Lightning Fires in a Brazilian Savanna National Park: Rethinking Management Strategies

Abstract

Fire occurrences and their sources were monitored in Emas National Park, Brazil (17°49′–18°28′S; 52°39′–53°10′W) from June
1995 to May 1999. The extent of burned area and weather conditions were registered. Forty-five fires were recorded and mapped
on a GIS during this study. Four fires occurred in the dry winter season (June–August; 7,942 ha burned), all caused by humans;
10 fires occurred in the seasonally transitional months (May and September) (33,386 ha burned); 31 fires occurred in the wet
season, of which 30 were caused by lightning inside the park (29,326 ha burned), and one started outside the park (866 ha
burned). Wet season lightning fires started in the open vegetation (wet field or grassy savanna) at a flat plateau, an area
that showed significantly higher fire incidence. On average, winter fires burned larger areas and spread more quickly, compared
to lightning fires, and fire suppression was necessary to extinguish them. Most lightning fires were patchy and extinguished
primarily by rain. Lightning fires in the wet season, previously considered unimportant episodes, were shown to be very frequent
and probably represent the natural fire pattern in the region. Lightning fires should be regarded as ecologically beneficial,
as they create natural barriers to the spread of winter fires. The present fire management in the park is based on the burning
of preventive firebreaks in the dry season and exclusion of any other fire. This policy does not take advantage of the beneficial
effects of the natural fire regime and may in fact reduce biodiversity. The results presented here stress the need for reevaluating
present policies and management procedures concerning fire in cerrado conservation areas.

Full text

Lightning Fires in a Brazilian Savanna National Park:
Rethinking Management Strategies
MA
´RIO BARROSO RAMOS-NETO
VA
ˆNIA REGINA PIVELLO*
Departamento de Ecologia, Instituto de Biocieˆ ncias
Universidade de Sa˜ o Paulo
Rua do Mata˜o
Travessa 14, Sa˜ o Paulo, S.P., Brazil 05508-900
ABSTRACT / Fire occurrences and their sources were moni-
tored in Emas National Park, Brazil (17°49⬘–18°28⬘S; 52°39⬘–
53°10⬘W) from June 1995 to May 1999. The extent of burned
area and weather conditions were registered. Forty-five fires
were recorded and mapped on a GIS during this study. Four
fires occurred in the dry winter season (June–August; 7,942
ha burned), all caused by humans; 10 fires occurred in the
seasonally transitional months (May and September) (33,386
ha burned); 31 fires occurred in the wet season, of which 30
were caused by lightning inside the park (29,326 ha burned),
and one started outside the park (866 ha burned). Wet season
lightning fires started in the open vegetation (wet field or
grassy savanna) at a flat plateau, an area that showed signifi-
cantly higher fire incidence. On average, winter fires burned
larger areas and spread more quickly, compared to lightning
fires, and fire suppression was necessary to extinguish them.
Most lightning fires were patchy and extinguished primarily by
rain. Lightning fires in the wet season, previously considered
unimportant episodes, were shown to be very frequent and
probably represent the natural fire pattern in the region. Light-
ning fires should be regarded as ecologically beneficial, as
they create natural barriers to the spread of winter fires. The
present fire management in the park is based on the burning
of preventive firebreaks in the dry season and exclusion of any
other fire. This policy does not take advantage of the beneficial
effects of the natural fire regime and may in fact reduce biodi-
versity. The results presented here stress the need for reevalu-
ating present policies and management procedures concern-
ing fire in cerrado conservation areas.
There is a consensus that fire has been occurring in
tropical savannas for thousands of years, shaping the
landscape and selecting for adapted flora and fauna. It
has also been accepted that ancient fires were caused by
natural events, mostly lightning, but also by volcanic
activity and friction between rocks. Nevertheless, after
humans came to gather in social groups, they became
the main cause of wildfires, greatly increasing the fire
frequency and changing fire regimes, from cool wet-
season fires to more intense dry-season fires (Komarek
1972, Edwards 1984, Coutinho 1990, Goldammer 1993,
Pyne 1993, Whelan 1995).
