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Effects of Quaternary Climatic Fluctuations on the Distribution of Neotropical Savanna Tree Species

  • Instituto Prístino, Belo Horizonte, Brazil

Abstract and Figures

In order to develop niche models for tree species characteristic of the cerrado vegetation (woody savannas) of central South America, and to hindcast their distributions during the Last Glacial Maximum and Last Inter-Glacial, we compiled a dataset of tree species checklists for typical cerrado vegetation (n=282) and other geographically co-occurring vegetation types, e.g. seasonally dry tropical forest (n=355). We then performed an Indicator Species Analysis to select ten species that best characterize typical cerrado vegetation and developed niche models for them using the Maxent algorithm. We used these models to assess the probability of occurrence of each species across South America at the following time slices: Current (0 ka pre-industrial), Holocene (6 ka BP), Last Glacial Maximum (LGM - 21 ka BP), and Last Interglacial (LIG - 130 ka BP). The niche models were robust for all species and showed the highest probability of occurrence in the core area of the Cerrado Domain. The palaeomodels suggested changes in the distributions of cerrado tree species throughout the Quaternary, with expansion during the LIG into the adjacent Amazonian and Atlantic moist forests, as well as connections with other South American savannas. The LGM models suggested a retraction of cerrado vegetation to inter-tableland depressions and slopes of the Central Brazilian Highlands. Contrary to previous hypotheses, such as the Pleistocene Refuge Theory, we found that the widest expansion of cerrado tree species seems to have occurred during the LIG, most probably due to its warmer climate. On the other hand, the postulated retractions during the LGM were likely related to both decreased precipitation and temperature. These results are congruent with palynological and phylogeographic studies in the Cerrado Domain.
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tropical forests. e savannas, generally referred to as ‘cer-
rado’ (note that throughout we use lower case to refer to the
vegetation type), are the subject of this study.
e Pleistocene refuge theory postulated that South
American savannas, especially cerrado vegetation, expanded
into the Amazon during the Last Glacial Maximum (LGM;
20 000–13 000 yr before present, 20–13 Ka), where it
fragmented the distribution of rain forest vegetation (Haffer
1969). However, paleoecological studies from the Amazon
have suggested continuous presence of rain forest there
through the LGM (Colinvaux et al. 2000, Mayle et al.
2000, Colinvaux and De Oliveira 2001, Bush et al. 2002,
2011, Mayle and Beerling 2004, Urrego et al. 2005, Bush
and de Oliveira 2006). Paleoecological studies focused on
the Cerrado Domain itself have suggested a retraction of
the cerrado tree flora during the LGM, probably caused by
considerable declines in both precipitation and temperature
(Salgado-Labouriau 1973, 1984, 2001, Ledru 1993, 2002,
Behling 1995, Ferraz-Vicentini and Salgado-Labouriau 1996,
Ecography 40: 403–414, 2017
doi: 10.1111/ecog.01860
© 2016 e Authors. Ecography © 2016 Nordic Society Oikos
Subject Editor: John Williams. Editor-in-Chief: Miguel Araújo. Accepted 20 January 2016
ere is strong evidence that global climate fluctuations,
and Pleistocene glacial/interglacial cycles in particular, have
played a key role in determining both the origin and dis-
tribution of living organisms (Hewitt 2000). While at one
time, tropical regions were considered to have been more
stable than temperate regions during Pleistocene climatic
cycles, a great number of studies have suggested otherwise
(Haffer 1969, 1982, Prance 1982). Savanna is one of the
main Neotropical biomes (Bourlière and Hadley 1983), and it
is thought to have shifted its distribution significantly during
the Pleistocene (Ledru 2002). e Cerrado Phytogeographical
Domain contains the largest expanse of the savanna in the
Neotropics, and there has been extensive research aimed at
understanding its distribution during the Pleistocene (Ledru
1993, 2002, Oliveira-Filho and Ratter 1995, 2002, Ledru
et al. 1996, Salgado-Labouriau 1997, Salgado-Labouriau
et al. 1998, Werneck et al. 2012). In addition to savannas,
which are the main vegetation type, the Cerrado Domain
also contains grasslands, semideciduous and seasonally dry
Effects of Quaternary climatic fluctuations on the distribution of
Neotropical savanna tree species
Marcelo Leandro Bueno, R. Toby Pennington, Kyle G. Dexter, Luciana H. Yoshino Kamino,
Vanessa Pontara, Danilo Mesquita Neves, James Alexander Ratter and Ary Teixeira de Oliveira-Filho
M. L. Bueno (, V. Pontara, D. M. Neves and A. T. de Oliveira-Filho, Programa de Pós-graduação em Biologia Vegetal,
Univ. Federal de Minas Gerais – UFMG, Campus Pampulha, Cep 31270-090, Belo Horizonte, Brazil. DMN also at: Royal Botanic Gardens,
Kew, TW9 3AB, UK. – R. T. Pennington, K. G. Dexter and J. A. Ratter, Royal Botanic Garden Edinburgh, 20a Inverleith row, EH3 5LR,
Edinburgh, UK. KGD also at: School of GeoSciences, Univ. of Edinburgh, 201 Crew Builing, King’s Buildings, EH9 3JN, Edinburgh, UK. – L.
H. Y. Kamino, Inst. Prístino, Rua Santa Maria Goretti, 86, Cep 30642-020, Belo Horizonte, Brazil.
In order to develop niche models for tree species characteristic of the cerrado vegetation (woody savannas) of central South
America, and to hindcast their distributions during the Last Glacial Maximum and Last Inter-Glacial, we compiled a
dataset of tree species checklists for typical cerrado vegetation (n 282) and other geographically co-occurring vegetation
types, e.g. seasonally dry tropical forest (n 355). We then performed an indicator species analysis to select ten species
that best characterize typical cerrado vegetation and developed niche models for them using the Maxent algorithm. We
used these models to assess the probability of occurrence of each species across South America at the following time slices:
Current (0 ka pre-industrial), Holocene (6 ka BP), Last Glacial Maximum (LGM – 21 ka BP), and Last Interglacial (LIG –
130 ka BP). e niche models were robust for all species and showed the highest probability of occurrence in the core area
of the Cerrado Domain. e palaeomodels suggested changes in the distributions of cerrado tree species throughout the
Quaternary, with expansion during the LIG into the adjacent Amazonian and Atlantic moist forests, as well as connections
with other South American savannas. e LGM models suggested a retraction of cerrado vegetation to inter-tableland
depressions and slopes of the Central Brazilian Highlands. Contrary to previous hypotheses, such as the Pleistocene refuge
theory, we found that the widest expansion of cerrado tree species seems to have occurred during the LIG, most prob-
ably due to its warmer climate. On the other hand, the postulated retractions during the LGM were likely related to both
decreased precipitation and temperature. ese results are congruent with palynological and phylogeographic studies in
the Cerrado Domain.
Ledru et al. 1996, Salgado-Labouriau et al. 1997, Barberi
et al. 2000, Lima-Ribeiro et al. 2004). Understanding the
nature of any LGM retraction of cerrado vegetation in the
Cerrado Domain has important implications, because refu-
gial areas may contain higher overall species richness and
higher genetic diversity within individual species (Collevatti
et al. 2012, Lima et al. 2014), and therefore should be
priorities for conservation. Understanding whether any
refugial areas were numerous and scattered micro-refugia, or
fewer, larger areas is therefore of great relevance (Rull 2009,
2011, Vegas-Vilarrubia et al. 2011).
e key question of whether cerrado vegetation may
have expanded into Amazonia or contracted during the
LGM can be addressed by modelling species distributions.
