamanders
Bolitoglossa peruviana Dwarf climbing salamander
Bufonidae Toads
Rhinella marina Cane Toad
Rhinella complex margaritifer Crested Forest Toad
Rhinella dapsilis Sharp-nosed Toad
Dendrophryniscus Leaf Toads
Dendrophryniscus minutus Orange bellied leaf toad
Centrolenidae Glass Frogs
Centrolene sp. undescribed Glass Frog
Cochranella anetarsia Glass Frog
Cochranella midas Glass Frog
Cochranella resplendens Glass Frog
Dendrobatidae Poison Frogs
Ameerega bilinguis
Ameerega ingeri Ruby Poison Frog
Ameerega insperatus
Ameerega parvulus
Ameerega zaparo Sanguine Poison Frog
Colostethus bocagei
Colostethus marchesianus Ucayali Rocket Frog
Dendrobates duellmani Duellmans Poison Frog
Hylidae Tree Frogs
Cruziohyla craspedopus Amazon Leaf Frog
cf. Sphaenorhychus carneus Pygmy hatchet-faced Tree Frog
Dendropsophus bifurcus Upper Amazon Tree Frog
49
**Dendropsophus marmorata **Neotropical Marbled Tree Frog
Dendropsophus rhodopeplus Red Striped Tree Frog
Dendropsophus triangulium Variable Clown Tree Frog
Hemiphractus aff. scutatus Casque-headed Tree Frog
Hyla lanciformis Rocket Tree Frog
Hyla maomaratus
Hylomantis buckleyi
Hylomantis hulli
Hypsiboas boans Gladiator Tree Frog
Hypsiboas calcarata Convict Tree Frog
Hypsiboas geographica Map Tree Frog
Hypsiboas punctatus Common Polkadot Tree Frog
Hypsiboas geographica Map Tree Frog
Hypsiboas punctatus Common Polkadot Tree Frog
Osteocephalus cabrerai complex Forest bromeliad Tree Frog
Osteocephalus cf. deridens
Osteocephalus leprieurii Common bromeliad Tree Frog
Osteocephalus planiceps Flat-headed bromeliad Tree Frog
Trachycephalus resinifictrix Amazonian Milk Tree Frog
Phyllomedusa tarsius Warty Monkey Frog
Phyllomedusa tomopterna Barred Monkey Frog
Phyllomedusa vaillanti White-lined monkey Tree Frog
Scinax garbei Fringe lipped Tree Frog
Scinax rubra Two-striped Tree Frog
Trachycephalus venulosus Common milk Tree Frog
Microhylidae Sheep Frogs
Chiasmocleis bassleri Bassler's Sheep Frog
Leptodactylidae Rain Frogs
Edalorhina perezi Eyelashed Forest Frog
Prystimantis acuminatus Green Rain Frog
Prystimantis aff peruvianus Peruvian Rain Frog
Prystimantis altamazonicus Amazonian Rain Frog
Prystimantis conspicillatus Chirping Robber Frog
Prystimantis lanthanites Striped-throated Rain Frog
Prystimantis malkini Malkini's Rain Frog
Prystimantis martiae Marti's rainfrog
Prystimantis ockendeni complex Carabaya Rain Frog
Prystimantis sulcatus Broad-headed Rain Frog
Prystimantis variabilis Variable Rain Frog
Hypnodactylus nigrovittatus Black-banded Robber Frog
Strabomantis sulcatus Broad-headed Rain Frog
Engystomops petersi Painted Forest Toadlet
Leptodactylus andreae Cocha Chirping Frog
Leptodactylus knudseni Rose-sided Jungle Frog
Leptodactylus mystaceus
Leptodactylus rhodomystax Moustached Jungle Frog
Leptodactylus wagneri Wagneris Jungle Frog
Lithodytes lineatus Painted Antnest Frog
Oreobates quixensis Common big headed Rain Frog
Vanzolinius discodactylus Dark-blotched Whistling Frog
Ranidae True Frogs
Rana palmipes Neotropical Green Frog
10.5 Class
Arachnida
Araneae
Nephila clavipes Golden Silk Spider
Ancylometes terrenus Giant Fishing Spider
10.6 Class
Insecta
Coleoptera
Euchroma gigantea Giant Ceiba Borer
Homoeotelus d'orbignyi Pleasing Fungus Beetle
Scarabaeidae
Canthon luteicollis
Deltochilum howdeni
Dichotomius ohausi
Dichotomius prietoi
Eurysternus caribaeus
Eurysternus confusus
Eurysternus foedus
Eurysternus inflexus
Eurysternus plebejus
Grylloptera
Panacanthus cuspidatus Spiny Devil Katydid
Hemiptera
Dysodius lunatus Lunate Flatbug
Lepidoptera
Lycaenidae
Celmia celmus
Janthecla sista
50
Thecla aetolius
Thecla mavors
Colobura annulata
Colobura dirce
Nymphalidae
Apaturinae
Doxocopa agathina
Doxocopa griseldis
Doxocopa laurentia
Doxocopa linda
Biblidinae
Biblis hyperia
Callicore cynosure
Catonephele acontius
Catonephele esite
Catonephele numilia
Diaethria clymena
Dynamine aerate
Dynamine arthemisia
Dynamine athemon
Dynamine gisella
Ectima thecla lerina
Eunica alpais
Eunica amelio
Eunica clytia
Eunica volumna
Hamadryas albicornus
Hamadryas arinome
Hamadryas chloe
Hamadryas feronia
Hamadryas laodamia
Nessaea batesii
Nessaea hewitsoni
Nica flavilla
Panacea prola
Panacea regina
Paulogramma peristera
Phrrhogyra amphiro
Pyrrhogyra crameri
Pyrrhogyra cuparina
Pyrrhogyra cf nasica
Pyrrhogyra otolais
Temenis laothoe
Charaxinae
Agrias claudina
Archaeoprepona amphimachus
Archaeoprepona demophon
Archaeoprepona demophon muson
Archaeoprepona licomedes
Consul fabius
Hypna clytemnestra
Memphis arachne
Memphis oenomaus
Memphis philomena
Memphis offa
Prepona eugenes
Prepona dexamenus
Prepona laertes
Prepona pheridamas
Zaretis isidora
Zaretis itys
Cyrestinae
Marpesia berania
Marpesia crethon
Marpesia petreus
Danainae
Pieridae
Appias drusilla
Dismorphia pinthous
Eurema cf xanthochlora
Perrhybris lorena
Phoebis rurina
Danainae
Danaini
Danaus plexippus
Ithomiini
Aeria eurimidea
Ceratinia tutia
Hypoleria sarepta
Hyposcada anchiala
Hyposcada illinissa
Hypothyris anastasia
Hypothyris fluonia
Ithomia amarilla
Ithomia salapia
Mechanitis lysimnia
51
Mechanitis mazaeus
Mechanitis messenoides
Methona confusa psamathe
Methone Cecilia
Oleria Gunilla
Oleria ilerdina
Oleria tigilla
Tithorea harmonia
Heliconinae
Acraeini
Actinote sp.
