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Conservation, Management and Expansion
of Protected and Non-Protected Tropical
Forest Remnants Through Population Density
Estimation, Ecology and Natural History of Top
Predators; Case Studies of Birds of Prey
(Spizaetus taxon)
M. Canuto, G. Zorzin, E. P. M. Carvalho-Filho, C.E.A. Carvalho,
G.D.M. Carvalho and C.E.R.T Benfica
S.O.S. Falconiformes,
Centro de Pesquisa Para a Conservação das Aves de Rapina Neotropicais,
Brazil
1. Introduction
Among the Accipitridae family, the genus Spizaetus is included in the group of the Booted
Eagles (Griffiths et al., 2007; Haring et al., 2007), which according to old taxonomic
classifications, was the most diverse, with 22 species that inhabited the tropical forests of the
New and the Old World (Brown and Amadon 1968, del Hoyo et al. 1994, Ferguson-Lees and
Christie 2001). Most specimens of this taxon are medium sized (1,100-1,600g), but there are
some exceptions which are smaller (S.nanus, 510-610g) or larger (S.nipalensis, 2,500-3,500g)
(del Hoyo et al. 1994, Ferguson-Lees and Christie 2001). The first description of the genus
Spizaetus was introduced by Vieillot in 1816, when he described the taxon S. ornatus (Haring
et al. 2007). This species, along with S.tyrannus, is found in the neotropical region, and both
are divided into two subspecies (Brown and Amadon 1968, Ferguson-Lees and Christie
2001). Only one species occurs in the African continent, while most of the species of this
genus are distributed throughout Southeast Asia (Haring et al. 2007). However, the
grouping of this genus based on comparisons of the external morphology and feather
patterns, according to traditional taxonomy, was refuted by a recent classification based on
genetic studies (Haring et al. 2007). These authors consider the genus as paraphyletic,
segregating the taxon into three distinct groups (Neotropical, African and Asian): while the
neotropical representatives maintained the genus name due to Vieillot’s first classification
(Spizaetus ornatus, 1816); the African representative was inserted in the genus Aquila and the
Asian ones renamed as Nisaetus.
Haring et al. (2007) and Griffiths et al. (2007) also evaluated the phylogenetic relationship of
the genus with two other neotropical taxons, Spizastur melanoleucus and Oroaetus isidori.
Although indicating that the archetypes from South America would not form a
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monophyletic clade, the authors adopted a more conservative classification, adding these
two species to the genus Spizaetus (Helbig et al. 2005, Haring et al. 2007, Griffiths et al. 2007),
which is the same taxonomy adopted by the AOU (American Ornithologist’s Union). Thus,
the genus would be represented by S. isidori, with distribution restricted to the Andes strip
extending from Venezuela to the far north of Argentina; S.tyrannus, S.ornatus and
S.melanoleucus, which are much more widely distributed through South America, including
almost all of Brazil (Sick 1997) and part of Central America (Blake 1977, Ferguson-Lees and
Christie 2001).
Even with phylogenetic uncertainties, these species have in common many ecological
characteristics which are important in terms of biodiversity conservation. They demand
large areas of well conserved forests (Jullien and Thiollay 1996, Thiollay 1989a,b, 2007,
Bierregard 1998, Canuto 2009), which characterizes them as “umbrella” species for their
environment (Newton 1979), when populations from other species, with smaller home
ranges are preserved in locations that support viable populations of these predators (Sergio
et al. 2006). These birds are also paramount for ecological balance, regulating populations of
their eventual prey (Newton 1979, Bierregard 1998, Watson 1998).
The loss of top predators, such as these hawk-eagles, may entail a large increase in meso-
predator release, affecting the populations of their prey and may even lead them to
extinction (Soulé et al. 1988, Terborgh 1992). Like other raptors, they are also good indicators
of environmental change (Newton 1979, Thiollay 2007, Seavy and Apodaca 2002, Carrascal
et al. 2008a, b, Carvalho and Marini 2007), as they are sensitive to anthropic disturbances,
including hunting and selective logging (Thiollay 1989a, 2007; Stotz et al. 1996).
Deforestation and fragmentation of tropical forests are this species’ main threats (Bierregard
1998, Bildstein et al. 1998, Thiollay 2007, IUCN 2010). Considering the rates of tropical
deforestation in the last few decades (Whitmore 1997), some taxons have become especially
vulnerable to local extinction.
The neotropical species, S. melanoleucus, S. ornatus and S. tyrannus, are much more widely
distributed throughout all of South America and parts of Central America (Blake 1977,
Ferguson-Lees and Christie 2001). These species have large populations in the Hylean
Amazon, thus contributing to the fact that they were not considered endangered in Brazil or
worldwide (Machado et al. 2008, IUCN 2010). However, they have become extremely rare
outside the Amazon domain (Sick and Teixeira 1979, Sick 1997“, Drummond et al. 2008).
The regional decrease of these taxons, due to the reduction of forest environments in
Southeastern Brazil, is made clear with their presence in state lists of endangered species in
Southeastern and Southern regions of Brazil (Bergallo et al. 2000, Silveira et al. 2009, Fontana
et al. 2003, Mikich and Bérnilis 2004, Simon 2007). As well as the deforestation of the
Atlantic rainforest “(SOS Mata Altântica e INPE 2010), which is identified as this species’
biggest threat, trapping and hunting are secondary contributors to the decrease of their
population status (Albuquerque 1995, Machado et al. 1998, Ribon et al. 2003).
Despite recent records in many localities of the Atlantic domain and in other areas of the
Cerrado (Kirwan et al. 2001, Azevedo et al. 2003, Manõsa et al. 2003, Ribon et al. 2003, Carlos
and Girão 2006, Joenck 2006, Olmos et al. 2006, Roda and Pereira 2006, Zorzin et al. 2006,
Dias and Rodrigues 2008, Carvalho Filho et al. 2009, Faria et al. 2009, Salvador-Jr. and Silva
Conservation, Management and Expansion of Protected and Non-Protected Tropical
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2009, Salvador-Jr. et al. 2011), there is no evidence about the reproduction of these species in
most areas where they were found. Also, there is a complete lack of substantial data on their
local density as well.
The best efforts of data collection on the biology and ecology of these taxons were
concentrated in areas of continuous forests in Guatemala (Flatten 1990, Julio et al. 1991,
Sixto, 1992, Montenegro 1992), the French Guyana (Thiollay 1985, 1989a,b Jullien and
Thiollay 1996, 2007) and in large forest fragments in Brazil (Canuto 2009, Manosa et al. 2002,
2003). Other works regarding territoriality and estimates of genus density usually include
collection of complementary data with the use of radio telemetry equipment (Manõsa and
Pedrochi 1997, van Balen et al. 2001 and Gjersshaug et al. 2004).
In some studies, such as Thiollay (1989a,b), Preulethner and Gamauf (1998), Whitacre et al.