Recent investigations, based on modelling species distribu-
tions and patterns of species richness, endemism and genetic
variation, have provided increased evidence that climati-
cally stable areas could have played the role of refugia for
moist forest species in the Neotropics during Quaternary
climatic fluctuations (Graham et al. 2006, Carnaval and
Moritz 2008, Carnaval et al. 2009, 2014, Keppel et al.
2012, Werneck et al. 2011, 2012, Montade et al. 2014).
Most of these recent studies have focused on moist forests
and the existence of such refugia for cerrado vegetation has
not been sufficiently tested using newer approaches, such
as species distribution modelling. In addition to this, there
has been little investigation of the distribution of savannas,
and the cerrado in particular, before the LGM (although see
Werneck et al. 2012). During the Last Interglacial (LIG,
which began 130 000 to 116 000 BP (130–116 Ka), the
climate was significantly warmer than during the Holocene
maximum, registering globally higher temperatures
(ca 2 °C) and higher summer insolation (Otto-Bliesner
et al. 2006). us, expansion of the cerrado vegetation and
contraction of moist vegetation may have actually occurred
during the LIG.
Species distribution modelling can be used to comple-
ment palynological studies and enhance our capacity to
hindcast and forecast changes in population and vegetation
dynamics (Scoble and Lowe 2010, Mellick et al. 2012).
is study is the first to hindcast the distributions of tree
species characteristic of the cerrado vegetation to the Last
Inter-Glacial (LIG) and Last Glacial Maximum (LGM).
Werneck et al. (2012) modelled the distribution of cerrado
vegetation based both on a map of the Cerrado Domain
from Brazilian Inst. of Geography and Statistics (IBGE
1998) and a broader spatial definition, as geographically
defined by Olson et al. (2001). However, this approach
is less realistic biologically than studying the responses
of individual species (Collevatti et al. 2013), which is the
approach that we use here.
Our main questions were: a) was there an expansion or
contraction of the cerrado vegetation during the LGM and/
or LIG; b) if cerrado vegetation contracted during one of
these time periods, were there areas of higher environmental
suitability that could have operated as refugia; and c) if and
when cerrado vegetation expanded, was it extensive enough
to fragment Amazonian forest and/or establish connections
between the cerrado and the savannas of northern South
Study area
e Cerrado Domain spreads across the Central Brazilian
Highlands, which comprise 1/4 of Brazil’s surface, and to
smaller areas in northwestern Paraguay and eastern Bolivia
(Olson et al. 2001, Oliveira-Filho and Ratter 2002) (Fig. 1).
It is the second largest Phytogeographical Domain in South
America, surpassed in area only by the Amazon (Ribeiro and
Walter 2008). e Cerrado Domain extends over 20 degrees
of latitude and from altitudes of 100 m in the Pantanal
(western floodplains) to 1500 m in the highest tablelands of
the Central Brazilian Highlands (Ribeiro and Walter 2008).
ere is remarkable variation in mean annual temperatures
across the region, ranging from 18 to 28°C. Rainfall also
varies widely, from 800 to 2000 mm yr–1, with a long-lasting
dry season during the austral winter (approximately April–
September) (Ab’Saber 2003).
e prevalent vegetation type of the Cerrado Domain
bears the same name, cerrado. It is a woody savanna that var-
ies from fairly open grasslands to forests with a nearly closed
canopy called cerradão (Ribeiro and Walter 2008). e typi-
cal cerrado vegetation grows on acidic, dystrophic soils and
is one of the richest savanna floras of the world, with over
12 000 species of vascular plants (Mendonça et al. 2008).
e floristic dataset was extracted from NeoTropTree
(Oliveira-Filho 2014), a database that consists of tree
(defined as free-standing woody plants 3 m in height)
species checklists for 2000 geo-referenced sites compiled
from the literature and herbarium specimen records. We
extracted all 638 sites and 2155 species from the Cerrado
Domain, representing 288 sites of typical cerrado vegeta-
tion, 112 sites of semideciduous forest, 116 of seasonally dry
tropical forest and 122 of mesotrophic cerradão.
e cerrado vegetation is essentially a vegetation of poor
dystrophic soils, and where more fertile soils occur in the
Cerrado Domain, they are occupied by seasonally try tropi-
cal forests or mesotrophic cerradão, which is transitional
between seasonally dry tropical forests and typical cer-
rado vegetation (Ratter 1973, Ratter et al. 1977, 1978a, b,
Oliveira-Filho and Ratter 2002, Ribeiro and Walter 2008,
Bueno et al. 2013). Seasonally dry tropical forests are nota-
ble for experiencing little fire and are thus occupied by a
different set of plant lineages (e.g. Cactaceae) than those
in typical cerrado vegetation, which experiences frequent
and more intense fires (Pennington et al. 2000, 2009).
Meanwhile, mesotrophic cerradão is an almost closed for-
est with a canopy cover of 50–90%, with trees often grow-
ing to 8–12 m (casting a considerable shade so that the
ground layer is much reduced), and including a blend of
species from both typical cerrado vegetation and seasonally
dry tropical forests (Ratter 1973, 1992, Ratter et al. 1977,
1978a, Furley and Ratter 1988, Oliveira-Filho and Fontes
2000, Oliveira-Filho and Ratter 2002, Bueno et al. 2013).
Semideciduous forests are found in more humid areas
than typical cerrado vegetation, such as along river courses
(i.e. gallery forest) or in transition zones with moist forests
of the Amazon or the Mata Atlantica. Semideciduous forests
tend to be richer in species than the other vegetation types
(Oliveira-Filho and Ratter 1995, 2000, 2002).
We then performed an indicator species analysis, ISA
(Dufrêne and Legendre 1997), of the same matrix from
the Cerrado Domain to extract the species that indicate
typical cerrado vegetation communities. e ISA produces
an IV (indicator value) obtained by a combination of a spe-
cies’ frequency within a group compared with other groups
(specificity) and the species’ presence in most sites of that
group (fidelity). We performed the analysis using the labdsv
package (Roberts 2013) in the R Statistical Software (R Core
Team). We then selected the ten species with the top IVs in
typical cerrado and extracted the geographical coordinates
of floristic lists in which the species were present from
NeoTropTree (Table 1).
Bioclimatic variables
For all sites, we obtained the value, at 2.5 arc-min (approxi-
mately 5 km) resolution, of the 19 standard BIOCLIM
variables, which reflect various aspects of temperature,
precipitation, and seasonality and which are likely to be
important in determining species distributions (Hijmans
et al. 2005). We cropped the bioclimatic layers to span
from 12°47N to 34°46S and from 78°31W to 35°00W,
following Werneck et al. (2012) and which represents a
much larger spatial range than that of the Cerrado Domain.
After assessing correlations between the bioclimatic variables,
we retained 10 of 19 variables, eliminating those with less
biological relevance from groups of strongly interrelated
variables (r 0.9). is procedure was done to avoid over-
parametrization of our modelling with redundant variables.
e final selected variables were: annual mean temperature,
mean diurnal range, isothermality, temperature annual
range, mean temperature of wettest quarter, mean tempera-
ture of the driest quarter, mean temperature of warmest
quarter, annual precipitation, precipitation of wettest month
and precipitation of the driest month.
Model construction
We modelled the ecological niche of the ten selected indicator
tree species (Table 1) using Maxent ver. 3.3 (Phillips
et al. 2006). It has been demonstrated that Maxent often
Figure 1. Geographic distribution of the Cerrado Domain and savannas in South America (Olson et al. 2001), with the location and veg-
etation type of floristic checklists used in this study (typical cerrado vegetation: blue circles, mesotrophic cerradão: red circles, seasonally
dry tropical forest: orange circles, and semideciduous forests: green cirlces), following (Oliveira-Filho 2009). Brazilian states are labelled as
follows: Acre (AC), Alagoas (AL), Amazonas (AM), Bahia (BA), Ceará (CE), Distro Federal (DF), Espírito Santo (ES), Goiás (GO), Mara-
nhão (MA), Minas Gerias (MG), Mato Grosso (MT), Mato Grosso do Sul (MS), Pará (PA), Paraíba (PB), Paraná (PR), Rio de Janeiro (RJ),
Rio Grande do Norte (RN), Rondônia (RO), São Paulo (SP), Sergipe (SE), Tocantins (TO).
