10 CONSERVATION STATUS OF THE SAFFRON TOUCANET

Grupo Estud. Ecol., Sér. Doc. 6(2): 10-25
São Paulo, novembro 2000
ISSN 0103-4154
CONSERVATION STATUS OF THE SAFFRON TOUCANET (Baillonius bailloni,
Ramphastidae): A NEW CASE OF POPULATION ISOLATION
AND DEPLETION IN SOUTH AMERICA
Juan Carlos Guixa, Marc Martína, Antonio Hernándeza & Franco Leandro Souzab
a
b
Departament de Biologia Animal (Vertebrats), Facultat de Biologia, Universitat de
Barcelona, Avda. Diagonal 645, E-08028 Barcelona, Spain.
E-mail: [email protected]
Departamento de Parasitologia, Instituto de Biologia, Universidade Estadual de Campinas,
CP 6109, 13083-970 Campinas - SP, Brazil.
ABSTRACT. The conservation status of the saffron toucanet (Baillonius bailloni) is reevaluated taking into account published distribution records from 1978 to 1998 and new data
collected in forest fragments during this period. Surveys were performed between January
1978 and September 1998 at 24 sites in Southern and Central-Western Brazil covered by
native forests. The sites encompassed altitudes between 0 and 1,800 m and a range of forest
habitats. B. bailloni was only found in Paranapiacaba, the largest forest fragment (1,400 km2),
in mature and old secondary Atlantic rainforest, at altitudes between 80 and 770 m. In the
Paranapiacaba fragment, on count routes (in which we counted the number of groups and
individuals per liner kilometer) performed between 1987 and 1991, 0.038 groups and 0.097
individuals of B. bailloni per km were found. In August/September 1998, using line transects,
we found 0.017 ± 0.007 groups/km and 0.051 ± 0.030 individuals/km. Data from these
surveys together with data on habitat loss, population isolation and intensity of illegal trade
indicate that the populations of B. bailloni have declined sharply. We suggest B. bailloni
should be included in the vulnerable category of the IUCN lists of threatened species, and in
the Appendix I of CITES. We also conclude that the same anthropic interferences that are
responsible for the decline of B. bailloni in the last decades may have had a negative effect on
the populations of Selenidera maculirostris.
Key words: Ramphastidae, habitat loss, distribution, threatened species, forest fragmentation.
10
INTRODUCTION
Since the beginning of the 16th century the South American biomes have suffered a
widespread process of depletion and fragmentation. Habitat loss and isolation of plant and
animal populations, constitute the major threats for neotropical species, especially those in
forest ecosystems (Willis, 1979; Collar & Juniper, 1992; Guix, 1995; Robinson, 1996; Collar,
1999).
As well as habitat alteration and destruction, the isolation of populations in forest
patches can produce other threats, such as loss of genetic variability (Camara & Mittermeier,
1984). Bird and mammal populations isolated in small and medium-sized forest fragments are
also more vulnerable to hunting and illegal trade than those living in large continuous forests
(Collar & Juniper, 1992; Robinson, 1996). All these factors may reduce chances of survival in
the long term.
The Brazilian Atlantic rainforest (sensu Hueck, 1972a,b) is one of the most diverse
and threatened biomes of the World, with about 70 endemic bird species, 38 of which are
threatened and 32 of which are expected to disappear in the next few decades (see Brooks &
Balmford, 1996 and references therein). Nowadays, forest fragments are scattered in Eastern
Brazil throughout a region of 3,000 km long and 100 km wide and < 10% of the original
Atlantic rainforest remains (SOS Mata Atlântica, 1992). The largest and best preserved
Atlantic rainforest fragments are found in the Serra do Mar mountain complex (a chain of
about 900 km long in Southeastern Brazil), mainly in the State of São Paulo.
The subtropical forests of SE Brazil, E Paraguay and N Argentina, on more level
ground and richer soils than those of the Atlantic rainforest, have suffered a greater impact
from anthropogenic activities. Since the end of the 19th century, these forests have been
progressively replaced by coffee plantations and pastures and, during the last two decades, by
sugar plantations (Dean, 1997).