(1992a) van Balen et al. (2001) and Canuto (2009), the authors estimated the density of pairs
and territoriality by direct observation of couples and individuals performing flight circuits
and aerial displays. Generally speaking, population census in preserved habitats of many
species of Accipitriformes – especially those that are more selective such as the individuals
of the Spizaetus genus – enable the prediction of the distribution of a specific population in a
mosaic of modified environments. This is how the regional or local status of the species may
be evaluated (Thiollay 2007). However, the lack of specific census that aim to evaluate more
precisely the density of these species in altered environments, does not permit further
inference on their local state of conservation in most of their current areas of occurrence.
Therefore, there is less information available on the dynamics of these species’ populations
in fragmented areas, such as the Southeast and Center-West regions of Brazil.
In the current chapter we describe the results of six studies conducted in the country by
analyzing the incidence of specimens of the genus Spizaetus in areas with different
fragmentation histories and considering the different population and reproductive
ecological aspects of these taxons collected at each locality. By analyzing each case study we
promote a reflection on the perspectives of local and punctual conservation of these species,
according to their ecological requirements. Thus, we used these species as “flags” to point
out the problems involving conservation of top predators, which present small density but
demand a large area, in fragmented and continuous areas.
2. Methods and study areas
For the study sites we present the different localities, including different regions of the
Cerrado and Atlantic Rainforest and their respective transition areas where different data
collections occurred. Later, these results are discussed in a regional context according to
previous results by the authors obtained from the Amazon biome and a second tropical
region (Central America).
In each case study specific methods were employed for census, mapping and monitoring of
these species according to Whitacre and Turley (1990), Thiollay (1989), Bibby et al. (2000),
Manõsa et al. (2003), Canuto (2009) and Granzinelli and Motta Junior (2010). These taxons
require an ample and specific sample effort, as they are highly territorial birds that occur in
low density and occupy extensive territories. However, these methods were applied
differently according to the focus of each study by different authors, thus involving different
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sampling parameters according to the environment, conditions of region preservation and
the logistics involved. The methods are described below:
i. Observations through point counts: This method consists of recording species from a
fixed observation point during a pre-established period, over a large time-scale,
involving different seasons. It was used to evaluate the density, frequency of occurrence
and incidence of pairs and individuals of the focus species in the sampling areas. For
the density estimates, we used a fixed observation radius, and for calculating the
frequency of occurrence, all individuals accurately identified within the range of
observation were considered. Each point should allow an ample field of vision, and
observations were made with the aid of binoculars 10x42 Nikon and a spotting scope
(20-60x), during a specific period of time that varied between 4 and 5 hours, beginning
first hours of the day.
ii. Data collection by routes: This technique was used to estimate the frequency of
occurrence of the species, as well as to identify new areas of use and nesting. Surveys
were conducted in roads, slowly driving a vehicle, as well as in rivers with a motorboat
or boat, or on foot in paths in the surrounding and interior areas of the remaining
forests.
iii. Spot mapping: According to Bibby et al. (2000) and Sutherland (2004), this technique
consists of mapping the movements of the individuals from observations made from
fixed points, including use of climbing techiniques for point counts within the forest
canopy. All the movements and routes of individuals of these species were recorded,
followed by the representation of these movements and activities on a digital map of
the area. After the identification of active territories or breeding sites, various
observation points were distributed in the area defended by the resident individuals.
The more repetitions performed within these territories, the more accurate are the
estimates of displacement, therefore confirming which sites were occupied or
defended. The birds observed were usually identified by the imperfections in the
flight feathers (remiges and rectrices) and patterns of plumage (adult, sub-adults or
youngsters). Other points in the surrounding area of the occupied territories and
adjacent ones were scouted with the objective of verifying the overlap of territories or
unoccupied areas.
As previously described, differences occurred in the use of these methods according to the
intrinsic characteristics of each area, logistics, and the objectives of the following studies:
Case Study 1 “Density of the representatives of the genus Spizaetus in remaining
continuous Atlantic Rainforest in the east of the state of Minas Gerais, Brazil”
Case Study 2 “Estimates of territoriality, incidence of couples and reproduction sites of
Spizaetus tyrannus in the south of the state of Minas Gerais, Brazil”
Case Study 3 “Estimates of territoriality, incidence of couples and reproduction sites of
Spizaetus melanoleucus in Atlantic Rainforest fragmented areas in the east of the state of
Minas Gerais"
Case Study 4 “Density and territoriality of Spizaetus ornatus in the Araguari river valley,
Triângulo Mineiro Region”
Case Study 5 “The effects of fragmentation of the Atlantic Rainforest on the richness
and abundance of Accipitriformes in the region of Viçosa, Minas Gerais”
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3. Results
3.1 Case study 1
“Density of the representatives of the genus Spizaetus in remaining continuous Atlantic
Rainforest in the east of the state of Minas Gerais, Brazil”
The Doce River State Park (Parque Estadual Rio Doce - PERD) is the largest Atlantic
Rainforest park in Minas Gerais, with an area of 35.976,43 ha, and 120 km in perimeter. The
reserve is located in the Doce River Valley, eastern part of the state, between the 42o 38’W
and 48o 28’W meridians and the 19o 45’S and 19o 30’S parallels, with an altitude varying
between 230 and 515m. The reserve has as important landmarks, the limits of the Doce and
Piracicaba rivers, to the east and northeast respectively (Hirsch 2003a).
The PERD vegetation belongs to the lower montane Atlantic Rainforest formation (Rizzini
1979) and is composed by a mosaic of primary and secondary forests (Ferreira and Marques
1998) classified as Semi Deciduous Forest (Viana 2001). The reserve has a freshwater system
of 38 to 44 lagoons which amounts to 3,529.7 ha (approximately 6% of the total area).
For the Spizaetus density estimates (Table 1), the spot mapping method was used registering
the routes of the three species of this genus. The results were obtained according to the
occupation of the species within the 12 sampling plots, a total of 21,400 hectares. These
records attested to the presence of pairs in reproductive activity or that were actively
nesting. It was collected 126 samples between 2006 and 2009, concentrated between the
months of July and January. There were 1 to 4 fixed observation points in each plot, inside
the reserve and border. These points occurred on the canopy of emerging trees (n=23 / 83
sample repetitions), with the use of climbing techniques, and also in open areas throughout
the border of the reserve (N=10 / 43 repetitions). All 33 points had a mean distance of 831m
(±514m), the minimum distance being 100m and the maximum 2 km between the points.
These sets of fixed points were sampled from 07:30 to 12:00. The mean distance between
plots, each one with 1-4 point counts, was 5.3 km (±2.2 km), and varied between 2.2 and 9
km. All points had a wide viewing angle, between 1200 to 3600, mean 2600 (± 64), which
enabled an evaluation of the occupation or defense of the plots by aerial and territorial
displaying individuals. This was determined by the recordings of couples engaged in
reproductive behavior or in defense of the plots, thus generating a density estimate of the
minimum number of couples inside the reserve’s boundaries. The plot was considered
occupied when a minimum of two records on couples took place. This estimate does not
include subordinate birds, immatures, wandering individuals with no defined territory, and
individuals not reproductively active, as predicted by Meunier’s “reservation population”
(1960). Methods i, ii and iii (see methods and study area sections) were applied during the
study, with a total of 567 hours of direct observation.