Neotropical Domains (Carnaval and Moritz 2008, Werneck
et al. 2011, 2012). Spatial models were converted from con-
tinuous outputs into presence/absence maps by applying the
lowest presence threshold for each model. is approach
maximizes agreement between observed and modelled dis-
tributions, balancing the cost arising from an incorrect pre-
diction against the benefit gained from a correct prediction
(Pearson et al. 2007). By summing up the presence/absence
maps obtained under Current, Holocene (6 ka BP), LGM
(21 ka BP) and LIG (130 ka BP) projections, we generated
a map of areas showing historical stability. is combined
map depicted areas that were potentially occupied by typi-
cal cerrado species during the climatic oscillations of the
Quaternary. ese historically stable areas, which we consid-
ered to be potential refugia, were defined as those grid cells
for which the presence of all indicator species was inferred
across all time projections.
Species distribution modelling validation
We calculated the sensitivity (the proportion of observed
presences in relation to those that were predicted, which
quantifies omission errors), the specificity (the proportion
of observed absences compared to those that were pre-
dicted, which quantifies commission errors) and the TSS
(true skill statistic), following Allouche et al. (2006). e
TSS test corrects the overall accuracy of the model predic-
tion by the accuracy expected by chance. is test provides
a score between –1 and 1, with values 0.6 considered to
be good, 0.2–0.6 to be fair to moderate and 0.2 to be
poor (Jones et al. 2010). e TSS is a threshold-dependent
measure that is appropriate for evaluating predictive accu-
racy in cases where the model prediction is formulated as
a presence–absence map (Allouche et al. 2006, Jones et al.
2010). ese analyses used the occurrence points of the ten
indicator tree species and 202 occurrences of Eugenia uru-
guayensis obtained from NeoTropTree (Oliveira-Filho 2014),
which has a restricted niche that differs from the typical cer-
rado species and is ideal for simulating absence points for
typical cerrado vegetation.
We also used a threshold-independent method of model
validation, the receiver operating characteristic (ROC) curve
analysis. e ROC curve is obtained by plotting sensitivity
values (the true positive fraction) on the y-axis against their
outperforms other modelling techniques to identify areas
critical to the maintenance of species populations (Elith
et al. 2006, 2011, Pearson et al. 2007, Phillips and Dudík
2008, Pena et al. 2014). In addition, an important reason for
choosing Maxent was that it allowed us to use presence-only
species data, which is of great utility because the vast majority
of the biotic data available, including those used here, come
in this form (Elith et al. 2006, Phillips and Dudík 2008).
To calibrate and evaluate the quality of the models, we
divided the data for each species into a training set (75% of
occurrences) and a test or validation set (25% of occurrences).
We constructed models five times and averaged the output to
produce the final results used in downstream analyses. Next,
for each species, we defined a threshold value above which
grid cells were considered to have environmental characteris-
tics suitable for the maintenance of viable populations of the
species (Pearson et al. 2007). We used the ‘minimum train-
ing presence’ as the threshold selection method because it
assumes that the species presence is restricted to sites at least
as suitable as those at which the species has been observed so
far (Pearson et al. 2007).
In order to produce models to infer the palaeodistribu-
tion of the cerrado indicator tree species, we produced pro-
jections of the suitability of occurrence during the Current
(0 ka pre-industrial), Mid-Holocene (6 ka BP), Last Glacial
Maximum (LGM – 21 ka BP), and Last Interglacial (LIG
130 ka BP) time periods based on climatic simulations
(< >; Hijmans et al. 2005). For the Last
Glacial Maximum (21 ka, LGM), Holocene (6 ka) and
Current (0 ka pre-industrial) time periods, we employed
the Community Climate System Model – CCSM4 (Gent
et al. 2011), which represents downscaled climate data from
simulations with Global Climate Models (GCMs) based
on the Coupled Model Intercomparison Project Phase 5
(CMIP5; Taylor et al. 2012). e paleo-climatic model for
the Last Interglacial (120 ka, LIG) used the approach of
Otto-Bliesner et al. (2006). We summed the projections of
the ten indicator tree species for each time period, which
together represent the probability of occurrence of typical
cerrado vegetation during that time period. We performed
all geographic information system (GIS) analyses in ArcGIS
ver. 10 (ESRI 2011).
To indicate potential areas of climatic stability for cerrado
tree species during the whole of the Quaternary, we adopted
protocols similar to those used in recent studies for other
Table 1. The ten tree species selected as indicators of typical cerrado vegetation. IV – indicator value; IV-p – the probability of obtaining as
high an indicator value as that observed for typical cerrado vegetation.
Relative frequency in main vegetation types
Seasonally dry
tropical forests
forests IV IV-p
Connarus suberosus Planch. 296 0.85 0.59 0.02 0.00 0.50 0.001
Erythroxylum suberosum St. Hil. 234 0.84 0.58 0.01 0.00 0.50 0.001
Palicourea rigida Kunth 182 0.65 0.20 0.00 0.01 0.50 0.001
Kielmeyera coriacea Mart. & Zucc. 244 0.87 0.58 0.03 0.09 0.49 0.001
Annona crassiflora Mart. 194 0.69 0.26 0.02 0.04 0.48 0.001
Caryocar brasiliense Cambess. 263 0.75 0.40 0.03 0.06 0.47 0.001
Couepia grandiflora (Mart. & Zucc.) Benth. 242 0.70 0.33 0.02 0.02 0.46 0.001
Qualea parviflora Mart. 254 0.91 0.84 0.04 0.03 0.45 0.001
Byrsonima coccolobifolia Kunth 218 0.78 0.48 0.03 0.06 0.45 0.001
Qualea grandiflora Mart. 266 0.95 0.92 0.12 0.08 0.43 0.001
coupled with a contraction toward central Brazil and eastern
Bolivia (Fig. 2B). Further, there was a notable retraction of
typical cerrado vegetation to inter-tableland depressions and
the slopes of the Central Brazilian Highlands, as well as a low
suitability at higher altitudes (Fig. 3).
In the Mid-Holocene (Fig. 2C), the modelled species
expanded their distributions to approach those of the cur-
rent distribution of the typical cerrado vegetation. Lastly, the
results obtained for the Current projection (Fig. 2D) showed
a distribution similar to that of the Cerrado Domain, as
delimited by Olson et al. (2001). Indeed, a map of under
vs over-prediction of cerrado vegetation with respect to the
map of Olson et al. (2001) shows high congruence, particu-
larly in areas of the central Cerrado Domain. Meanwhile,
we overpredicted typical cerrado vegetation in ecotonal
areas between the Cerrado Domain and adjacent Domains,
i.e. in semideciduous forests that transition to the Amazon
and Mata Altantica moist forests (Supplementary material
Appendix 1, Fig. A1).
Some areas in the central region of the Cerrado Domain
showed a high probability of climatic stability throughout
the Quaternary and are shown in yellow in Fig. 4. ese
postulated refugia for typical cerrado vegetation occur mainly
in Minas Gerais and São Paulo states and the Federal District,
with smaller areas scattered across the Cerrado Domain in
other states, such as Tocantins, Goiás and Mato Grosso. e
distribution of Brazilian conservation units shows a low level
of coincidence with these postulated refugia (Fig. 4).