These changes have had a considerable impact on several forest bird populations. No
species of toucans (family Ramphastidae) has been included in the international lists of
threatened animals as endangered or vulnerable (Collar et al., 1994; WCMC, 1998) but it has
been recently suggested that the population of the saffron toucanet (Baillonius bailloni) is
decreasing due to habitat destruction and trade (cf. CEE, 1992; Guix, 1995; Parker III et al.,
1996).
The aim of this study was to re-evaluate the conservation status of the saffron toucanet
over its range on the basis of published information, and new data obtained between 1978 and
1998.
The species
The saffron toucanet is found in the Atlantic rainforest of Eastern Brazil (from the
Brazilian States of Pernambuco to Rio Grande do Sul) and the subtropical forests of Eastern
Paraguay and Northern Argentina (Misiones Province)(Sick, 1993). It is a cavity nesting
species which feeds largely on fleshy fruits in the canopy and subcanopy (Guix, 1995). It is
usually found alone, in pairs or small groups (up to six individuals) (Guix, et al., 1997).
Although it flies only short distances, its bright colours (yellow and red) and large size (350
11
mm total length) make it conspicuous in the dense forest. The genus Baillonius is monotypic
and seems to have evolved close to Pteroglossus spp. (Sick, 1993).
METHODS
Recorded distribution
The historic distribution of the saffron toucanet before the European colonization of
South America was obtained from published accounts and localities of collected specimens
compiled by Pinto (1938, 1945) and Sick (1993).
Forest distribution
Since the species is closely associated with dense forests, Landsat TM5 images (years
1986, 1989, 1990, 1993 and 1994 processed by SCT/INPE and NMA-EMBRAPA) and aerial
photographs (1978, 1981, 1989, 1996) of the Serra do Mar mountain complex and
surrounding regions were used to estimate the forest cover to these dates and potential present
area of distribution of the species.
Field surveys
Between January 1978 and September 1998, 24 sites were surveyed in Southeastern
and Central-Western Brazil (22 sites located in the State of São Paulo, one site in the State of
Rio de Janeiro and one site in the State of Mato Grosso do Sul). They covered an altitudinal
gradient from 0 to 1,800 m (Appendix I). These sites were selected since: (a) they cover a
wide range of the former distribution of the species; (b) they show the widest altitudinal
gradient of the forests where B. bailloni lives; (c) they include several habitats, such as
different types of forests and stages of ecological succession (including young secondary
forests, old secondary forests and mature forests), and sites ranging from 1.5 to 1,400 km2,
including the largest remnant fragments of the Brazilian Atlantic rainforest (see Appendix I).
Between 1987 and 1991, count routes in 442 km of trails and unpaved forest roads of
the Paranapiacaba forest fragment, where B. bailloni lives, were performed. During "count
routes" all detected individuals and groups were counted, irrespective of their distance from
the route.
In order to obtain density estimates, line transects were made in the Paranapiacaba
fragment during August/September 1998 (total sampling distance: 352.4 km). Each count was
conducted by 3-4 people and the number and size of groups of birds and their perpendicular
distance to the transect line were recorded. Counts were made during two daily periods
(07:00-11:00 and 16:00-18:00 hours; solar time). For estimating encounter rates we used the
Distance sampling method (Buckland et al., 1993).
12
RESULTS
Current distribution
Based on the Landsat images and aerial photographs, we estimated that the "extent of
occurrence" of the species (see IUCN criteria in WCMC, 1998), around its original
distribution, was < 15,000 km2.
Between 1978 and 1998, B. bailloni was reported by other authors in 20 sites over its
original range of distribution (see Figure 1 and Appendix II). Considering these areas
together, the extent of forest fragments where the species was recorded between 1978 and
1998 period is equal to 6,000 km2.
Figure 1. (1a) Distribution of the Atlantic rainforest of Brazil and the subtropical forests
during the 16th century (according to Hueck, 1972a,b). (1b) Coast of Brazil and inlands
showing the distribution of Baillonius bailloni according to historic records (dotted area).
Sites where the species was reported between 1978 and 1998 (large dots); see Appendix II.