However, the belief that almost all tropical fires at
present are anthropogenic has not been adequately
demonstrated. Lightning fire outbreaks are poorly doc-
umented in tropical ecosystems, although there are
some records (Tutin and others 1996, Middleton and
others 1997). In Brazil, it was probably this lack of
recorded fire strikes that led to the opinion that light-
ning fires are rare in cerrados, the Brazilian savannas.
As Soares (1994) states “in cerrados...lightning might
even be an important cause for fires; however, studies
to confirm or to reject this hypothesis do not exist.”
The cerrado biome is the second largest realm in
Brazil, occupying over 1.8 million km
2
on the Brazilian
Central Plateau, at altitudes from 300 to 1,000 m above
sea level (Ab’Saber 1971). Although patches of forest
and grassland forms appear in the cerrado landscape, it
is dominated by savanna forms, in a gradient from open
grassy to woodland savannas. The more open the sa-
vanna structure, the more fire prone it is. On the other
hand, forest patches are not fire prone and only burn
when fire is intense.
The tropical humid climate in the cerrado region,
with a dry winter (3–6 months) and a wet summer,
imposes a strong seasonality to the vegetation, espe-
cially grasses, which dry out in the winter. At this time
of the year, cattle grazers used to burn cerrados to
promote grass regrowth and to supply palatable forage
to cattle. Subsistence farmers also used to burn arable
areas to prepare the land for cultivation in the wet
season. Therefore, cerrados managed in these ways
(almost all, except the natural reserves) sustain little
fuel to be burned by natural lightning fires in the next
wet season.
Hence, especially because of the management that
humans apply to cerrados, the burning season runs
from May to September, when the herbaceous vegeta-
KEY WORDS: Wildfire; Lightning; Brazilian savanna; Cerrado; Fire man-
agement; Emas National Park
*Author to whom correspondence should be addressed.
DOI: 10.1007/s002670010124
Environmental Management Vol. 26, No. 6, pp. 675– 684 ©2000 Springer-Verlag New York Inc.

tion is dry and more flammable, and fire spreads easily
from farmlands to natural areas. Early fires in May–June
are usually cool fires and burn the area patchily as the
vegetation still has high water content. As the dry sea-
son continues the curing status of the grass layer in-
creases and fire intensity also tends to increase. Fire
outbreaks peak by the end of the dry season (July–
August) (Coutinho 1990, Pivello 1992, Mistry 1998). In
the early wet season (September–October), fire occur-
rences decrease, although the vegetation is still able to
carry a fire (H. S. Miranda, personal communication).
Present-day discussion on the causes of wildland
fires, a subject explored since the 1970s (Komarek
1972, Edwards 1984), is not only a matter of conjecture;
it may be important to management approaches and
policies for conservation areas. Yet, little concern given
to the natural fire dynamics in Brazil, and the miscon-
ceptions about fire effects in natural environments led
the governmental sectors responsible for nature con-
servation to reject any fire in cerrado conservation ar-
eas, either natural or prescribed. The environmental
legislation, although very conservative, has permitted
the use of fire since 1989 for managing nature reserves
(Federal Decree No. 97635 from 10 April 1989) but, in
fact, decision-makers in the governmental body rarely
allow fire management in parks and reserves, even
though it can be a very useful and cheap management
tool.
Several environmental benefits may be brought by
fire in savannas, especially the stimulus to nutrient
recycling and to sprouting, fruiting, and seeding of
several plant species; it also increases the vigor and
palatability of a number of herbaceous species. Differ-
ent fire regimes (fire type, frequency, intensity, and
season) may favor distinct groups of species or may
consume more or less intensively the accumulated fuel
(Warming 1908, Coutinho 1980, 1982, 1990, Kruger
1984, Christensen 1985, Pivello 1992, Pivello and
Coutinho 1992, 1996, Whelan 1995, Pivello and Norton
1996). Such fire outcomes may result in management
ends, as wildfire control, food supply to native fauna,
weed control, and the maintenance of biodiversity and
ecological processes (Pivello 1992, Pivello and
Coutinho 1996, Pivello and Norton 1996).