For the Spizaetus tyrannus species, records of territories occupied by pairs were inexistent, so
clear patterns of territoriality were not obtained. However, the species’ incidence in the plots
is still considered because of the random records of individuals presenting the territorial
behavior.
A minimum number (Table 1) of 4 pairs of the Ornate Hawk-eagle (S. ornatus) in 21,400 ha,
and 6.7 pairs in 36,000 hectares of the PERD was estimated, with a density of approximately
1 pair per 5,373 hectares. For the Black-and-white Hawk-eagle (S. melanoleucus) five plots
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had records of matched pairs in 21,400 ha (12 sampling plots), generating a minimum
estimate of 5 pairs in 21,400 ha, and 8.4 pairs of the species in 36,000 ha, with an
approximate density of 1 pair per 4,285 hectares. For the Black Hawk-eagle (S. tyrannus), 4
plots had individuals recorded, being those characterized by territorial defense behavior, as
soaring flights along with vocalizations specific to the species. This generated an estimate of
a minimum of 4 pairs in 21,400 hectares, and 6.7 pairs in 36,000 hectares of the PERD, with a
density of approximately 1 pair per 5,373 hectares, similar to the first species. Therefore, S.
melanoleucus was considered the most abundant species in this Atlantic Rainforest reserve of
semideciduous seasonal lowland of 36,000 hectares, more than 40 lake formations, and three
watersheds, as well as the Doce River, along the eastern limits of the reserve, and the
Piracicaba River, along the northern limits.
3.2 Case study 2
“Estimates of territoriality, incidence of couples and reproduction sites of Spizaetus tyrannus
in the south of the state of Minas Gerais, Brazil”
For this study, three sites were evaluated (Table 1), two located between the municipalities
of Ibertioga, Juiz de Fora and Itutinga (Study Sites 1 and 2), and one in the municipality of
Capela Nova (Study Site 3), all of which are in the state of Minas Gerais (200 49’S - 210 34’S -
440 13W 430 24’W). The region has remnants of Atlantic Rainforest, which are concentrated
on the slopes and hilltops. It also has tracts of Cerrado vegetation, with modifications due to
agriculture. The region’s altitude varies between 780 to 1,200 meters ASL. It is characterized
by seasonal, semi-deciduous forests associated to Cerrado vegetation, with field areas with
anthropogenic interference and areas of aquatic environment. The municipality of Capela
Nova is characterized by a mosaic of forest fragments on hill tops and depressions, pasture
areas, rural properties and river valleys, as well as rocky formations on forested slopes.
Photo 1. Black hawk-eagle nest with young. Photo credit: Eduardo Pio Carvalho
The three sites are located to the south of the state capital, Belo Horizonte, and are near or
part of the Serra da Mantiqueira mountain chain.
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For case study 2, the methods included direct observation of the species using fixed points
of variable radius in accordance with Whitacre and Turley (1990), Whitacre et al. (1992a) and
Canuto (2009), in landscape vantage points such as hill crests (sites 1 and 2). An observation
platform was also used in a tree canopy (site 3), with ascension techniques for the
monitoring of a nest (Photo 1). To avoid influences on the individual’s behavior, a blind tent
was used, in such a way that the nesting couple could not see the observers most of the time.
The different areas were monitored by at least quarterly visits for collecting data on the
reproductive biology, monitoring of the reproductive sites or active nesting and,
consequently, evaluating the patterns of territoriality. In the nesting area monthly visits
were carried out.
In sites 1 and 2, two pairs were monitored, 23 km apart, through methods i, ii, and iii. Both
pairs presented display or territorial defense behavior in both areas in the years of 2007 and
2008. In both cases the forests were considered of late secondary succession and had distinct
strata. Movements and territoriality patterns were characterized in displacements of up to
1.6 km. On one occasion, 3 individuals were sighted in one of the areas, which could have
been a couple and a youngster. Both areas are characterized by forested slopes or hilltops on
rugged terrain.
In site 3 a nest was identified (Charles Moreira, personal communication) inside a ravine in
a small drainage basin at an altitude of 776 meters, in a secondary fragment in intermediate
stage of regeneration. Starting at this point, specimens used a route along the ravine valley
to exit and enter the nest as well as other points. The patch is approximately 175 hectares in
size and is inserted in a mosaic of larger and smaller forest patches in a region of river
valleys with some local agropastoral pressure. The nest was on an Angico tree
(Anadenanthera sp.) at a height lower than 20 meters. The tree is located 400 meters from the
Piranga River and 700 meters from a stream. Its circumference at breast height (CBH) is
1.40m.
3.3 Case study 3
“Estimates of territoriality, incidence of couples and reproduction sites of Spizaetus
melanoleucus in Atlantic Rainforest fragmented areas in the east of the state of Minas Gerais”.
Eastern Minas Gerais, precisely the middle Doce river basin, is located between parallels
18°45' and 21°15' S and meridians 39°55' and 43°45' W, comprising a drainage area of about
83,400 sq. km, of which 86% belongs to the state of Minas Gerais and the remaining area to
Espírito Santo. In its southern border is the Paranaíba do Sul river basin, and in the west the
São Francisco river basin, as well as some of the Grande river. In the north, it borders the
Jequitinhonha and Mucuri river basins and in the northeast the São Mateus river basin. The
average annual precipitation varies from 1,500 mm, in the springs located in the
Mantiqueira and Espinhaço mountain ranges, to 900 mm, in the region of the city of
Aimorés, increasing towards the coast.
The study areas were the Doce River State Park and surroundings (Case study 1), the
Private Reserve of the Feliciano Miguel Abdala Natural Patrimony in Caratinga, the
municipalities of São José do Mantimento and São Pedro do Suaçuí, and a district near the
city of Governador Valadares, Baguari, all of which are in the middle Doce river watershed,
in the state of Minas Gerais. In these areas, the presence of active or inactive nests of S.
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melanoleucus, or incident couple, were documented. Patterns of territoriality and distance
estimates (Table 1) were obtained according to the spot mapping method. Also, data was
collected on the reproductive biology of the species. Methods i, ii and iii were used.
In the first area, located in the Doce River State Park and surroundings (see Case study 1),
two nests were found and tracked. One inside the reserve (Canuto 2008b), located on a pink
Jequitiba tree (Cairina legalis – CBH 291cm) at a height of 37 meters and at a distance of
about 800 meters from the border. It was located at the base of the hill among different
ravines or drainage systems, near a ridge of approximately 250 meters in altitude and about
770 meters away from the Turvo stream.