Modelling cerrado indicator species
Our results demonstrated the greatest extent of typical
cerrado tree species in the LIG, the greatest contraction in
the LGM, and a subsequent re-expansion in the Holocene.
e values obtained by TSS and AUC modelling suggest that
the environmental variables used in our models provided
important information on the distribution of the tree species
selected as indicators of typical cerrado vegetation, and were
higher than those obtained by other studies modelling the
climatic distribution of neotropical vegetation (Carnaval and
Moritz 2008, Werneck et al. 2011, 2012, Pena et al. 2014),
but which did not model individual indicator species. e
indicator species method has been widely and effectively
equivalent specificity values (1 – specificity, the false positive
fraction) on the x-axis for all possible thresholds (Fielding
and Bell 1997). e ROC analysis characterizes the predic-
tive performance of a model at all possible thresholds by a
single number, the area under the curve (AUC) (Fawcett
2003, Phillips et al. 2006). A single AUC value was calcu-
lated for each species, representing the average across the five
iterations of model construction. e value of the AUC can
fall between 0.5 and 1.0. If the value is 0.5, the model is no
better than random, while models with values above 0.75
are generally considered potentially useful and models with
a value near one are considered to be strongly supported
(Fielding and Bell 1997, Elith 2002, Rushton et al. 2004,
Phillips et al. 2006).
e ten tree species identified by our indicator species
analyses as the most important indicators of typical cerrado
and therefore chosen to generate ecological niche models
and predict current and past distributions are given in Table
1. e quality of the models, according to AUC and TSS
values computed for the ten indicator tree species, showed
that sample and background predictions generated by
Maxent were generally in agreement (Table 2). at is, the
Maxent model performance in this study is much better than
random. is was confirmed by the correct assignment of
the test data using the models, indicating that the models
showed a good performance in predicting species occurrences
with bioclimatic variables.
e palaeomodels suggest significant changes in the
distributions of typical cerrado tree species during the
Quaternary (Fig. 2). e cerrado tree flora experienced its
maximum expansion during the Last Inter-Glacial (LIG),
when the modelled species spread toward the south and east
of the Amazon basin as well as toward the Atlantic coast in
both southeastern and northeastern Brazil (Fig. 2A). All of
these areas shelter current-day cerrado enclaves within moist
forests of both the Amazonian and Atlantic Forest Domains,
as well as within the semi-arid thorn-woodlands of the
Caatinga Domain.
In contrast with the LIG, the models suggest a maximum
retraction of the modelled cerrado species during the Last
Glacial Maximum (LGM), with an almost entire withdrawal
from both eastern Amazonia and Atlantic coastal areas
Table 2. Evaluation of the model performance for cerrado indicator tree species of cerrado vegetation by Maxent. True skill statistic (TSS) and
area under the curve (AUC).
External test
presence points
External test
absence points Sensitivity Specificity TSS AUC
Connarus suberosus Planch. 237 59 202 0.95 1.00 0.95 0.92
Erythroxylum suberosum St.Hil. 176 58 202 0.78 1.00 0.78 0.92
Palicoria rigida Kunth 137 45 202 0.90 1.00 0.90 0.92
Kielmyera coriacea Mart. & Zucc. 183 61 202 0.61 0.99 0.60 0.92
Annona crassiflora Mart.146 48 202 0.95 1.00 0.94 0.93
Caryocar brasiliensis Cambess.211 52 202 0.85 1.00 0.85 0.93
Couepia grandiflora (Mart. & Zucc.) Benth. 194 48 202 0.64 0.99 0.63 0.92
Qualea parviflora Mart.191 63 202 0.93 1.00 0.93 0.91
Byrsonima coccolobifolia Kunth 164 54 202 0.75 1.00 0.75 0.93
Qualea grandiflora Mart. 200 66 202 0.93 1.00 0.93 0.91
2005, 2007a, b). Because of this uncertainty, wherever
possible we discuss our results in light of palaeoclimatic recon-
structions based upon other proxies, including fossil pollen
and speleotherms (Van der Hammen 1991, Ledru 1993,
Van der Hammen and Absy 1994, Ledru et al. 1996, Ferraz-
Vicentini and Salgado-Labouriau 1996, Salgado-Labouriau
1997, Salgado-Labouriau et al. 1997, 1998, Barberi et al.
2000, Saniotti 2002, Cruz et al. 2005, 2006, 2009, Cheng
used to determine ecological indicators of community types,
habitat conditions, and environmental changes (Dufrêne
and Legendre 1997, Carignan and Villard 2002, Niemi
and McDonald 2004, De Cáceres and Legendre 2009, De
Cáceres et al. 2010, 2012).
Our conclusions are based upon palaeoclimate simulations
derived from GCMs, which are known to be inaccurate,
particularly in simulating precipitation (Stainforth et al.
Figure 2. Predicted occupancy across northern South America of ten tree species that are indicators of typical cerrado vegetation during:
(A) – the Last Interglacial (LIG 130 ka BP); (B) – the Last Glacial Maximum (LGM 21 ka BP); (C) – the Mid-Holocene (6 ka BP); and
(D) – under Current climate (0 ka pre-industrial). Predictions were based on ecological niche models of climatic preference developed
separately for each species using the MaxEnt algorithm (Phillips et al. 2006). Predicted occupancy was then summed across all ten species.
Warmer colours (red/yellow) of the logistic output correspond to regions with a higher probability of occurrence. Black lines represent the
borders of Brazilian states and South America countries.
Santarém (Haffer 1969, Figueroa and Nobre 1990, Van Der
Hammen and Absy 1994). Although most of this region
is forested, numerous isolated savannas are found there,
and it connects the savannas of central Venezuela with the
savannas of central and northeastern Brazil (Haffer 1969).
Ab’Saber (2003) suggested the existence of savanna cor-
ridors in Amazonia during the Quaternary, though he was
not certain about the period when such corridors may have
existed. He also hypothesised that the corridors probably
linked present-day disjunct patches of Amazonian savannas.
Our models provide some corroboration for this idea, show-
ing the expansion of cerrado species toward many of these
currently disjunct savannas (Sanaiotti et al. 2002), such as
Alter do Chão, Amapá, Redenção, Roraima, Humaitá and
the Beni in Bolivia.
Our results are congruent with those of Werneck et al.
(2012) who also suggested past connections of the cerrado
to other areas of savanna in South America during the LIG
and a lack of significant savanna areas or corridors across
central Amazonia during the LGM. Baker and Fritz (2015)
discussed the importance of applying a salinity and tempera-
ture correction to d18O isotopic records. When these cor-
rections are applied to the mean value of d18O during the
LGM in Amazonia (Cheng et al. 2013), this substantially
alters previous climatic interpretations that the Amazon was
‘severely dry’ during the LGM. ese findings all contrast
with one assumption of the Pleistocene Refuge eory
(Haffer 1969, Prance 1982, Whitmore and Prance 1987),
which implicated an LGM savanna expansion due to drier
Palaeoecological studies from localities across lowland
tropical South America support a decrease in temperature
et al. 2013, Baker and Fritz 2015). One important point
that is clear from these studies is that climatic changes were
probably not synchronised across lowland tropical South
America; rather, different parts of South America may have
experienced climatic change in different directions at the
same time. Predicting the exact history of dispersal, extinc-
tion and recolonization of any typical cerrado tree species
across lowland tropical South America is therefore challeng-
ing. us, here we try and focus on general patterns that
can be inferred from our multi-species, palaeodistribution
modelling approach.