Each dot represents an isolated forest fragment. ? = Sites reported before 1978 and possibly
extinct (from North to South): regions close to Recife (PE), Una (BA), Sooretama Biological
Reserve and Linhares Forest Reserve (ES), Turvo Forest Reserve (RS).
13
In some of these fragments, though, the species has not been recorded in the last 10
years and the fragments where the species was recently (< 5 years) reported are small. In the
largest areas where B. bailloni lives, the species is not found in wide marginal areas covered
by young forests. Thus, a more conservative estimation of the "area of occupancy" (see
WCMC, 1998), between 2,500 and 3,700 km2, is required.
Nowadays, the main populations of B. bailloni are found in a 800 km section of the
Serra do Mar mountain complex, located between Midle Rio de Janeiro and the Northern
Santa Catarina States (Figure 1). From wide regions which were located in the edges of the
historical species distribution (e.g. in the States of Pernambuco and Rio Grande do Sul, and in
the limit of Brazil-Argentina-Paraguay) there are recent records only in four sites: Viçosa
(Brazil), the Reserva Mbaracayú (Paraguay), the Parque Provincial Urugua-í and Puerto Luján
(Argentina)(Figure 1 and Appendix II). On the other hand, in some areas of the State of São
Paulo where other authors have reported the presence of B. bailloni, the species was not found
during our surveys.
Habitat and encounter rates
Out of the 24 sites surveyed during this study, B. bailloni was found only in the largest
forest fragment (Paranapiacaba), from 80 to 770 m of elevation (Figure 2). Thirty nine of the
encounters (93%) were in the hillside Atlantic rainforest and three (7%) in altitudes close to
the limit between this type of forest and the lowland Atlantic rainforest (100 m). Thirty four
encounters (81%) were in mature and old secondary forests, and eight encounters (19%) were
in young forests (Table I). The species was not found in the lowland Atlantic rainforest or the
"restinga" forests, unlike other species of toucans (e.g. Ramphastos vitellinus and Selenidera
maculirostris).
14
Number of records
12
10
8
6
4
2
010
0
10
120
0
20
130
0
30
140
0
40
150
0
50
160
0
60
170
0
70
180
0
0
Elevation (m)
Figure 2. Distribution of Baillonius bailloni according to elevation. Altitudinal range
sampled: from the sea level to 1,800 m.
14
Table I. Occurrence of Baillonius bailloni in relation to the main vegetation types in the State
of São Paulo, Southeast Brazil. The main successional stages of the vegetation found in the
study areas: C = Capoeiras (tall shrubland); S = Young secondary forests; M = Old secondary
and mature forests.
+ = presence and number of encounters during the surveys (n = 42 encounters).
VEGETATION TYPES
C
S
M
Lowland Atlantic rainforest
LB?
+(3)
Hillside Atlantic rainforest
+(8)
+(31)
Subtropical forests
LB
LA
Transitional areas (Atlantic rainforest / subtropical forest)
LD
Bushy "Restinga"
"Restinga" forests
Riparian forests
Dry savannas
Araucaria forest (Araucaria angustifolia)
References before 1986 for vegetation types where the presence of Baillonius bailloni was not
detected during the present study: LA: José Carlos Magalhães, unpublished; LB: Willis and
Oniki, 1981; LD: Graham, 1986a,b.
The effective strip width, which could provide density estimates of B. bailloni, cannot
be assessed statistically because of the low number of records. Thus, encounter rates (groups
and individuals per linear kilometer) were used as an estimator of variation in population size
(see Hochachka et al., 2000).
Encounter rates of B. bailloni in the Paranapiacaba fragment found in 1998 were half
of those found during 1987-1991 (Table II). Along the 352.4 km of line transects performed
in 1998, six groups were observed up to 12 m away from the line transect.
Table II. Group sizes (GS) and encounter rates (ER) of the saffron toucanet in Paranapiacaba
fragment using count routes (1987-1991 period; sampling effort: 442 km) and line transects
(Aug/Sept 1998; sampling effort: 352.4 km). n = number of individuals seen.