A second nest (Fabiano R. de Melo, personal communication) was studied around the same
location in a hillside forest patch in a dry valley of approximately 1,700 hectares, which is
located 2 km away from the Mumbaça stream, border of the PERD. This nest was 13 km
away from the first nest. The patch was isolated from the reserve by Eucalyptus crops and
open areas. The nest was located on an Arara Nut Tree (Joannesia sp.) of approximately 35
meters in height. Displacements up to 3.5 km were mapped in both areas.
In the second area, a nest which was already known (Fernanada Tabacow, personal
communication) was visited and found to be active (Photo 2) in the municipality of
Caratinga, which has protected semidecidual forests of 1,000 hectares in size. The nest was
on a Zeyheria cf. tuberculosa of 51 meters in height and CBH 2.7 meters. This nesting tree is
located at an altitude of 700 meters, also along forested ridges and valley depressions. The
location of the nest provides a broad view of the depression. The tree is 1.7 km away from
the Manhuaçu river. Displacements of up to 1.5 km were mapped. This area is located at a
distance of 75 km from the first two nests mentioned.
Photo 2. Black-and-white Hawk-eagle nest with young. Photo credit: Marcus Canuto
In the third area, near the city of Governador Valadares, the nest was on an emerging tree
(≥30 meters) located at the crest of a hill, 280 meters in altitude, near many slopes and
depressions, and at a distance of 1.73 km from the Doce river. The tree was beside a small
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portion of native vegetation on top of the hill, even though the environment is dominated by
Eucalyptus sp. plantations (approximately >60%). The tree was not measured. The species
had been previously recorded by different observers on an island with mature trees (>30m),
in a nearby area, 8 km away from the nest, which had not yet been discovered at the time.
After the island was flooded by a hydroelectric company, the couple was recorded on a
monthly basis around the nest area for a period of 8 months before evidence of nesting was
confirmed. Displacements of up to 4 km were mapped. The area used by the specimens
throughout the months amounts to 1,293 hectares of Eucalyptus, streams, native vegetations
and environments inhabited by man.
Another nest of the same species was found in 2001 (Marcelo Vasconcelos personal
communication) in the northern region of the Doce river basin, in the municipality of São
Pedro do Suaçuí, a more dry and arid region. This nest was located 900 meters away from
the margins of the Suaçuí Grande river. The area was revisited in 2010, where an individual
was recorded 7.5 km away from the previous nesting tree; however, the structure of twigs
was no longer present. At the same location, an adult individual of the species S. tyrannus
was recorded. This area is located at approximately 95 km northwest of the Governador
Valadares nest.
To the east of the Doce river basin, a couple was sighted in São José do Mantimento,
showing courtship or territorial defense behaviors, as observed by the vocal emissions and
diving or dashing against each other over the course of two days. This was recorded in a 966
hectares forest patch that is located at the margins of the José Pedro river. This site is
approximately 30 km southeast of the Caratinga nest.
3.4 Case study 4
“Density and territoriality of Spizaetus ornatus in the Araguari river valley, Triângulo
Mineiro Region”
The Araguari river source is located in the Serra da Canastra national park in the
municipality of São Roque de Minas and covers an area of approximately 2185 ha, with an
extension of 475 km. The vegetation above the river gorge, such as the remnants of the
Cerrado latu sensu, were heavily modified due to the creation of extensive pastures and
the modernization of agricultural techniques of edaphic correction, geared towards the
production and exporting of grains (Ferreria et al. 2005). Enclaves of Atlantic Rainforest
are concentrated along the valley, where the rugged topography has limited the advance
of agropastoral activities, with some patches remaining somewhat isolated on steeper
slopes. However, the implementation of the hydroelectric power plants of Nova Ponte,
Miranda and Amador Aguiar I and II eradicated the riparian vegetation and contributed
to the disfigurement of the remaining vegetation physiognomy, such as the deciduous
forests.
Estimates of vegetation coverage and the use of the soil in the valley’s area point to few
areas occupied by deciduous forests, riparian vegetation and savannahs (19%), all in
secondary stages, with the largest part of the area used for pastures (50%) and other annual
cultures (31%) (Rosa et al. 2006). The region’s climate is of the Aw type, according to
Köppen’s classification, which is characterized by a dry period, from the months of April to
September, and a humid period between the months of October to March (Rosa et al. 2006).
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The valley’s altitude varies between 500 and 950m, and the slope percentage varies between
20 and 80%.
To protect the few remaining areas of native vegetation, the Pau Furado State Park was
created, located between the municipalities of Araguari and Uberlândia, and established as
a compensatory measure for the Amador Aguiar I and Amador Aguiar II hydroelectric
power plants. The area includes 2.200 ha, covered by remnant forests in different stages of
succession. It’s the first conservation unit of this category located in the Triângulo Mineiro
Region, and one of the areas in the state that has been most affected by deforestation
throughout the years.
Photo 3. Ornate Hawk-eagle nest Photo credit: Eduardo Pio Carvalho
After the year 2005, when a few sporadic contacts with S. ornatus and S. tyrannus occurred in
the Araguari river valley, another two years of efforts were carried out with the objective of
finding the reproductive sites of these species and mapping the distribution of these taxons
in an area of approximately 700 sq. km, including part of the valley and adjacent areas.
Some contacts occurred randomly during field work done in the site in 2005, while other
records were obtained during surveys carried out in the area in the following two years,
when survey methods by transit and fixed point observations and spot mapping were used.
Several recordings occurred during car trips and motorboat trips on the Araguari river.
Many observations were randomly performed throughout the valley, with an average time
of 4 hours of observation (08 am – 12 pm). The selected sites had a field view of at least 150
degrees and were located on hilltops with an ample view of the valley. Through direct
observations, the routes of individuals or matched pairs were mapped when it was possible
to distinguish the individuals by imperfections in their flight feathers and describe distinct
territories. Additional observations were performed after the identification of the occupied
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areas to better map the individuals. Other points were established among the identified
territories in order to identify possible overlapping territories or unoccupied areas.
Through mapping, pairs of S. ornatus were recorded in an area of 70.000ha. Their activities
were concentrated around the two largest remaining forest areas in the region, of
approximately 1.000 ha, and a distance of 21 km between them (Table 1). In one of these
areas we found an active nest in 2006. The area is characterized by secondary vegetation
with some patches in initial stages and others more advanced, and with a few emerging
trees, including patches of Cerrado. The nest was built on a Copaiba (Copaifera langsdorffii)
with approximately 23m in height and a CBH of 2.07m. The tree was located 1.9 km from
the Araguari river, 40m from a small stream and 27m from a pasture in the valley. During
the reproduction period we observed displacements of at least 4.5 km from the nest. In the
other forest fragment no nests were found; however, a pair was observed performing
courting flights and vocalizations. The records of S. tyrannus in the valley can be
summarized by two isolated contacts with adult individuals.