As fire consumes the fuel, burned patches may act as
firebreaks to unburned areas and management burn-
ings can be used to avoid the spread of wildfires. Still, a
savanna landscape formed by a mosaic of unburned
patches and patches burned at different time intervals
is able to maintain a great variety of both sun-loving
fire-prone species and those from woodland savanna.
To achieve these goals, prescribed fires are used in
parks of diverse ecosystems worldwide as a management
tool, for example, in the North American Yellowstone
and Everglades national parks and in the Australian
Kakadu and Uluru national parks, among many others
(Saxon 1984, Parsons and others 1986, Schullery 1989,
Australian National Parks and Wildlife Service 1991,
Conroy and others 1997, Russel-Smith 1997).
In Brazilian protected areas, where an antifire policy
prevails, the consequence has been the occurrence of
periodic and severe wildfires, when fuels accumulate
and fire becomes inevitable, threatening animals and
humans. In Emas National Park and Chapada dos Vea-
deiros National Park, for example, severe fires occur
every 3–4 years (Redford 1985, Pivello 1992, 1996, Piv-
ello and Coutinho 1992, Franc¸a and Setzer 1997). Se-
vere wildfires in Emas National Park occurred in 1975,
1978, 1985, 1988, 1991, and 1994 and burned 74–93%
of the 132,133 ha of the park, killing a number of
vertebrates (I.B.D.F. 1981, Redford 1985, Silveira and
others 1996, Franc¸a and Setzer 1997). Furthermore,
the critical problem of invasions of alien grasses in
cerrados (Pivello et al. 1999a, 1999b) could, in some
cases, be controlled by low-intensity prescribed fires
(Pivello 1992, Pivello and Norton 1996).
The objective of this study is to demonstrate the
importance of lightning fires in the cerrados and to
emphasize the need to consider the beneficial effects of
these fires in management strategies. It is also impor-
tant to stress that we are justifying the use of prescribed
fires to manage savannas, and not tropical forests, as
the functioning and dynamics of these ecosystems are
totally different; as a rule, fire seriously damages trop-
ical forests (see Nepstad and others 1999).
The Study Area
Emas National Park is located in the core region of
the cerrado biome, the Brazilian savanna, in the SW of
Goia´s State, Central Brazil (17°49⬘–18°28⬘S and 52°39⬘–
53°10⬘W) (Figure 1). It is the largest (132,133 ha) and
most important protected cerrado area, because of its
diverse flora and fauna (I.B.D.F. 1981, Redford 1987).
In this park, cerrado fauna is abundant and easily ob-
served. Several threatened species, including the giant
armadillo (Priodontes maximus), giant anteater (Myrme-
cophaga tridactyla), pampa cat (Felis colocolo) and puma
(Felis concolor), still occur there (Redford 1983,
Machado and others 1998).
Regional climate is tropical and humid, with wet
summers and dry winters (June–August), typical of sa-
vannas (zonobiome II, according to Walter and Lieth)
(Walter 1971). Annual rainfall ranges from 1,200 to
2,000 mm (Franc¸a and Setzer 1997, and this study),
concentrated from October to March (Figure 2a). Ac-
676 M. B. Ramos-Neto and V. R. Pivello

cording to the rainfall and soil water regime, May and
September are considered transitional months, since
they represent, respectively, the end and the onset of
the rainy season (Figure 2). Frost is expected every
winter, in June and/or the beginning of July.