Method
GS
ER (groups/km)
ER (ind/km)
n
Count routes
2.54
0.038
0.097
66
3.0 ± 1.0
0.017 ± 0.007
0.051 ± 0.030
18
Line transects*
*
mean and standard error
15
DISCUSSION
Historical and current distribution
Until the end of the 19th century, B. bailloni was widespread in the East and Southeast
South American forests, which mainly comprised the subtropical forests (from the Western
region of the State of São Paulo to Southeastern Paraguay) and the Atlantic rainforest of
Eastern Brazil (from the State of Pernambuco to the State of Rio Grande do Sul) (sensu
Hueck, 1972a,b) (compare Figures 1 and 3). During the 1978-1998 period, the species was
not reported in the remaining fragments of the northern Atlantic rainforest of Brazil (from the
States of Espirito Santo to Rio Grande do Norte).
Although the species was common in the subtropical forests (Pinto, 1938, 1945; see
also Willis, 1979), occurrence records in this habitat have been very scarce in the last two
decades (Willis & Oniki, 1981; Graham, 1986a, b; Chebez, 1994; Madroño, 1996). In several
wide regions formerly covered by subtropical forests (such as in the western portion of the
State of São Paulo) the species became extinct (cf. Willis, 1979; Willis & Oniki, 1981).
Until the middle of the 20th century, large areas with pristine forests in the states of
Rio de Janeiro, São Paulo, Paraná and Santa Catarina remained. From the 1960s on, several
new roads and urban development projects contributed in a substantial way to habitat loss in
the coastal areas (Dean, 1997). Extensive deforestation, followed by habitat fragmentation
and hunting, have been the main causes of the local extinction of several large and mediumsized species of frugivores (Sick & Teixeira, 1979; Willis, 1979; Scott & Brooke, 1985;
Parker III et al., 1996). Surveys carried out between 1979 and 1999 in several areas of the
Paraíba Valley, State of Rio de Janeiro, revealed the presence of B. bailloni at Serrinha in
1988 (Pacheco et al., 1997). Berla (1941), who collected birds in the municipality of Parati (in
the south edge of the State o Rio de Janeiro), in the late 1930s, reported that B. bailloni was
common there. Today, the remmanent forests of this area are very fragmented and B. bailloni
seems to be locally extinct. In the last two decades, other authors have reported the presence
of some of the largest threatened frugivorous birds (such as Pipile jacutinga and Penelope
obscura bronzina) in the remnant forests of the Paraná, the São Paulo and the Rio de Janeiro
States, but failed to find B. bailloni (see Straube, 1988; Scott & Brooke, 1985; Olmos, 1996;
Pacheco et al., 1997). In the southern limit of the Atlantic rainforest, in the state of Rio
Grande do Sul, the last record of the species is in 1974 (cf. Belton, 1984, 1994; Bencke &
Kindel, 1999).
However, several forest fragments located between the latitudes 8o and 20o S require
surveying in order to obtain updated data on the presence/absence of B. bailloni populations.
These areas include the Sooretama Biological Reserve (24,250 ha), the Linhares Forest
Reserve (21,800 ha of which 15,700 are covered by native forests), the Córrego do Veado
Biological Reserve (2,400 ha), the Córrego Grande Biological Reserve (1,500 ha), in the State
of Espírito Santo, the Rio Doce Sate Park (35,973 ha), in the State of Minas Gerais, the
Parque Nacional de Monte Pascoal (22,500 ha), the 7,000 ha Una Biological Reserve, in the
State of Bahia and some old records cited by Sick (1985, 1993), such as Limoeiro (ES) and
Serra Negra (PE).
16
Habitat loss
Collar (1999) argued that the ecological requirements of a given species are important
data to take into account when evaluating its conservation status. Parker III et al. (1996) have
classified B. bailloni as a species with ecological "high sensitivity", which lives in "tropical
lowland evergreen forest" and "montane evergreen forest".
Baillonius bailloni was almost extinguished in the lowland Atlantic rainforest (sensu
Hueck, 1972a,b) and today most of its remaining habitat consists of small and isolated forest
fragments. The smallest isolated forest fragments in the State of São Paulo where B. bailloni
was reported between 1978 and 1998, were the Caetetus Ecological Station (formely Fazenda
Paraíso; 22o 25'S, 49o 42'W), a 2,178 ha reserve (Willis & Oniki, 1981), and the Parque
Estadual da Serra da Cantareira (23o 24'S, 46o 35'W), a 8,000 ha reserve neighboring the city
of São Paulo (Graham, 1986a,b, 1992), in 1976-1979 and in 1985-1986 respectively.