3.5 Case study 5
“The effects of fragmentation of the Atlantic Rainforest on the richness and abundance of
Accipitriformes in the region of Viçosa, Minas Gerais”
This effort was focused between the municipalities of Viçosa, Paula Cândido and Cajuri, in
the mesoregion of the “Zona da Mata” in Minas Gerais, which covers an extension of 100 sq.
km, between the parallels 20o 42’ 30”and 20o 50’ 00” S and 42o 48’ 45”and 42o 56’ 15”W. The
original vegetation is part of the Sub-montane Semideciduous Forest formation (Oliveira-
Filho and Fontes 2000), characterized by the seasonal loss of 20 to 50% of tree leaves, and by
an altitude of 300 to 700m.
In 1817, the region was covered by primary forests, with small secondary patches due to
subsistence farming of indigenous peoples and isolated farming activities (Ribon et al. 2003).
The effective occupation of the Forest Zone began with the introduction of coffee plantations
in the Parnaíba river basin in Minas Gerais, around mid-19th century, with the occurrence of
widespread destruction and fragmentation of the landscape, caused by the creation of
extensive plantations (Valverde 1958). Following the coffee plantations, cattle ranching
expanded as the crop became unproductive, and the plantations became pasture grass
(Melinisminutiflora) (Resende and Resende 1996).
The coffee cycle ended in the first decades of the 20th century, which probably led to the
regeneration of various forest fragments from old abandoned crops (Ribon et al. 2003). Thus,
many fragments in the region of Viçosa have between 20 and 60 years of regeneration
(Ribon et al., 2003). According to the latest expectations, the area´s forest cover reaches 20%
(Zorzin 2011), with fragments concentrated on slopes and hilltops, rarely on lowlands and
caves, and practically none with watercourses in their interior (Ribon 1998). Most of these
remaining fragments are no larger than 50ha and few cover an area superior to 300ha. Even
with the regeneration of many fragments, they are still exposed to distinct anthropic
disturbances, such as fire, invasion by domestic cattle and selective logging (Ribon et al.
2003, Silva Júnior et al. 2004), while many also have their area reduced by the implantation
of small cultures (personal communication).
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Currently, the landscape matrix has different uses, such as coffee plantations of various
extensions, other crops to a lesser extent (such as corn, rice and beans), small eucalyptus
(Eucalyptus spp.) plantations, pastures and secondary forests (Ribon et al. 2003).
For the recording of medium and large sized Accipitriformes, we used fixed observation
points and trajectory surveys. The selection of points was based on a PRISM/ALOS satellite
image with a 2.5m resolution. We selected 25 points that had distances longer than 800m
from other points and offered a different field view from these. The shortest distance
between selected points was 820m and the average minimum distance was 1.714 km.
These points were selected during two seasons, according to the Brazilian species´
reproductive cycle (Sick 1997, Carvalho-Filho et al. 1998, 2005, 2006, 2009, Ferguson-Lees
and Christie 2001, Zorzin et al. 2004, Azevedo et al. 2006, Canuto 2008b, Canuto2009). The
first sampling was concentrated between December of 2009 and February of 2010, which
corresponds to the end of the reproductive period, when it was possible to record the
dispersal of the youngsters; the second period occurred between the months of August and
November of 2010, which includes reproductive activity such as pairing of mates, courting
flights and incubation.
Observations at the points occurred for five hour periods, from 7 am to 12 pm. The transit
observations were conducted in the interior and outskirts of the region´s 35 remaining forest
fragments.
After reviewing Ribon et al (2003), Zorzin (2011) attested to the local extinction of S.ornatus
and S.melanoleucus. These species were previously considered as critically endangered in the
region by Ribon et al. (2003). The only species observed by Zorzin (2011) was S.tyrannus,
when a minimum number of 3 adults, identified by imperfections in the remigi, were
estimated in an area of 10,000ha (Table 1). One of these birds was recorded at points
distanced by 10 km. Zorzin (2011) also analyzed the landscape´s influence, in different
scales, on the abundance of S. tyrannus in the region, analyzing the presence of this species
in 35 fragments. This author found significant correlations (p<0.01) between the species
abundance and the sizes of the remaining forest areas. Using buffers of 500, 1000, 1500 and
2000m, this author also found significant correlations between the abundance of the taxon
and the percentage of forest cover around the fragments, the amount of nuclear area and the
average size of the remaining fragments of the landscape. On the broadest scale adopted,
the 2000m radius, the abundance of the species showed significant negative correlation
(p<0.05) to the average isolation of the surrounding fragments.
4. Discussion
For the case studies conducted in the Atlantic Rainforest and transition areas, according to
territoriality estimates for the genus corresponding to Table 1, we were able to evaluate the
incidence of the group in forest patches of at least 179 ha for S. tyrannus nests, and of 840-
1.000 hectares for the incidence of couples and nests of S. melanoleucus and S. ornatus in areas
with intense history of fragmentation. It is clear that their protection should be a priority, as
well as of small, medium and large Atlantic Rainforest fragments, to create wildlife
corridors which guarantee the existence of refuges and source or dispersal areas (see
Laurance et al. 1997). However, most of what is left of the Atlantic Rainforest is found in
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small forest fragments <100ha (Ranta et al. 1998; Ribeiro et al. 2009) which are isolated from
each other and composed of portions of secondary forests in recent or medium regeneration
stages (Viana et al. 1997, Metzger 2000, Metzger et al. 2009 In Ribeiro et al. 2009). Therefore,
the pressure caused by deforestation of the genus in the Atlantic Rainforest is still present,
whereas the process or history of deforestation in the biome is prior to the 20th century.
Bibliography Estimates S. tyrannus S.melanoleucus S. ornatus
Dist. among Terriotries x 6.9±1.5 Km 6.9±1.5 Km
Min imum Movemen t x 4,7 km 6.7 km
Density Estimate in PERD 1 pair/5373 ha 1 pair/4285 ha 1 pair/5373 ha
Distance between nests x 13 km x
Minimum Defended Territory 729 ha x x
Min imum movement 1.6 km x x
Dist. among Terriotries 23 km x x
Forest site occupied x 840 ha x
Dist. among Nests x 13 km x
Min imum Movemen t x 4 km x
Forest site occupied x x 1000 ha
Dist. among Terriotries x x 21 km
Movement x x 4.5 km
Density Estimate x x 2 pair/70000 ha
Min imum Movemen t 1 0 km x x
Density Estimate 3 individuals /10000 ha x x
Territory x 925 to 1090 ha 1375 ha
Density Estimate x 2 pair/4200 ha 4 pair/10000 ha
Maximum territory size x 4200 to 5800 m 3000 to 6900 m
Dist. be tween nests x x 3 .5 km
Territory x x 977 to 1315 ha
Max. movement from nest x x 5 km
Nest density x x 1/787 ha
Male territory 1090 ha x x
Female territory 1450 to 2470 ha x x
Sixto (1992) Max. Movements from nest by female 3 km x x
Female territory x x 256 to 2100 ha
Max. Movements from ne st by female x x 5 km
Max. Movemen ts from nest by ma le x x 3.3 km
Joenck (2006) Density estimate 2 indiv./4500 ha x x
Density Estimate 1 pair/2960 ha x 1 pair/4440 ha
Dist. a mong Terriotries 5.7 km x 7 .9 km
Minimum Density Estimate, Distance among Nests, Territory and Movement for Spizaetus in the N eotropics
Julio (1991 )
Thiollay (1989 a)
Stud
y
case 1
(Canuto 2009)
Study ca se 2
Study ca se 3
Study ca se 4
Canuto (2008)
Study ca se 5
Montenegro (1992)
Flatten (1990)
Table 1. Case studies and literature on estimates and patterns of nesting and individuals
densities, specimen movements, telemetry gear data and territoriality among Spizaetus.