Cerrado distribution during the LIG, LGM and
Climate models suggest a warmer and slightly drier climate
during the LIG in those areas of the present-day Atlantic
and Amazon rain forests into which the cerrado tree spe-
cies modelled here are suggested to have expanded. Seasonal
climates expanded toward the Atlantic coast in southeast-
ern Brazil, and the palaeomodel indicated suitable areas for
typical cerrado species near the coast, e.g. in the Paraíba
river valley, in Rio de Janeiro and São Paulo. In fact, there
were small remnants of cerrado in this region, most of which
have disappeared due to habitat alteration in the last century
(Matsumoto and Bittencourt 2001).
e modelled expansion of typical cerrado tree species
into the Amazon during the LIG is particularly notable
within the ‘Amazonian Dry Corridor’, a transverse zone with
mean annual precipitation below 1750 mm extending in a
northwest-southeast direction near the cities of Óbidos and
Figure 3. Predicted occupancy of ten tree species that are indicators of typical cerrado vegetation during the Last Glacial Maximum (LGM
21 ka BP) showing the main highland systems of central Brazil and the low suitability of higher altitudes. Black lines are stat borders.
Warmer colours (red/yellow) correspond to regions with a higher probability of occurrence for all ten species. See Fig. 2 and text for further
in the Cerrado Domain, particularly in the Central Brazilian
Highlands. For example, LGM palaeorecords of Salgado-
Labouriau et al. (1997) and Barberi et al. (2000) infer a
prevalence of cold and semi-arid climates in those highlands,
with strong winds, partial soil exposure and concomitant
increased erosion, based on the almost complete absence
of arboreal pollen elements. Our LGM models suggest
that cerrado tree species persisted at lower altitudes, prob-
ably favoured by a warmer climate, deeper soil and higher
ground water storage than at higher altitudes. us, the
inter-tableland depressions and highland slopes of central
Brazil may have been refugia for cerrado species, rather than
the highlands where climates were too cold and dry, as
suggested by Ab’Saber (2003) and Werneck et al. (2012).
Our model, showing a retraction of major areas of typi-
cal cerrado vegetation during the LGM, is also corrobo-
rated by recent studies of population genetics in cerrado
tree species (Ramos 2007, Novaes 2010, Lima et al.
2014). Phylogeographic studies of Hymenaea stignocarpa,
Plathymenia reticulata, Tabebuia aurea and Mauritia flexuosa
found greater genetic diversity in the central region of the
Cerrado Domain, which is indicative that this area could
have been more stable during the LGM. A study of the
during the LGM, indicated by the expansion of cold-
adapted taxa, which are currently either relictual elements
in Amazonia and the Central Brazilian Highlands, such as
Podocarpus, Ilex, Myrsine and Hedyosmum (Colinvaux et al.
1996, Cardenas et al. 2011), or have vanished completely,
like Araucaria (Ledru 1993). On the other hand, during
the LGM there was a drastic retraction in the occurrence
of the tropical palm Mauritia, which has been considered
as an indicator of higher temperatures (Barberi et al. 2000),
as well as the disappearance of tree species characteristic of
seasonally dry tropical forest in eastern Bolivia (Whitney
et al. 2013).
Many authors agree that climate in the central area of
the Cerrado Domain during the LGM was characterized by
a decrease in both precipitation and temperature (Ferraz-
Vicentini and Salgado-Labouriau 1996, Barberi et al. 2000,
Lima-Ribeiro et al. 2004). However, according to Salgado-
Labouriau et al. (1998), there was no synchronicity of LGM
climates inferred from palynological studies in the Cerrado
Domain, which they attributed to differences in latitude and
regional topography.
Our models emphasize low climatic suitability during the
LGM for cerrado tree species at high altitudes (above 800 m)
0 model
0360 720 1,440
Datum WGS, 1984
1 model 2 models 3 models 4 models
Figure 4. Predicted regions of historical stability for typical cerrado vegetation across the Quaternary, based on summing the predicted
occupancy of ten indicator tree species across Current (0 ka pre-industrial), Mid-Holocene (6 ka BP), Last Glacial Maximum (LGM 21 ka
BP) and Last Interglacial (LIG 130 ka BP) climatic scenarios. Areas in yellow are those where all ten species are predicted to occur at all four
time periods, and represent postulated refugial areas for typical cerrado vegetation. Areas outlined in red are Brazilian conservation units,
while black lines represent the limits of Brazilian states and South America countries. Maps are given for (A) northern South America,
(B) the central area of the Cerrado Domain, and (C) the Federal District.
of a vegetation mosaic with a predominance of typical cer-
rado species, interspersed with forest and wet grassland for-
mations, is suggested by numerous authors (Oliveira-Filho
and Ratter 1995, 2002, Ab’Saber 2003, Ribeiro and Walter
2008). In the modelled current potential distribution, areas
of the central Cerrado Domain are maximally suitable for
the occurrence of typical cerrado tree species, particularly
on the central Brazilian tablelands. is finding is corrobo-
rated by Ratter et al. (2003) and Bridgewater et al. (2004),
who demonstrated that areas of the central Cerrado Domain
show the highest species richness of cerrado tree species.
is high diversity may reflect the stability of the central
Cerrado Domain throughout the timespan of our climate
models. Other studies have indicated that the stability of cli-
mate through time facilitates the accumulation and mainte-
nance of diversity in Neotropical vegetation (Graham et al.
2006, Carnaval et al. 2009, Werneck et al. 2012). e persis-
tence of some species in multiple refugia located throughout
their present distribution indicates that these species might
have persisted through multiple climatic cycles in heteroge-
neous environments (Keppel et al. 2012, Turchetto-Zolet
2013). e microrefugia (yellow areas in Fig. 4) are small
areas with favourable environmental features within which
small populations could have survived when their main dis-
tribution area contracted (Rull 2009, 2011, Vegas-Vilarrubia
et al. 2011). ese areas of historical climate stability likely
allowed a number species to persist through time, whereas
extinction took place in areas that experienced the most
severe climate changes. is then likely resulted in greater
diversity in more stable areas (Rull 2008, 2011, Collevatti
et al. 2012, Keppel et al. 2012).
ere has been a great loss in species diversity and
endemism in important areas of the cerrado, as a result of
disturbance, and total clearance, by humans, especially due
to the expansion of agriculture, cattle ranching, and charcoal
production (Ratter et al. 1997, Silva and Bates 2002). ere
are estimates that less than 20% of the Cerrado Domain veg-
etation remains undisturbed while only 7.44% is legally pro-
tected in conservation units. Meanwhile, many threatened
species remain outside any of the regions parks and reserves
(MMA 2011) contributing to the status of the Cerrado
Domain as one of the world’s biodiversity hotspots, deserv-
ing urgent conservation intervention (Myers et al. 2000).
In our model, climatically stable areas are mostly outside
the existing protected areas. e few exceptions are those
located in the Federal District and a number of Environmental
Protection Areas (APA; a lesser protection level) in Tocantins
state (Fig. 4). Larger climatically stable areas in Minas Gerais
and São Paulo states have no conservation units (Fig. 4). We
suggest that the areas identified as climatically stable in our
analyses should be incorporated into systematic conservation
planning to preserve the cerrado tree flora, as they represent
probable refugial areas with potentially high species and
genetic diversity.
Palaeodistribution modelling of tree species representative of
typical cerrado vegetation showed expansions and contrac-
tions related to the climatic fluctuations of the Quaternary,
phylogeography of the tree species Caryocar brasiliense by
Collevatti et al. (2003, 2012) showed that multiple lineages
may have contributed to the present-day populations of
Caryocar brasiliense in the Cerrado Domain, and that popu-
lations restricted to refugia in the central region during the
LGM may have spread and dispersed to favourable areas in
the last 7000 yr. Moreover, in his revision of Neotropical
Andira, Pennington (2003) highlighted a north to south
parapatric distribution of Andira cuyabensis and Andira
cordata across the centre of the Cerrado Domain, perhaps
related to a prior separation of the currently continuous
typical cerrado vegetation during the LGM, as also suggested
by the palynological data of Ledru (1993).