Nevertheless, the species has not been reported recently in these areas. In other smaller and
more isolated areas, such as Fazenda Barreiro Rico (22o 40'S, 48o 11'W; comprising three
forest fragments of 422, 540 and 936 ha), where the species was reported until the early
1960s, the populations are extinct (Willis, 1979; Werner C.A. Bokermmann, pers. comm.,
1989).
In other Brazilian states, the smallest forest fragment which harbours B. bailloni is the
Parque Estadual de Vila Rica do Espírito Santo (Fênix, state of Paraná), a 335 ha reserve of
subtropical forest (Mikich, 1996). Surprisingly, B. bailloni has also been reported in a 54 ha
isolated woodlot of subtropical forest in Viçosa (State of Minas Gerais) (Bustamante, 1996);
the areas of these two forest fragments are 0.24 and 0.04% of the area of the Paranapiacaba
forest fragment (Appendix II). Giraudo and Sironi (1992) observed one individual in a small
island of the Paraná river (Puerto Luján - Corrientes, Argentina), today partialy inundated by
the Yacyretá Dam.
The sum of the areas of the 16 isolated forest fragments where B. bailloni was reported
during the 1978-1998 period (near 134,000 ha) is smaller than the area of the Paranapiacaba
fragment (140,000 ha). Thus, the conservation of the Paranapiacaba fragment seems to be
crucial to the survival of the remaining populations of B. bailloni and other threatened species
of forest birds.
The presence of the species in the areas is strongly linked to the presence of mature
and old secondary forests, with well developed understory (cf. Guix, 1995), and to large live
and dead trees, with woodpecker cavities for nesting (Sick, 1993; Guix et al., 1992). Collar
(1999) pointed out that species which are cavity nesters should be considered as "breeding
specialists". Thus, selective cutting of large trees may affect the breeding success of B.
bailloni in the remaining forests areas.
Baillonius bailloni is also a feeding specialist, its diet depending mostly on the fruiting
of the palmito palm (Euterpe edulis), a species which has undergone intensive harvesting for
food during the last 50 years. Out of 29 feeding bouts, 21 (72%) were on mature fruits of this
palm tree (J.C. Guix, X. Ruiz and L. Jover, umpublished data).
The past and present distribution of the palmito and the saffron toucanet are closely
related. The palmito palm is a keystone species for large and medium-sized frugivores in
Eastern Brasil (Guix, 1995), which has undergone intensive harvesting for food during the
17
last 50 years. At the beginning of the 16th century, E. edulis was widely distributed through
the Atlantic rainforest, the riparian forests of the Tietê and the Paranapanema rivers, and some
valleys covered by wet subtropical forests (Dransfield et al., 1988). Today, this threatened
species is restricted to few reserves, and, in spite of Brazilian laws, illegal harvesting
continues (see Dransfield et al., 1988; Galetti & Fernandez, 1998).
Out of the 24 study areas only in the Paranapiacaba fragment (140,000 ha) and in the
Ilha do Cardoso (22,500 ha) were wild populations of E. edulis found. However, between
1992 and 1998, illegal harvesting was specialy intensive in the Ilha do Cardoso.
Population
The absence of records in 96% of the surveyed areas in the present study suggest a
decline of the populations of the saffron toucanet in the last two decades. This is probably the
result of both extensive habitat loss (habitat fragmentation) and palmito harvesting in private
and goverment protected areas, such as National and State Parks and Field Research Stations.
The Serra de Paranapiacaba (1,400 km2) is the largest fragment of continuous mature and old
secondary forests in the range of distribution of the species and probably contains the largest
populations of B. bailloni.
In a previous survey at the Parque Estadual Intervales, using line transects counts and
the DISTANCE 2.02 suite, the density estimation found for B. bailloni was 12.61 ± 23.76
ind/km2 (Guix et al., 1997). Nevertheless, the poor distance sampling data for this species
prevented the estimation of the effective strip width.