In the study areas, the use of large trees for nesting by the species S. melanoleucus (N=4) and
S. ornatus (N=3) is evident. The location of the reproduction sites for the three species of the
genus also coincided with areas of rugged terrain, valleys and forested ravines, which are
favorable for isolation or areas with difficult access for human activities, according to Silva
et al. (2007) (Figure 1, Photo 2 and 3).
In areas with patches of 6,000 to 12,000-36,000 ha, in contiguous or protected remnants, it is
possible to perceive the incidence of the three different species in the same fragment. It is
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also possible to observe population patterns, regarding the defense of different neighboring
areas, through mapping and reproductive behavior. These may be considered to be refuges
for reproductively active populations, although they are isolated at a regional level. Only
large fragments with mature forests are capable of preserving sensitive species, especially
those with large area requirements (Ferraz et al. 2007) or with strict habitat requirements,
whose survival is particularly problematic in the present fragmented state (Aleixo 1999;
Ribeiro et al. 2009). Therefore, these species, though present in extensive or contiguous
forest environments, have low density and are naturally rare in the landscape, according to
characteristics that are sparse in the environment, (for example Nesting areas; photo 4,
Newton 1979). Thus, these ecological parameters make them even more susceptible to
fragmentation (Laurance et al. 1997, Henle et al. 2004).
Photo 4. Black-and-white hawk-eagle nesting site. Photo credit: Marcus Canuto
Fig. 1. Map of Spizaetus records in the Atlantic Rainforest; squares indicate records of pairs,
circles indicate nests and diamonds indicate records from cited literature. Big stars indicate
the incidence of the three species of Spizaetus (yellow), or of two, S. ornatus and S. tyrannus
(brown with black), and S. tyrannus and S. malanoleucus (white with black). Small stars
indicate records of species in this study. In general, white is for S. malanoleucus, black is for
S. tyrannus and brown is for S. ornatus. Scale: 1:10685101.
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The distance of 25 km from most remaining fragments of Atlantic Rainforest to its largest
reserves (Ribeiro et al. 2009) presents serious conservation problems even for medium sized
birds according to the patterns and estimates of movement and density presented (Table 1).
According to the biometrics of the nesting trees previously discussed, we observe a
tendency of the species S. melanoleucus in using emergent or mature trees in inland Atlantic
Forest and transition areas, as does S. ornatus. For S. tyrannus, according to Sixto (1992) and
the nest monitored, the species used medium sized trees (20-25m) for nesting. According to
case study 3, in the highly fragmented region of Governador Valadares, an active Spizaetus
melanoleucus’ nest was located in an area mostly covered by Eucalyptus sp. The nest was
located in a fragment of approximately 1,293 hectares, with an area roughly evaluated to be
70% covered by Eucalyptus. However, the presence of an emerging tree for nesting, isolated
from the rest of the vegetation, in a drainage system of difficult access, near extensive bodies
of water and riparian vegetation, are probably decisive factors in the occupation of this
territory. The population maintenance of these species depends on creating or increasing
wildlife corridors, due to the large life area required by the taxon. A better evaluation is
needed on the dispersion pattern of adults and youngsters throughout the various
fragments in a mosaic of altered environments, as well as the selection of nesting areas (see
Table 2).
Study case
Species Record
Site Forest site of the
record Landscape Featu res Habitat
1 and 3
S. melanoleucus Nest
Baixa Verde MG 1700 ha Forested slope, valley and lakes Tall protected forest
1 and 3
S. melanoleucus Nest
PE Rio Doce MG 36000 ha Lowland forest, small valleys and lakes Tall protected forest
2
S. tyrannus Pair
Ibertioga MG x Slope, valleys and forested hill tops Late seconday growth
2
S. tyrannus Pair
Ibertioga MG x Slope and forested hill tops Late seconday growth
2
S. tyrannus Nest
Caranaíba MG 179 ha Valeys and forested hill tops Early secondary growth
3
S. melanoleucus Nest
Governador Valadares MG 1293 ha Lowland forest, Eucalyptus plantations and valleys Early secondary growth
3
S. melanoleucus Nest
São Pedro do Suaçuí MG x Valeys and forested hill tops Early secondary growth
3
S. melanoleucus Nest
RPPN Miguel Abdala, Caratinga MG 1000 ha Valeys and forested hill tops Tall protected forest
5
S. ornatus Nest
Uberlândia MG 1000 ha Forested valley Early secondary growth
5
S. ornatus Pair
Uberlândia MG 1000 ha Forested valley Early secondary growth
6
all 3 Spizaetus Incidence
PN do Pau Brasil, Porto Seguro BA 12000 ha Lowland forest with valley formations Tal l protected forest
6
all 3 Spizaetus Incidence
Estação Veracel 6000 ha Lowland forest with valley formations Tall protected forest
6
S. melanoleucus Pair
PN do Pau Brasil, Porto Seguro BA 12000 ha Lowland forest with valley formations Tal l protected forest
Pers. c omm. 1
S. tyrannus Pair
Antônio Dias x Slope, valleys a nd forested hill tops Late seconday growth
Pers. c omm. 2
S. tyrannus Pair
São Bartolomeu/Ouro Preto MG 2846 ha Slope, valleys and forested hill tops Early secondary growth
Pers. c omm. 3
S. tyrannus Pair
Serro MG x Cerrado of altitude, deciduous and s emideciduous forest Early secondar y growth
x
S. melanoleucus Pair
Além Paraíba MG 840 ha Valeys and forested hill tops Late seconday growth
x
S. tyrannus Pair
Camanducaia MG 410 ha Montane forest and slope Late seconday growth
x
S. tyrannus Young and adults
Nova Lima, MG 343 ha Monatne forest, valleys and forested hill tops Late seconday growth
x
S. melanoleucus Pair
São José do Mantimento MG 966 ha Lowland forest and valleys Early secondary growth
x
S. ornatus Nest
Matozinhos MG 900 ha Cerrado, deciduous and semideciduous forest Early secondary growth
Forest site of the record: it was only considered the fragment of the nest or from where individuals appeared, and not the surrounding ones.
Characterization on areas of nests and records on pairs
Table 2. Characteristics of some of the areas, and records used in the case studies to illustrate
area sizes in hectares whereas records of the three species took place. Personal
communication 1 (Gustavo Pedersoli); personal communication 2 (Frederico Pereira de
Castro Andrade); personal communication 3 (Estefane N. L. Siqueira).