At the end of the LGM, between 17 000 and 11 000 BP,
the climate became progressively more humid. However,
permanent polar fronts remained at 10°S–20°S latitude
( 8500 BP), inferred from the presence of Araucaria forests
(now confined to southern and southeastern Brazil) and the
association of temperate-adapted Podocarpus with Caryocar
in areas presently covered by typical cerrado (Ledru 1993,
Ledru et al. 1996). With increasing temperatures, the cold
weather elements were probably confined to higher altitudes,
principally in gallery forests, a hypothesis supported by the
presence of Podocarpus in the higher plateaux of the Federal
District and Chapada dos Veadeiros (Barberi et al. 2000).
e return of warmer, humid conditions in the Mid-
Holocene would have favoured the expansion of typical
cerrado vegetation in the core area of the Cerrado Domain
(Oliveira-Filho and Ratter 2000). e appearance of
Mauritia (Barberi et al. 2000, Ledru 2002, Lima et al. 2014)
and the increasing concentration of charcoal particles, are
both associated with increasing temperatures and the re-
expansion of cerrado vegetation (Salgado-Labouriau 1997).
ese changes are corroborated by palaeoecological studies
from various localities and supported by our palaeomodels
for 6000 BP. During this period, Behling (1995) recorded
an increase of species typical of cerrado vegetation, such
as Curatella americana, in the Lagoa do Pires between the
Cerrado and Atlantic Forest Domains in Minas Gerais state.
In the state of Rondônia, there was an isotopic enrichment
related to the replacement of forest vegetation by typical cer-
rado vegetation (Pessenda 1998a), as also observed in the
region of Humaitá, in the south of Amazonas state (Gouveia
et al. 1997, Pessenda 1998b, De Freitas et al. 2001). At
the Bolivian border with Brazil, in an area now covered
by Amazonian forest, Mayle et al. (2000) and Mayle and
Whitney (2012) also recorded the presence of Curatella and
Mauritia during the same period. is find is compatible
with a trend of continuously increasing pollen deposition of
typical cerrado taxa in the period (Barbieri et al. 2000, Ledru
2002). e patterns may have been accentuated by soil
leaching and acidification, which would also have favoured
the expansion of typical cerrado vegetation (Oliveira-Filho
and Ratter 2000).
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Acknowledgements – is study was in partial fulfilment of the
Doctoral requirements of MLB who thanks CNPq for supporting
a 12-month study period at the Royal Botanic Garden Edinburgh
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Supplementary material (Appendix ECOG-01860 at
< >). Appendix 1.
... We considered savanna a vegetation complex which includes three types of physiognomies, namely: open savanna, woody savanna and savanna woodland (Coutinho, 1978;Furley, 1999Furley, , 1992. The vegetation complex predominates in ecoregions which are typically savannas, such as the Llanos, Gran Sabana, Beni Savanna, and Cerrado (Olson et al., 2001), but disjunct savannas areas occur in non-savanna ecoregions as a result of the expansion and retraction of the savanna through the glacial cycles especially in the Neogene and Quaternary (Berrio et al., 2002;Bueno et al., 2017), such as in the Amazon ( Barbosa and Fearnside, 2004), Caatinga (Castro et al., 1999;Vieira et al., 2019), Chacos (Kunst et al., 2006;Morales et al., 2019), and Atlantic forest (Costa-Lima and Chagas, 2019; Moura et al., 2011). Although the macro-conditions (i.e., temperature and precipitation) in non-savanna ecoregions are different from savanna ecoregion conditions, local variations of soil and topography (Goodland and Pollard, 1973) or disturbance regime such as fire (Pivello, 2011;Pivello et al., 2021) support savanna vegetation in non-savanna ecoregions. ...
... Therefore, different from the Atlantic Forest where stenochory and stenoecy were the main parameters demining rarity (Caiafa and Martins, 2010), scarce population and stenochory are the main parameters determining rarity in the SAS. Many species which are now considered characteristic of the Cerrado experienced their maximum expansion during the Last Interglacial period (Bueno et al., 2017). Regions that include disjunct savannas currently had suitable climatic conditions for the expansion of the savanna in the past (Bueno et al., 2017;Haffer, 1969). ...
... Many species which are now considered characteristic of the Cerrado experienced their maximum expansion during the Last Interglacial period (Bueno et al., 2017). Regions that include disjunct savannas currently had suitable climatic conditions for the expansion of the savanna in the past (Bueno et al., 2017;Haffer, 1969). Climate conditions such as precipitation and temperature are quite different among regions in the Quaternary period (Auler and Smart, 2001). ...
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The interest in quantifying rare species has been increasing, but less attention has been paid to analysing their conservation status. Here, we used the Rabinowitz method based on geographical range, habitat specificity and population size to classify 2,203 tree species of South American savannas (SAS). We considered species with narrow (stenochoric) or wide (eurychoric) geographic range respectively occurring in up to 10% or over of the latitudinal belts in the SAS, specialist (stenoecious) or generalist (euryoecious) species occurring in one or more ecoregions, respectively, and locally scarce or abundant populations of species with low or high numbers of records within a grid cell of 1° latitude by 1° longitude, respectively. We then quantified species which only occur inside protected areas (PAs), in and outside PAs, or only outside PAs. Of the 2,203 species, 49.25% were rare, 40.35% stenochoric, 14.12% stenoecious and 56.15% had a scarce population. The Cerrado (433) followed by Caatinga (259), Campos Rupestres montane savanna (256), Bahia interior forests (189) and Guiana savanna (154) had the highest number of rare species. Only 6.44% species only occurred inside PAs, 83.79% in and outside PAs and 9.75% only outside PAs. Unprotected species are mostly geographically restricted with ecoregion specialists, and have small population sizes. The number of protected species are is positively correlated with the number of records within them. The establishment of PAs should focus on both core and disjunct savannas to encompass all ecoregions in order to ensure the conservation of species and the range of evolutionary processes in SAS.
... Sobretudo, pode também alterar a fisiologia das plantas, uma vez que a poluição se torna disponível para a absorção da planta e para infiltração no solo, podendo ser, inclusive, fitotóxica para a superfície foliar. Além disso, a emissão desses gases pode contribuir, a longo prazo, para o aumento dos gases do efeito estufa e, consequentemente, para a ocorrência de alteração na composição florística e fitossociológica (Bueno et al., 2017). ...
... A localização da UTGCA e as peculiaridades climáticas da região do presente estudo podem favorecer a contaminação da água da chuva (Högberg, 2007), alterando o balanço de nutrientes e mudando a relação de competição entre espécies, causando queda e alteração na diversidade florística em longo prazo (Bueno et al., 2017). Assim, torna-se imprescindível que façamos o diagnóstico destas áreas do NCR que estão na vertente direcional à UTGCA e que poderão receber a pluma de poluição da usina. ...