During the 1994 survey, only the Parque Estadual Intervales (38,000 ha) was sampled
and most of the contacts with B. bailloni occurred in the region surrounding the Alecrim
Base. In 1998, all the parks (a total of 110,000 ha) of the Paranapiacaba fragment were
surveyed. The comparison between the encounter rate value in 1998 (0.017 ± 0.007
groups/km) at the Paranapiacaba fragment (where P.E. Intervales is the core area), and that in
1994 (0.072 ± 0.021 groups/km) may suggest that the latter was overestimated.
During the surveys, the spot-billed toucanet (Selenidera maculirostris) - a sympatric
species living in the Atlantic rainforest and subtropical forests - was only detected in two of
the areas studied (The Paranapiacaba fragment and the P.E. da Ilha do Cardoso). Since the
bulk of human interferences detected in the areas studied could also have affected the
populations of S. maculirostris, estimations of the densities of these populations are required.
Nevertheless, S. maculirostris preferently uses subcanopy (Guix, 1995), and its cryptic
coloration prevents the observer from simultaneously detecting and counting the two species.
Trade incidence and captive specimens
Although trading with wild animals has been banned in Brazil since 1967 (cf. Sick &
Teixeira, 1979), specimens captured have been found in the illegal trade and in avicultures
(Werner C.A. Bokermann, pers. comm., 1989). Sick (1979) also reported that B. baillonius
was traded in the market of Recife (PE-Brazil) in 1978, which is the last report on wild
specimens in the State of Pernambuco.
18
In Brazil, B. bailloni was highly appreciated by aviculturists as a cage-bird (Sick,
1979; Werner C.A. Bokermann, pers. comm., 1989) and wild trade probably contributed to
the population decline. In Argentina, B. bailloni was described as "traded as cage-bird"
(Chebez, 1994).
Nowadays, the species is rare in the zoos of Brazil (SBZ, 1999) and in those of other
countries (ISIS, 1999). Reports on succesful breeding in captivity are scarce (14 survivors
between 1978 and 1994, all of them in U.S.A. zoos and gardens (Olney, 1986; Olney et al.,
1988; Olney & Ellis 1990, 1991; Olney & Fisken, 1997).
Status of the species
In Brazil, the local lists of threatened species regard B. bailloni as endangered in the
State of Rio Grande do Sul (Belton, 1994), and as "endangered and vulnerable" in the State of
Minas Gerais (Diário Oficial do Estado, 1996), while no threatening is considered in the State
of São Paulo (Secretaria de Estado do Meio Ambiente, 1998). It is listed as "uncommon"
(Nores, 1991) and "probably endangered" (Chebez, 1994) in Argentina, and in the "medium
conservation priority" (Parker III et al., 1996) and as "near threatened species" (Collar et al.,
1992, 1994) over its whole range. According to the IUCN's categories of threatened animals,
B. bailloni is considered as a "lower risk / near threatened" species (WCMC, 1998). The
saffron toucanet is listed in the Appendix III of CITES (CITES, 1997).
Conclusion
The distribution range of the saffron toucanet is shrinking rapidly and its populations
are strongly fragmented over this range. The ecological requirements of the species suggest
that it is a feeding and breeding specialist which needs well preserved forests. Based on
habitat loss, population isolation and depletion and persistence of illegal trade in the last 20
years we suggest that B. bailloni should be included in the "Vulnerable B1+2abcd" category
of IUCN's lists of threatened species (compare criteria in WCMC, 1998; Collar, 1999;
IUCN/SSC, 1999; Akçakaya et al., 2000) and in the Appendix I of CITES.
Acknowledgements. Juan Manuel Grande, Alejandro Pérez, Josep Luis Melero, Elis Regina
Ribas and Giane Chaves Kristosch helped us with the literature review. We thank Kátia
Pisciotta, Paulo Martuscelli and Cristiane Leonel for assistance and advice. We also thank
Carlos Yamashita, Júlio Cesar Roma and Francesc Llimona for improving the manuscript.
Fundação Florestal and Instituto Florestal de São Paulo provided logistic support and NMAEMBRAPA some edited satelite images. We dedicate this study to our late friend Carles
López Adzerias.