Three quarters of Emas National Park consist of flat
tableland, 820–888 m in elevation; the remaining area
consists of hilly terrain, 720–820 m in elevation. A
gradient of open savanna types (68.1%) and dense
savanna (cerrado sensu stricto) (25.1%) can be found in
the park, as well as wet fields (4.9%) and riparian and
mesophyllous forests (1.2%) (Figure 3).
Up to 1984, the park was exploited by farmers for
cattle ranching and fire was used to promote forage
regrowth. After that time, the park was totally fenced,
and cattle were no longer permitted inside it. Since
then, a policy of fire exclusion was established in the
park, except for the annual burning of 314 km of
preventive firebreaks (I.B.D.F. 1981, IBAMA 1993). In
spite of this, uncontrollable wildfires occur every 3–4
years (Franc¸a and Setzer 1997).
The federal government owns all the parkland, and
there are no residents inside it. Visitors to the park are
always accompanied by an authorized guide.
Methods
Fire occurrences in Emas National Park were re-
corded in the field from June 1995 to May 1999
through direct observation. Additionally, the park was
checked for evidence of spot fires, by airplane, on three
occasions during the study period. We recorded for
each fire, the time it started and stopped and local
weather conditions during the burn. After each fire, the
burned area was immediately visited in order to locate
its perimeter, with the aid of a GPS (global positioning
system). The location of the initial fire point was esti-
mated by analyzing the remaining grass stalks, ash pat-
terns, and wind behavior, as suggested by Cheney and
Sullivan (1997).
Local rainfall was registered during the study period
by 35 rain gauges installed in the park, and additional
climatic data were obtained from the nearest climatic
station, in Mosteiro Sa˜o Jose´, Mineiros Municipality,
GO (Franc¸a and Setzer 1997). The climatic data were
used to build a climatic diagram according to Walter
and Lieth (Walter 1971) (Figure 2a) and a water bal-
ance diagram, according to Thornthwaite and Mather
(1955) (Figure 2b).
Using GIS software (IDRISI for Windows, version
2.0, Clark University), each fire occurrence was
mapped and the perimeter and extent of each burned
area was calculated.
A grid of 4 ⫻4 km was overlaid on the park map and
the randomness of the distribution of fire starts in each
cell was statistically tested by a chi-square test (Kershaw
and Looney 1964).
Fires were classified as natural or human-induced.
When the lightning strike that caused a fire had not
been observed in the field, the fire would be considered
natural if thunderstorms occurred at the time of fire
event, the fire focus was distant from park limits, and
visitors had not been in the park the day of the fire
event. If one or more of these conditions were not
satisfied, the fire would be considered human-induced.
We considered each natural fire as resulting from one
lightning strike.
Results
Fire outbreaks during the study period are pre-
sented in Table 1. Forty-five fires were registered and
five of them were considered human-induced. Forty-
one fires were identified immediately after they started
and four small burned areas were detected by airplane.
Three of the anthropogenic fires were caused by the
park staff when burning firebreaks, and the other two
came from farms outside the park, as observed in the
field. Four human-induced fires occurred during the
dry season, when vegetation was undergoing a water
deficit (Figure 2b), and burned a total of 7,942 ha; the
other one occurred in January and burned 866 ha. Ten
Figure 1. Cerrado region (according to I.B.G.E. 1992) and
the location of Emas National Park, Brazil.
LIghtning Fires in a Brazilian Savanna Park 677

fires happened in the seasonally transitional months
(May and September), burning 33,386 ha; 31 fires oc-
curred in the wet months, 30 of which were caused by
lightning (29,326 ha burned) and one of which came
from outside the park (866 ha burned). Multiple fire
points caused by a single lightning strike were not
observed, as in this case the fire points would appear
near each other and all fires registered were isolated.
Small spot fires merging to a large fire were not ob-
served.