É necessário compreender a diversidade da Mata Atlântica para monitorar possíveis impactos das mudanças climáticas e mitigar o desaparecimento deste hotspot de biodiversidade. Apresentamos dados do Parque Estadual da Serra do Mar, Núcleo Caraguatatuba (NCR), com objetivo principal do conhecimento florístico, fitossociológico e similaridade das áreas florestais. Os dados foram coletados em parcelas permanentes de 1 ha, incluindo espécies com diâmetro ≥ 15 cm (PAP; 1,30 m de altura do solo), para conhecimento das áreas e para testes de similaridade entre as parcelas dos núcleos Picinguaba e Santa Virgínia, de mesma cota altitudinal. São apresentados tabelas florísticas das áreas, análise de UPGMA e teste de Mantel, para verificar o agrupamento das áreas. As famílias com maior índice de valor de importância foram Euphorbiaceae, Myrtaceae, Rubiaceae, Lauraceae, Arecaceae e Fabaceae, na parcela do NCR Submontana 1, e Myrtaceae, Sapotaceae, Monimiaceae, Nyctaginaceae, Lauraceae, Arecaceae e Rubiaceae, na parcela do NCR Montana 1. Através dos testes, foi possível verificar similaridades entre as áreas. Em alguns casos, ocorreu dissimilaridade, que estaria ligada a possíveis fatores ambientais e antrópicos, os quais não foram testados para afirmação, sugerindo estudos futuros a médio e longo prazo.
... While we recognize that the caatinga forests and woodlands can support high richness of annual herbs, we do not consider caatinga to be grassy ecosystems, due to shrub and tree dominance and discontinuous herbaceous cover. In some regions, however, the Caatinga does harbor small savanna areas ( Fig. 3c) that are probably remnants of larger savannas that formed during Pleistocene climatic fluctuations (Bueno et al., 2017;Costa et al., 2018) and that persist today due to frequent fire and edaphic factors (de Castro . While many woody Caatinga species can colonize these areas, in large savanna patches on highlands like the Araripe Plateau or the Chapada Diamantina, the flora is mostly composed by species that also occur in savannas of the Cerrado; these sites have greater similarity with the Cerrado flora of central Brazil than with adjacent Caatinga woodlands (Nepomuceno et al., 2021). ...
In Brazil, the country with the highest plant species richness in the world, biodiverse savannas and grasslands – i.e., grassy ecosystems, which occupy 27% of the country – have historically been neglected in conservation and scientific treatments. Reasons for this neglect include misconceptions about the characteristics and dynamics of these ecosystems, as well as inconsistent or regionally restricted terminology that impeded a more adequate communication about Brazil's savannas and grasslands, both within the country and internationally. Toward improved communication and recognition of Brazil’s diversity of ecosystems, we present the key drivers that control the main types of grassy ecosystems across Brazil (including in regions of the country where forests dominate). In doing so, we synthesize the main features of each grassy ecosystem in terms of physiognomy and ecological dynamics (e.g., relationships with herbivores and fire). We propose a terminology both for major grassland regions and for regionally relevant vegetation physiognomies. We also discuss terms associated with human land management and restoration of grassy ecosystems. Finally, we suggest key research needs to advance our understanding of the ecology and conservation values of Brazil’s grassy ecosystems. We expect that a common and shared terminology and understanding, as proposed here, will stimulate more integrative research that will be fundamental to developing improved conservation and restoration strategies.
... Ecological indicators of habitat types or environmental conditions (i.e., indicator or diagnostic species) have been used successfully for modeling the distribution of vegetation types (Bueno et al., 2016;Esser et al., 2019). Here, we used a non-exhaustive set of 18 indicator tree species as a proxy to model the current and potential distribution of Araucaria moist forests (Appendix S1). ...
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Aim: Araucaria moist forests are particularly vulnerable to climate change due to their strict climatic requirements and patchy distribution. Therefore, identifying areas where these forests are expected to lose or retain climatically suitable space (i.e., climate change refugia) is urgently required. Here, we modeled the current and future climatic suitability for the Araucaria moist forests aiming (a) to identify areas of suitable climate (i.e., in situ and ex situ refugia), (b) to identify areas of climate retraction, and (c) to assess the effectiveness of protected areas to capture climatically suitable space. Location: Araucaria moist forests ecoregion, southern Brazil, and northeast Argentina. Methods: We mapped the potential distribution of the Araucaria moist forests using an ensemble forecasting approach with 18 indicator tree species (all wet- and cold-adapted taxa), six algorithms, eight global circulation models, three representative concentration pathways (RCPs 4.5, 6.0, and 8.5), and three periods (current, 2050, and 2070). Results: We predicted substantial losses of future climatic suitability across almost the entire range where these forests occur, ranging from 43 to 64% under optimistic (RCP4.5/2050) and high emissions (RCP8.5/2070) scenarios. We found that the protected areas network captured only 3% of the climatically suitable space under current conditions. We found that only 4% (top 1% of cells) and 12% (top 5% of cells) of the potential refugia would be protected in the future, with less than half of their areas corresponding to in situ refugia. Conclusions: Projected losses of potential distribution and the low efficacy of protected areas to buffer climate-change impacts point to a high-risk scenario for the Araucaria moist forests in the near future. Cold-adapted tree species likely will face increased extinction risk, especially as climate change will interact with other anthropogenic drivers.
... Much of the Cerrado is distributed over the Brazilian Central Plateau (Sano et al., 2010). The Cerrado vegetation has a gradient of physiognomies; from pure grasslands to forests, however, savanna predominates (Bueno et al., 2017;Borghetti et al., 2019). Although separated by the Amazon basin, these two regions share several species, suggesting that they were in some way connected in the past (Silva and Bates, 2002;Prance, 2006;Furley, 2007). ...
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Functional traits related to regeneration responses to the environment are highly determinants of distribution patterns of plant communities. A large body of studies on seed traits suggests that regional climate may act as a strong filter of plant recruitment; however, few studies have evaluated the relative importance of seed traits and environmental filters for seed persistence at the population level. We tested the role of seed mass, water content and desiccation tolerance, as well as the germination time as proxies for seed tolerance to environmental filters (water deficit, heat shock and high temperatures) by comparing the response of tree species co-occurring in savannas located in different regions: Cerrado biome of Central Brazil and the Rio Branco savannas of northern Brazil. Seeds collected in savannas of Rio Branco showed a higher tolerance to environmental filters than those collected in savannas of the Cerrado. While the germination percentages largely varied in response to the treatments, the germination times were virtually unaffected by them, irrespective of seed origin, seed mass and water content. At the population level, the regional environment was a key determinant of seed tolerance to stress, irrespective of seed traits. Germination time was shown to represent a conservative seed trait and more linked to a species-specific germination strategy than to regional characteristics. Our results suggest that recruitment patterns of Cerrado savannas may be more impacted than Rio Branco savannas by the climate scenarios predicted for the future.
... Aqui, cabe a ressalva de que esses dois biomas (Cerrado e Mata Atlântica) são importantes representantes da vegetação brasileira, pois abrigam extensas áreas do território nacional, apresentando ampla biodiversidade de plantas e animais, elevados índices de endemismos, além de estarem entre os mais ameaçados ecossistemas do Brasil (RIZZINI, 1997;BUENO et al., 2016;SOS MATA ATLÂNTICA, 2019a). Por essa razão, ambos são classificados como Hotspots mundiais de biodiversidade, que segundo Myers (1988) são locais caracterizados por apresentarem níveis excepcionais de endemismo de plantas, assim como taxas notáveis de destruição de habitats. ...
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O livro consta de quatro partes. Na Parte I abordamos um pouco da vida de Saint-Hilaire na França: sua origem, vocação e a carreira como botânico antes de sua vinda ao Brasil, em 1816. No segundo capítulo apresentamos a concepção do "Caminho Saint Hilaire", uma trilha de longo curso que serpenteia a Reserva da Biosfera na Serra do Espinhaço Meridional. Na Parte II, buscamos reverberar a importância paisagística e sua biodiversidade quando da passagem de Saint-Hilaire pela Serra do Espinhaço Meridional. A Parte III busca descrever, a partir das obras do naturalista, a riqueza das construções pelo caminho. E a Parte IV é composta por capítulos que remetem à concepção do projeto "Caminho Saint Hilaire", uma inspiradora trilha de longo curso entre Diamantina, Serro e Conceição do Mato Dentro. Esperamos que você, leitor, viaje conosco na companhia de Saint-Hilaire!