For S. ornatus and S. tyrannus, case studies 2 and 4, the density estimation is lower in
fragmented areas. There are two couples with approximately 20 km between them. In
extensive fragments, there are two couples every 5.3-13 km, according to mapping and
estimations for the three species (case study 1; Canuto 2008a). According to Ribeiro et al.
(2009) the average isolation between forest fragments along the Atlantic Rainforest
extension is 1.4 km, varying from a few meters to dozens of kilometers. By removing
fragments smaller than 50 hectares from the equation, the isolation between fragments
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increases to 3.5 km, and by removing fragments up to 200 hectares, this average isolation
becomes 8 km.
Therefore, the existing and continuous fragmentation of the biome has isolated populations
and individuals, and is still continuously depleting prey resources and top predator
populations (according to Newton 1979, Thiollay 1989a, 2007). Jullien and Thiollay (1996), in
the French Guiana, after extensive sampling with various habitats and gradients of
anthropogenic degradation, described the decline and loss of forest species and their
substitution by more generalist and open habitat species.
According to Harestad and Bunnell (1979), Schoenerand and Schoener (1982), and Kennedy et
al (1994) cited in Perry (2000), the interspecific variations in the life size areas, which were not
evaluated in this study, have also been correlated to age, sex and seasons. Therefore, according
to Table 1, the differences between values derived from the different methods, environments,
ecological patterns and specimens. However, we emphasize that, regardless of the differences,
there is evidence of great dislocations in kilometers in fragmented and continuous
environments, low density of the species in the area and reproduction sites in all the studies.
There is also incidence of the species in environments or sites that have characteristics such as
isolation, difficult access (rugged topography), and the presence of bodies of water and mature
trees for nesting. Also, certain local populations are present along extensive protected forest
areas, that are however isolated from the Atlantic Rainforest.
For Salvador-Jr. et al (2011), 16 records of the species S. tyrannus were obtained in an area of
720,000 hectares, including 37 municipalities, known as the “Quadrilátero Ferrífero” (Iron
Quadrilateral) in the mountain formations in the state of Minas Gerais. According to these
authors, the region has been under great pressure from mining and deforestation
throughout its colonization history. In the previous and present studies, 23 sites were
contemplated for the species, with the farthest points covering a range of approximately
200sq. km in fragmented environments. The records show an average distance of 18.8+_11,
varying between 40 km and 8 km. Thus, we point out that the “Quadrilátero Ferrífero” is of
extreme importance for conservation of potential reproductive populations of the species.
In Mendonça-Lima et al. (2006) several records were made of S. ornatus and its respective
geographical locations in the south of the country generally associated with preserved forest
portions. However, the authors suggest more efforts are needed to conserve this species in
the south of the country, with the species having been sub-sampled, which is partly due to
their refuge in environments of difficult access. Still regarding the southern Atlantic
Rainforest, Joenck (2006) recorded the species Spizaetus tyrannus in several occasions in a
preservation park, estimating two individuals in 4,500 hectares (Table 1).
In the northeast, the Endemism Center of Pernambuco, the species S. tyrannus was recorded
as shown in Figure 1. According to Carlos and Girão (2006), still in the northeastern Atlantic
Rainforest, the species S. ornatus may never have occurred, such as S. melanoleucus that were
never recorded in the region. However, we emphasize the sub-sampling problems,
inadequate methods, prior to habitat fragmentation, which may have made this/these
species extinct in the state, according to previously cited studies.
In the case of nest records or couples incidence for the genus in the Brazilian Amazon
(Figure 1), these records were associated to extensive forests or mosaics of continuous
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environments, but also to fragmented areas. The presence of extensive source areas may
complicate an evaluation on territoriality or density in the Amazon Forest, or fragments of
the forest, according to the recruiting of individuals. S. tyrannus was recorded in extremely
fragmented areas, with records of couples in areas distanced between 22 and 67 km, with
open and altered environmental mosaics among these, as well as in portions of continuous
forest, with records of two specimens exhibiting territorial behavior distanced in 28 km.
However, possible gaps or occupied territories among these were not evaluated in the
continuous areas. S. ornatus, in the Amazon, was only recorded in continuous or extensive
fragments, forests with a minimum of dozens of kilometers in extension.
5. Conclusion
Alvarez et al. (1996) obtained throughout five years in Venezuela, during hike and drives,
one record of S. melanoelucus, two records of S. ornatus and four records of S. tyrannus. These
species were seen in areas that suffer from selective logging, monoculture plantations,
clearings and other altered environments. The authors attested that methods for censuses of
birds of prey must be complemented with observations above the forest canopy. This
warranted the evaluation in this study conducted with appropriate techniques for the
visualization of these species, presenting results of low frequency occurrence and low
density for S. melanoleucus and S. ornatus in the fragmented areas, which shows a greater
sensibility to these environmental changes for both species.
Some authors consider Spizaetus tyrannus less sensitive to fragmentation than its congeners
because it is observed more frequently in fragmented areas (Table 2) and altered forests
(Brown and Amadon, 1968; Jullien and Thiollay, 1996; Thiollay, 2007). In addition, there are
recent records of their occurrence in fragments near major urban centers (Azevedo et al.
2003, Zorzin et al. 2006, Canuto 2008, Salvador-Jr et al. 2011).
We obtained sparse or isolated records of its congeners S. melanoleucus and S. ornatus in the
different case studies. This loss of sympatry (presence of sister species in the same place),
previously cited and evident in extensive or continuous areas (case study 1), shows a lesser
sensibility of the species S. tyrannus to fragmentation when compared to its congeners in the
Atlantic Rainforest, where the species’ natural distribution would be throughout all of the
biome (Brown and Amadon 1968, del Hoyo et al. 1994, Ferguson-Lees and Christie 2001).
According to Canuto (2008a), in the lowland tropical rainforest of Panama, the density of the
group was larger than that of case study 1 (semideciduous Atlantic Forest), with the use of
quite different methods in each study, random hikes and direct observation of the canopy
respectively, but with the same sampling effort (approximately 550 hours). Thus, for the
group, both methods are essential and complementary, with the need of continuous efforts
and several counts or annual campaigns. Therefore, according to these density differences we
can infer, primarily, that Hawk-eagles in less productive areas should be spaced further apart
than those in more productive areas (Hustler and Howells, 1988). According to Lyon and
Kuhnigk (1985), a region with higher primary productivity should support a higher density of
Hawk-eagles. This was attested here for S. tyrannus and S. ornatus, according to Canuto (2008a)
study and few results showed here for the Amazon forest, in comparison with study case 1.