The majority of wet-season lightning fires (76%)
were patchy, burned small areas (less than 500 ha)
Figure 2. Climatic diagram (a), following
Walter and Lieth (Walter 1971), and the re-
gional water balance (b), according to Thorn-
thwaite and Mather (1955), for Emas National
Park region. Data from the nearest climatic
station, in Mosteiro Sa˜o Jose´, Mineiros munici-
pality, Goia´s state (Franc¸a and Setzer 1997)
and from this study, for the period of 1985 to
1997. In a: black ⫽excess water, vertical
strips ⫽regular water supply, dotted ⫽water
deficit. In b: vertical strips ⫽surplus soil water,
right dashed ⫽soil water withdrawal, left
dashed ⫽soil water replenishment, dotted ⫽
water deficit).
678 M. B. Ramos-Neto and V. R. Pivello

(Figure 4) and were extinguished primarily by rain
(Table 2); active fire suppression was applied in only
two of them, and even so the main causes for their
extinction were rain, a natural barrier such as river or
gallery forest, or a burned firebreak. In contrast, dry-
season (June–August) fires burned larger areas com-
pared to wet season lightning fires, spread more
quickly, and required vigorous suppression efforts to
bring them under control (Tables 1 and 2). February
was the month with the highest fire incidence (11 fire
outbreaks with 1,312 ha burned), followed by Septem-
ber (eight outbreaks with 24,020 ha burned) (Figure
5).
During the study period, 53.4% of the park area did
not burn; 38.1% burned once; 8.4% burned twice, and
only 0.1% of the park burned three times (Figure 6).
Examination of the spatial distribution of fires revealed
some places in the park where fire outbreaks were more
frequent, and this was confirmed statistically when an-
alyzed against cells in a grid (␹
2
⫽37.7; df ⫽2; P⬍
0.001). All lightning fires started on the flat plateau,
which occupies the highest elevation in the park and is
covered mostly by open vegetation (wet field or grassy
savanna) (Figures 3 and 6).
Discussion
Although scientists have long recognized lightning
as an important cause of wildland fires (Warming 1908,
Komarek 1972, Coutinho 1980, 1990, Tutin and others
Figure 3. Vegetation forms in Emas Na-
tional Park, Brazil.
LIghtning Fires in a Brazilian Savanna Park 679

1996, Middleton and others 1997), records of fire out-
breaks that included precise information on location,
area burned, and ignition source were not previously
available for the cerrados. In most cerrado parks and
reserves, human-caused fires are, indeed, much more
frequent than natural fires and originate at nearby
farms or urban areas (Pivello and Coutinho 1992).
The low incidence of anthropogenic fires in the
study area may be explained by several reasons. First,
preventive firebreaks, especially the ones located at the
park limits, had been maintained in reasonably good
condition by annual burning during the dry season,
thus avoiding the spread of fires coming from outside
the park. Second, mechanical agriculture now prevails
around the park, where fire is not frequently used.
Third, the fire-combat staff, although numbering only a
few persons and limited equipment, was present in the
park during the entire dry season and ensured a rapid
response when fires began. Finally, visitors in the park
were always guided by an authorized person and an
educational program was developed for farmers who
live near the park. However, these measures were not
able to suppress fire from the park because when hu-
man-induced fires are repressed natural lightning fires
predominate. That was evidenced by the highest fire
incidence during the wet months, probably related to
the number of lightning strikes in that period, since
heavy showers with thunderstorms and lightning are
frequent in the wet season.