... Pollen records suggest that grasslands covered large areas of southern Brazil during the most recent glacial maximum, which are now covered with tropical forest and savanna (Behling 2002). Paleo-niche models also suggest range contraction of neotropical savanna trees toward central Brazil and eastern Bolivia and to lower altitudes during the last glacial maximum likely related to decreased temperatures and precipitation and their expansion during the warmer and moister last interglacial and the Mid-Holocene (Bueno et al. 2017). ...
One of the core issues in community ecology is the understanding of mechanisms that determine community structure. In this study, we examine how two structurally distinct habitats (campo sujo – a grassy savanna habitat with low shrubby cover – and seasonal semi‐deciduous forest) and distinct hydrological seasons (dry and rainy) influence the taxonomic, functional and phylogenetic diversity of lizard assemblages in a savanna area in the Brazilian Cerrado. We used pitfall traps to sample lizards from May 2000 to February 2002. To quantify spatio‐temporal changes in the lizard assemblages, we used parameters of taxonomic (species richness – SR), functional (functional diversity – SES.FD, functional redundancy – FR and functional dispersion – FDis), and phylogenetic diversity (phylogenetic species richness – PSR and phylogenetic species variability – PSV). We also estimate functional and phylogenetic structure of the assemblages in each habitat during dry and rainy seasons. We recorded 182 lizards distributed among 14 species. Species composition differed among habitat types, but did not differ seasonally within habitats. SES.FD, FDis, and FR also differed among habitat types but not among seasons, with SES.FD and FDis being greater in seasonal semi‐deciduous forest, while FR was greater in campo sujo. SR, PSR, and PSV were not influenced by the factors analysed. The lizard assemblage of campo sujo was functionally clustered in the dry season and phylogenetically clustered in the rainy season. These results demonstrate that differences among habitat types and seasons are important in shaping the taxonomic, functional, phylogenetic diversity and structure of lizard assemblages in the savanna area studied. Our study also demonstrates the importance of using different measures of diversity to obtain a better understanding on the mechanisms that influence the lizard assemblages in a highly seasonal environment.
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The maximum entropy (MaxEnt) model for predicting the potential suitable habitat of species has been commonly employed in many ecological and biological applications by using presence-only occurrence records along with associated environmental factors. Parnassia wightiana , a perennial herb, is a cold-adapted plant distributed across three diversity hotspots in China, including the Hengduan Range, Central China and the Lingnan region. The MaxEnt model was used to simulate the historic, current and future distribution trends of P. wightiana , as well as to analyse its distribution pattern in each historical period and explore the causes of species distribution changes. The results of our analysis indicated that annual precipitation, annual temperature range and mean temperature of the warmest quarter were the key bioclimatic variables affecting the distribution of P. wightiana . Most temperate species retracted into smaller refugial areas during glacial periods and experienced range expansion during interglacial periods. Possible refugia of the species were inferred to be located in the Hengduan Range and Qinling Regions.
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O objetivo foi abordar um mosaico de vegetação de savana (áreas marginais-MS e disjuntas-DS) no Cerrado Setentrional Brasileiro para investigar o papel desempenhado por fatores ambientais como determinantes da organização comunitária em escala espacial, a fim de compreender os padrões divergentes ao longo de uma gradiente ambiental. Analisamos preditores espaciais, edáficos e climáticos em 21 comunidades arbóreas do Cerrado, compreendendo 235 espécies, 154 gêneros e 52 famílias. Os resultados sugerem uma dependência espacial significativa entre as assembleias, apesar de funcionarem como sistemas ecológicos independentes. Eles também confirmaram que embora os efeitos das concentrações dos atributos edáficos não fossem homogêneos, evidenciaram que fatores climáticos e espaciais foram os responsáveis pela maior explicação dos dados. As análises de ordenação indicaram um gradiente ambiental com alta rotatividade de espécies e um mosaico de floras individuais ao longo do gradiente espacial. Oito espécies contribuíram com pelo menos 70% do faturamento entre os subgrupos. Os drivers mais influentes foram precipitação, amplitude térmica, elevação, espacialização latitudinal longitudinal das áreas e teor de alumínio.
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Indicator species are species that are used as ecological indicators of community or habitat types, environmental conditions, or environmental changes. In order to determine indicator species, the characteristic to be predicted is represented in the form of a classifi cation of the sites, which is compared to the patterns of distribution of the species found at the sites. Indicator species analysis should take into account the fact that species have diff erent niche breadths: if a species is related to the conditions prevailing in two or more groups of sites, an indicator species analysis undertaken on individual groups of sites may fail to reveal this association. In this paper, we suggest improving indicator species analysis by considering all possible combinations of groups of sites and selecting the combination for which the species can be best used as indicator. When using a correlation index, such as the point-biserial correlation, the method yields the combination where the diff erence between the observed and expected abundance/frequency of the species is the largest. When an indicator value index (IndVal) is used, the method provides the set of site-groups that best matches the observed distribution pattern of the species. We illustrate the advantages of the method in three diff erent examples. Consideration of combinations of groups of sites provides an extra fl exibility to qualitatively model the habitat preferences of the species of interest. Th e method also allows users to cross multiple classifi cations of the same sites, increasing the amount of information resulting from the analysis. When applied to community types, it allows one to distinguish those species that characterize individual types from those that characterize the relationships between them. Th is distinction is useful to determine the number of types that maximizes the number of indicator species.
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The Cerrado, which includes both forest and savanna habitats, is the second largest South American biome, and among the most threatened on the continent.
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This study, which was carried out in the southern Brazilian Amazon region (Rondônia state and Humaitá, Southern Amazon state), presents and discusses the significance of carbon isotope data measured in soil profiles collected across natural boundaries of forest to savanna vegetation. The main objective of this study was to evaluate the expansion-regression dynamics of these vegetation units in relation to climate changes during the Holocene. 14C data from charcoal, soil organic matter (SOM) and its component humin fraction indicate that the organic matter in the studied soils is essentially Holocene in origin. 13C data indicate that C3 type plants were the dominant vegetation at all study areas in the early Holocene, and during the entire Holocene, in the forest sites of Central Rondônia state and in the forest site 50 km from the city of Humaitá. 13C data also indicate that C4 plants have influenced significantly the vegetation at the transitional forest and the Cerrado (wooded savanna) sites of Southern Rondônia state and the forest ecosystem located 20 km from the Humaitá city. These typical C4 type isotopic signatures probably reflect a drier climate during the mid-Holocene. The 13C records representing probably the last 3000 yr show an expansion of the forest, due to a climatic improvement, in areas previously occupied by savanna vegetation. These results and other published data for the Amazon region indicate that the areas representing today's forest-savanna boundaries have been determined by significant vegetation changes during the Holocene. The boundary between forest and savanna vegetation seems to be quite sensitive to climatic change and should be the focus of more extensive research to correlate climate and past vegetation dynamics in the Amazon region.
In the future, Arctic warming and the melting of polar glaciers will be considerable, but the magnitude of both is uncertain. We used a global climate model, a dynamic ice sheet model, and paleoclimatic data to evaluate Northern Hemisphere high-latitude warming and its impact on Arctic icefields during the Last Interglaciation. Our simulated climate matches paleoclimatic observations of past warming, and the combination of physically based climate and ice-sheet modeling with icecore constraints indicate that the Greenland Ice Sheet and other circum-Arctic ice fields likely contributed 2.2 to 3.4 meters of sea-level rise during the Last Interglaciation.