Heliconiini
Dryas iulia
Eueides Eunice
Eueides Isabella
Eueides lampeto
Eueides lybia
Heliconius erato
Heliconius hecale
Heliconius melponmene
Heliconius numata
Heliconius sara
Heliconius xanthocles
Heliconius doris
Philaethria dido
Limenitidinae
Adelpha amazona
Adelpha cocala
Adelpha cytherea
Adelpha erotia
Adelpha iphicleola
Adelpha iphiclus
Adelpha lerna
Adelpha melona
Adelpha mesentina
Adelpha naxia
Adelpha panaema
Adelpha phrolseola
Adelpha thoasa
Adelpha viola
Adelpha ximena
Nymphalinae
Anartia amathae
Anartia jatrophae
Baeotus deucalion
Eresia eunice
Eresia pelonia
Historis odius
Historis acheronta
Metamorpha elisa
Metamorpha sulpitia
Phyciodes plagiata
Siproeta stelenes
Smyrna blomfildia
Tigridia acesta
Satyrinae
Brassolini
Bia actorion
Caligo eurilochus
Caligo idomeneus idomeneides
Caligo illioneus
Caligo teucer
Catoblepia cassiope
Caligo placidiamus
Catoblepia berecynthia
Catoblepia cassiope
Catoblepia generosa
Catoblepia sorannus
Catoblepia xanthus
Opsiphanes invirae
Haeterini
Cithaerias aurora
Cithaerias menander
Cithaerias pireta
Haetera macleannania
Haetera piera
Pierella astyoche
Pierella hortona
Pierella lamia
Pierella lena
Pierella lucia
Morphini
Antirrhea hela
Antirrhea philoctetes avernus Common Brown Morpho
Morpho Achilles
Morpho deidamia
52
Morpho helenor
Morpho Menelaus
Morpho peleides
Morpho polycarmes
Satyrini
Caeruleuptychia scopulata
Chloreuptychia agatha
Chloreuptychia herseis
Euptychia binoculata
Euptychia labe
Euptychia myncea
Euptychia renata
Hermeuptychia hermes
Sarota chrysus
Sarota spicata
Setabis gelasine
Stalachtis calliope
Stalachtis phaedusa
Synargis orestessa
Magneuptychia analis
Magneuptychia libye
Magneuptychia ocnus
Magneuptychia ocypete
Magneuptychia tiessa
Pareuptychia hesionides Pareuptychia hesionides
Pareuptychia ocirrhoe
Taygetis Cleopatra Cleopatra Satyr
Taygetis echo Echo Satyr
Taygetis mermeria
Taygetis sosis Sosis Satyr
Papilionidae
Battus belus varus
Battus polydamas
Papilio androgeus
Papilio thoas cyniras
Parides aeneas bolivar
Parides Lysander
Parides pizarro
Parides sesostris
Riodinidae
Amarynthis meneria
Ancyluris endaemon
Ancyluris aulestes
Ancyluris etias
Anteros renaldus
Calospila cilissa
Calospila partholon
Calospila emylius
Calydna venusta
Cartea vitula
Emesis fatinella
Emesis Lucinda
Emesis mandana
Emesis ocypore
Eurybia dardus
Eurybia elvina
Eurybia franciscana
Eurybia halimede
Eurybia unxia
Hyphilaria parthenis
Isapis agyrtus
Ithomiola floralis
Lasaia agesilaus narses
Lasaia pseudomeris
Leucochimona vestalis
Livendula amaris
Livendula violacea
Lyropteryx appolonia
Mesophthalma idotea
Mesosemia loruhama
Mesosemia latizonata
Napaea heteroea
Nymphidium mantus
Nyphidium nr minuta
Nymphidium lysimon
Nymphidium balbinus
Nymphidium caricae
Nymphidium chione
Pandemos pasiphae
Perophtalma lasus
Pirascca tyriotes
Rhetus arcius
Rhetus periander
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