19
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Appendix I. Study areas
Paranapiacaba fragment (SP). 140,000 ha (24o 15'S, 48o 05'W). Located in the Serra do mar mountain complex,
it comprises four contiguous natural parks (Parque Estadual de Carlos Botelho, Parque Estadual Intervales,
Parque Estadual Turístico do Alto Ribeira, and Estação Ecológica de Xitué) and private properties. Elevation:
20-1,095 m. Survey period: between May 1987 and September 1998.
Parque Estadual da Ilha do Cardoso (SP). 22,500 ha. Cardoso Island (25o 10'S, 48o 00'W). Elevation: 0-800 m.
Survey period: between April and October 1990.
Parque Estadual de Ilhabela (SP). 33,593 ha. São Sebastião Island (23o 50'S, 45o 20'W). Elevation: 0-1,379 m.
Survey period: 10 July to 18 August 1997.
Parque Estadual da Cantareira (SP). 8,000 ha. Serra da Cantareira (23o 24'S, 46o 35'W). Elevation: 800-1,010 m.
Survey period: August-September 1998.
Parque Estadual de Vassununga (SP). 1,732 ha. Located near the town of Santa Rita do Passa Quatro (21o 43'S,
47o 36'W). Elevation: 500-600 m. Surveys: 22 November 1979, 26 June and 16 December 1980, 7-8 September
1982, 12-13 November 1983.
Reserva Estadual de Morro Grande (Formerly "Caucaia do Alto", SP). 10,700 ha. (23o 45'S, 47o 30'W).
Elevation: 500-700 m. Survey: February 1990.
Estação Experimental de Zootecnia de Sertãozinho (SP). 675 ha. (21o 08'S, 47o 59'W). Elevation: 500-600 m.
Survey period: July and August 1990.
Área de Proteção Ambiental da Serra do Mar (SP). > 5,000 ha. Data colected in the municipality of Cubatão,
Serra do Mar Atlantic chain. Elevation: 150-700 m. Survey period: between May 1990 and September 1994.
Estação Ecológica de Ribeirão Preto (Formerly "Mata de Santa Tereza" - SP; 21o 35'S, 47o 48'W). 154.2 ha.
Elevation: 550 m. Survey period: July 1981.
Estação Ecológica de Jataí (Município de Luiz Antônio - SP). 4,532 ha of savannas and forests. Survey period:
May to November 1993, August 1997.
Reserva da Fazenda Santa Adelaide (Ribeirão Preto - SP). 78 ha. Elevation: 500 m.
Serra do Japi (SP). 8,000 ha. (23o 11'S, 46o 52'W). Elevation: 700-1,170 m. Survey period: between April 1987
and August 1990.
23
Mata do Pau Furado (SP). About 200 ha. (23o 31'S, 46o 51'W). Includes the Condomínio Transurb area.
Elevation: 700-800 m. Survey period: from February 1989 to November 1990.
Fazenda Santa Carlota (SP). 6,292 ha. Woodlots of forests and dense savanna (21o 22'S, 47o 15'W). Elevation:
600-944 m. Survey period: December 1983, November 1987 and February 1988.
Fazenda Capricórnio (SP). Six kilometers from the city of Ubatuba (23o 23'S, 45o 04'W). Elevation: 10-400 m.
Survey period: January 1985.
Fazenda São Vicente (SP). Municipality of Campinas, near the Atibaia river. Elevation: 500-600 m. Surveys: 21
July 1991 and 03 September 1994.
Fazenda Santa Úrsula (SP). 40 ha. Municipality of Jaguariuna, 2 km from the city of Jaguariuna. Elevation: 500600 m. Surveys: 21 July 1990 and 4-5 September 1994.
Ouro Fino Paulista (SP). 150 ha. Two kilometers from Ouro Fino Paulista village (23o 40'S, 46o 26'W).
Elevation: 500-650 m. Survey period: from February 1987 to October 1991.
Gleba de Sousas (SP). 200 ha. Eight kilometers from the city of Sousas (22o 52'S, 46o 59'W). Elevation: 500-600
m. Surveys: 21 and 27 September 1990, 4 September 1994.