Very few lightning strikes have been documented in
the cerrado region; the best available records come
from Pinto and others (1996), who registered 0.4 oc-
currences/km
2
in a place (Uberlaˆndia, MG, Brazil) that
lies at the same latitude as the Emas Park, about 400 km
east. Considering that in the present study each natural
fire was started by only one lightning strike and taking
the lightning records of Pinto and others (1996), we
Table 1. Fire outbreaks registered from June 1995 to May 1999 in Emas National Park, Brazil
Date
Natural fire Human-induced fire Total
area (ha)Number Area (ha) Number Area (ha)
Jun 95 — — 2 6,780 6,780
Aug 96 — — 1 792 792
Sep 96 4 4,628 — — 4,628
Oct 96 1 9,619 — — 9,619
Dec 96 2 6,767 — — 6,767
Feb 97 4 275 — — 275
Mar 97 2 23 — — 23
May 97 1 61 — — 61
Jun 97 — — 1 370 370
Sep 97 4 19,390 — — 19,390
Oct 97 1 1 — — 1
Nov 97 1 70 — — 60
Jan 98 2 323 — — 323
Feb 98 2 377 — — 377
Mar 98 1 378 — — 378
Nov 98 1 1,592 — — 1,592
Dec 98 3 2,716 — — 2,716
Jan 99 4 4,164 1 866 5,030
Feb 99 5 659 — — 659
Mar 99 1 2,362 — — 2,362
May 99 1 9,307 — — 9,307
Total 40 62,702 5 8,808 71,510
Figure 4. Fire outbreaks according to size classes (hectares)
and fire season, in Emas National Park, Brazil.
680 M. B. Ramos-Neto and V. R. Pivello

estimate that 1%–2% of the lightning strikes cause
wildfires in Emas National Park, not a negligible figure.
Although the highest fire incidence happened in
February (wet season), the total area burned (1,312 ha)
was relatively small, in contrast to September (transi-
tional month), when the largest cumulative area
burned (24,020 ha). Large fires in September were
probably related to weather and fuel conditions. By this
time of the year, the vegetation is cured and undergo-
ing severe water deficit (Figure 2b), the fuel is dry and
plentiful, especially if frosts occur (Pivello 1992, Pivello
and Norton 1996) and where the grass Tristachya leiosta-
chya is dominant (Ramos-Neto and Machado 1996).
The onset of the wet season in September brings heavy
Table 2. Main causes of fire extinction according to fire season in Emas National Park, Brazil
Causes of fire extinction Dry season Transition Wet season Area (ha)
Natural causes (rain, natural barriers or low
temperature) 0 4 14 5.459
Natural causes ⫹preventive firebreak 0 2 15 12.367
Natural causes ⫹suppression 0 2 0 8.383
Natural causes ⫹preventive firebreak ⫹
suppression 0 1 1 25.686
Preventive firebreak 0 1 0 10.807
Suppression 0 0 0 0
Preventive firebreak ⫹suppression 4 0 1 8.808
Total 4 10 31 71.510
Figure 5. Total fire outbreaks (a) and the total area (hect-
ares) burned per month (b), in Emas National Park, Brazil,
from June 1995 to May 1999.
Figure 6. Fire frequency in Emas National Park, Brazil, from
June 1995 to April 1999.
LIghtning Fires in a Brazilian Savanna Park 681

showers with thunderstorms and lightning, causing fire
outbreaks and spread (Schule 1990, Pivello 1992, Piv-
ello and Norton 1996).
Another factor that seems to influence fire occur-
rence is the elevation. Higher lightning fire occurrence
was registered in elevated plateaus. Frequent lightning
fires at high elevations have also been reported in Costa
Rica dry forests (Middleton and others 1997). The
altitude probably influences local meteorological con-
ditions and cloud formation, resulting in greater light-
ning incidence. This phenomenon, however, deserves
more investigation.
The present study shows the importance of natural
fires, at least in the most important protected cerrado,
Emas National Park. Cool fires in the wet season and
more intense fires in the transitional months may dom-
inate the natural pattern in the region studied, instead
of high-intensity winter fires, as has been believed up to
the present time. Wet-season fires usually burn small
areas due to the high moisture content in the vegeta-
tion (Pivello 1992) and are rapidly extinguished by the
heavy summer rains. Wet-season fires contribute to the
creation of a mosaic of low-fuel patches, which may
function as natural firebreaks and reduce the spread of
subsequent fires. This patchy landscape also provides
shelter for animals during a fire and maintains seed
banks of less fire-tolerant plant species; patchy burns
may increase the area of ecotones, permitting higher
diversity. In contrast, winter fires are hot, spread much
quicker, and may burn huge areas if fuel is abundant, as
often occurs under full fire-suppression policies.