Also it’s important to show that populations, in Amazon forest or other tropical or
subtropical forets (Canuto 2008a, Carvalho-Filho 2009, Canuto 2009, Thiollay 1989a, 2007),
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on large or protected areas, includes 2-3 Spizaetus species at the same sites or portions of
mature forest. Also according to the cited studies the species are of low densitie even at
large portions of mature forest. At Minas Gerais state, those, earlier sympatric species, are
being separated or already are, through local extinction, on several regions by deforestation,
with exception of one extensive reserve in Minas Gerais as PERD (study case 1), or probably
just a few.
Also, as evaluated by Carvalho and Marini (2007), urbanization led to a loss of one-third of
diurnal raptors at the surrounding areas of the Minas Gerais state capital, Belo Horizonte,
including all three Spizaetus, that became extremely rare or probably extinct.
Azevedo et al (2003) recorded several times two individuals together of S. tyrannus at an
island of approximately 42300ha, apart from the main land approximately by 2-10 km, at
Santa Catarina state, on the Atlantic rainforest domain south of Brazil. No other taxon from
Spizaetus was recorded or estimates on density were made.
Therefore, the local decline and extinction of forest raptors in the Atlantic Rainforest, with
their posterior substitution by countryside generalist taxons, due to deforestation of tropical
forests, is very worrying and documented in several studies (Thiollay 1985, Albuquerque
1986, Ellis et al. 1990, Jullien and Thiollay 1996, Sick 1997, Seavy and Apodaca 2002,
Salvador-Jr. and Silva 2009, Zorzin 2011).
Along with the loss of habitats, the local preservation of the genus Spizaetus may be affected
by selective logging, since these species use large trees to build their nests (Brown and
Amadon 1968, Lyon and Kuhnigk 1985, Montenegro et al. 1992, Canuto 2008), and these
evidences of suppression oh emergent trees was evidentiated on several occasions at the
Minas Gerais state (personal communication by the authors), furthermore, these trees are
sparse or rare in already fragmented habitats.
Due to the extinction of those species on several locations of the Atlantic rainforest its
fundamental the creation of a bridge between technical-scientific knowledge and public
opinion through environmental education and publicizing results and conservation
programs, as well as the creation of wildlife corridors. The examples of pressure of
deforestation of areas surrounding conservation parks and along the Atlantic Rainforest due
to mining, selective logging and fragmentation, as well as changes in the Brazilian Forest
Code, and hunting and poaching of the group’s species, are all directly linked to the public
opinion in rural communities and environmental sectors of the municipal, state and federal
governments. This consequently influences the preservation of the Atlantic Rainforest
habitat, along with the Spizaetus group and other indicator or rare species.
According to Figure 2, the central east, northeast, south and west of the state of Minas
Gerais and the south of the state of Bahia are extremely important for the preservation
and study of the genus. Including areas of natural incidence or occurrence, these portions
include the middle basin of the Doce river, the south-central section of the Espinhaço
mountain chain, the Mantiqueira mountain chain (the part in Minas Gerais), transition
cerrado areas in the Triângulo Mineiro Region and the northeast and northwest
(insufficient data) part of the state, and the border between the states of Minas Gerais and
Bahia.
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Fig. 2. Map of Spizaetus records in the Atlantic Rainforest; squares indicate records of pairs,
circles indicate nests and diamonds indicate records from cited literature. Big stars indicate
the incidence of the three species of Spizaetus (yellow), or of two, S. ornatus and S. tyrannus
(brown with black), and S. tyrannus and S. melanoleucus (white with black). Small stars
indicate records of species in this study. In general, white is for S. melanoleucus, black is for
S. tyrannus and brown is for S. ornatus. Scale: 1:5036552.
Several unpublished records of most of individuals, from different observers, were not used
on the assessments. We were more concern in population status at some regions, pairs
together, young and nests, than distribution or occurrence. Therefore according to the
pattern of specimen movements, several kilometers, due to and human persecution or
deforestation pressure, could lead certain species to wander throughout the regions,
mistaken the actual active breeding population with survivors.
We also have to realize that the few or absent records on fledged youngs, meaning
reproductive success, at least in Minas Gerais state, are a crucial alert to lack of active
breeding populations, yet to be evaluated for future conservation plans for the medium or
large birds of prey. As any charismatic or umbrela species, that figures as conservation flags
for any threatened environments, predators generally uses extensive portions of mature, or
protected, or in need to protection, forest habitats, and therefore could provide and serve as
conservation flags for our natural resources and those of local communities.
6. Acknowledgments
We would like to thank Biocev Serviços de Meio Ambiente and staff, the Veracel Station and
staff, the administration of PARNA do Pau Brasil and staff, Tânia Sanaiotti (INPA), the
Instituto Estadual de Florestas (State Forest Institute), the staff and all the surrounding
communities of the “Parque Estadual do Rio Doce”, The Peregrine Fund, the Federal
University of Ouro Preto staff, teachers, students, city community and CAPES, and the
Federal University of Viçosa. Also the collaborators Fernanda Pedreira Tabacow, Breno G.
M. da Silva, Carla de Borba Possamai and staff of the RPPN Miguel Feliciano Abdala-FMA,
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Charles Lopes Moreira and Djalma de Carvalho Junior, Geraldo dos Santos Adriano
(Canela) Fabiano R. Melo, Marcelo Ferreira Vasconcelos, Frederico Pereira de Castro
Andrade, Gustavo Pedersoli, Luiz Gabriel Mazzoni, Alyne Perillo, and Estefane N. L.
Siqueira for their valuable contribution in recording data.
Photo 5. Point count in the canopy (Study case 1). Photo credit: Marcus Canuto
Photo 6. Galery forest, Cerrado-Amazon forest, Mato Grosso state, site of incidence of S.
ornatus. Photo credit: Eduardo Pio Carvalho
Photo 7. Climbing techiniques to access Black-and-white Hawk-eagle nest for
measurements. Study case 3. Photo credit: Breno G M da Silva
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Photo 8. Adult individual of S. tyrannus on flight. Photo credit: Eduardo Pio Carvalho
Photo 9. Adult individual os S. ornatus. Photo credit: Eduardo Pio de Carvalho
Photo 10. Fledgling of S. melanoelucus in the nest. Photo credit: Carlos Eduardo Carvalho
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Photo 11. Selective logging, Viçosa, Minas Gerais. Photo credit: Giancarlo Zorzin
Photo 12. Tallon of hunted Spizaetus specime. Photo credit: Gustav Specht
7. Filliation universities and institutions
Some of the data were presented as part of master degree programs at Universidade Federal
de Ouro Preto – PPG Ecologia de Biomas Tropicais, and Universidade Federal de Viçosa -
Museu de Zoologia João Moojen. Those dissertations were supported by the scientific
scholarship CAPES and The Pregrine Fund, Boise state, Idaho, USA.
8. References
Albuquerque, J.L.B. 1995. Observations of rare raptors in southern Atlantic rainforest of
Brazil.Journalof Field Ornithology 66: 363-369.
Alvarez, E., D. H. Ellis, D. G. Smith, and C. T. Larue. 1996. Diurnal raptors in the fragmented
rain forest of the Sierra Imataca, Venezuela. Pages 263-273
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