Rio Paranapanema (SP). 57-140 ha Several woodlots located close to the Paranapanema river, in the Ourinhos
region. Elevation: 400-550 m. Surveys: 3-4 January 1978, 22 September 1990.
Cássia dos Coqueiros (SP). Several woodlots located close to the city of Cássia dos Coqueiros. Elevation: 500650 m. Survey periods: 7-13 July 1980, September 1989.
Hidrelétrica Armando Laydner (SP). Savannas and woodlots located in the municipalities of Avaré and Itaí,
close to the Jurumirim dam. Elevation: between 400 and 600 m. Survey periods: 05-19 January 1978, September
1990.
Fazenda Floresta Negra (MS). Two woodlots totaling 967 ha. Located in the municipality of Sete Quedas, State
of Mato Grosso do Sul, close to the frontier between Brazil and Paraguay. Elevation: between 300 and 400 m.
Survey period: 22-26 September 1990.
Parque Nacional do Itatiaia (RJ). 11,943 ha. Located in the Serra da Mantiqueira chain (22o 37'S, 44o 45'W).
Elevation: 816-2,787 m. Survey: 3-4 October 1990.
24
Appendix II. Sites where Baillonius bailloni was reported by other authors during the 1978-1998 period.
Campus da Universidade Federal de Viçosa (MG-Brazil). 54 ha. (Bustamante, 1996).
Serra do Tinguá (RJ-Brazil). 25,000 ha (Scott and Brooke, 1985).
Serra da Sibéria, near Nova Friburgo (RJ-Brazil). 1,200 ha (Scott and Brooke, 1985).
Parque Nacional da Serra dos Orgãos (RJ-Brazil). 12,000 ha (Scott and Brooke, 1985).
Serrinha, Paraíba Valley (RJ-Brazil) (Pacheco et al., 1997).
Parque Nacional de Itatiaia (RJ-Brazil). 11,943 ha. (22o 37' S, 44o 45' W). In the Serra da Mantiqueira (Sick,
1985, 1993; Goldbach, 1998).
Ubatuba (SP-Brazil). (23o 25'S, 45o 07'W). Located 5 km from the Ubatuba city (Willis and Oniki, 1981).
Estrada da Petrobrás, entre Salesópolis e Caraguatatuba (SP-Brazil). (230 36' S, 450 24' W). Município de
Caraguatatuba. (Höfling & Lencioni, 1992).
Parque Estadual da Cantareira (SP-Brazil). 8,000 ha. (23o 24' S, 46o 35' W) (Graham, 1986a,b, 1992).
Estação Ecológica de Caetetus (formely Fazenda Paraíso). Município de Gália (SP-Brazil). 2,178 ha. (Willis and
Oniki, 1981).
Paranapiacaba fragment (SP-Brazil). 140,000 ha. (24o 15' S, 48o 05' W) (Guix et al., 1992).
Parque Estadual da Ilha do Cardoso (SP-Brazil). 22,500 ha. (25o 10' S, 48o 00' W) (Martuscelli, 1990;
Martuscelli in São Paulo, 1998).
Fazenda Santa Rita, Palmeira (PR-Brazil). 2,000 ha. (280 18'S, 490 48'W)(Anjos, 1992).
Parque Estadual de Vila Rica do Espírito Santo, Fênix (PR-Brazil). 335 ha. (23o 54'S, 51o 58'W)(Mikich, 1996).
Parque Botânico Morro do Baú, Ilhota (SC-Brazil). 750 ha. (260 49'S, 480 56'W) (Marterer, 1994).
Parque Ecológico Artex, Itoupava Rega-Blumenau (SC-Brazil) (C. Zimmermann, 1990, 1991 in Rosário, 1996).
Serra da Moema, Itaiópolis (SC-Brazil) (Rosário, 1996).
Reserva Mbaracayú (Southeastern Paraguay) (Madroño, 1996)
Puerto Luján, Departamento Ituzaingó (NE Provincia de Corrientes-Argentina) (27o 22' S, 56o 10' W) (Giraudo
& Sironi, 1992).
Parque Provincial Urugua-í (Argentina) (Chebez, 1994).
25