As virtually no records of wet-season fires in cerrados
exist, studies and experimentation considering fire ef-
fects in flora and fauna until now have only considered
dry-season fires. In the case of Emas National Park, that
condition would be unrealistic, as most fires occur be-
tween September and May. In that case, the response of
plants and animals to fire may be different than those
described in the literature. For instance, studies on
plant biomass production after fire indicate very differ-
ent results according to whether the burn occurs in
June, September, or November (Ramos-Neto, personal
communication).
Conclusion: Are Present Fire Management
Strategies Adequate?
The lack of more precise information on cerrado
fires and the fact that policy-makers are not well in-
formed on recent advances in fire ecology have led to
inadequate management policies concerning fire in
cerrado preserves (Pivello 1992). Full-suppression pol-
icies come from conservative attitudes and are based on
past ideas about the harmful effects of wildland fires.
This is reflected in the fact that legislation permitting
the use of management burning, in special cases, was
not passed until 1988/89 (IBDF Law No. 231-P/88;
CONAMA Resolution No. 011 from 14 December 1988;
Federal Decree No. 97635 from 10 April 1989).
The policy of total fire suppression has proved to be
inadequate in cerrado preserves, as extensive and hot
fires periodically occur when fuels accumulate, de-
manding huge efforts and cost to be controlled. A
proper management policy in protected cerrados
should be based on continuous monitoring and assess-
ment of flora and fauna responses to specific fire re-
gimes. It should include the possibility of using natural
or periodic hazard-reduction fires in view of all the
benefits fire can bring to the ecosystem.
In the case of Emas National Park, we suggest that
natural lightning fires should be allowed to burn and
should be monitored; fire suppression should occur
only if the fire becomes too large or intense. Fuels
should also be monitored and a patch-burning strategy
using prescribed fires could be adopted for hazard
reduction. The effectiveness of this strategy has been
demonstrated in savanna parks elsewhere in the world
(Edwards 1984, Bradstock and Bedward 1997, Gill
1997).
Preventive firebreaks must be maintained, especially
at the park limits, because they are reasonably effective
in containing the spread of winter fires. However, the
number of firebreaks and their location and width
should be reviewed, especially if a patch-burning strat-
egy is adopted. At present, firebreaks are kept clean of
fuel by burning strips 25–60 m wide, by the middle of
the dry season. We recommend they be burned early in
May, both to follow a more natural burning pattern
(since lightning fires still occur in May) and because
burning is safer when vegetation is not so dry. Guide-
lines for prescribed fires in cerrados are discussed in
more detail by Pivello (1992) and Pivello and Norton
(1996).
In conclusion, a fire management policy that inte-
grates natural and prescribed fires with conservation
goals should be adopted in cerrado preserves. The
present policy concerning wildland fire in Emas Na-
tional Park may not protect its biodiversity on the long
term because of the damage to native flora and fauna
resulting from uncontrollable winter fires. A flexible
strategy of allowing and monitoring wet-season fires
and patch-burning when necessary would be a more
appropriate approach to maintaining the park natural
species and habitat diversity. This strategy has to be
based on additional studies of cerrado dynamics and
fire ecology and on continuous monitoring. Further-
682 M. B. Ramos-Neto and V. R. Pivello

more, fire management actions must account for local
conditions, since fire behavior is dependent on climatic
events that may differ from one region to another.
These differences will affect the basic approach to fire
management, including how firebreaks are designed,
the scheduling of prescribed fires, the circumstances
under which fires are allowed to burn, and postfire
dynamics in the communities.
Acknowledgments
The authors wish to thank the Emas National Park
staff for their assistance in the field, especially Ary
Soares dos Santos and Jose´ Carlos Bernardo, and WWF-
World Wide Fund for Nature, Brazil, for financial sup-
port.
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