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Brazilian Journal of Botany

On-line version ISSN 1806-9959

Rev. bras. Bot. vol.30 no.3 São Paulo July/Sept. 2007

http://dx.doi.org/10.1590/S0100-84042007000300003 

ARTICLES

 

Structure and dynamics of a woody plant community of a tropical semi-deciduous seasonal forest in the "Estação Ecológica do Panga", municipality of Uberlândia, Minas Gerais, Brazil

 

Estrutura e dinâmica da comunidade arbórea de uma floresta semi-decídua na Estação Ecológica do Panga, Uberlândia, Minas Gerais, Brasil

 

 

Luciana Vieira de PaivaI; Glein Monteiro de AraújoII, *; Fernando PedronIII

IUniversidade de Brasília, Departamento de Ecologia, Pós-graduação em Ecologia, 70910-900 Brasília, DF, Brasil
IIUniversidade Federal de Uberlândia, Instituto de Biologia, Campus Umuarama, 38400-902 Uberlândia, MG, Brasil
IIIUniversidade Federal de Mato Grosso, Departamento de Ciências Biológicas e da Saúde, 78698 000 Pontal do Araguaia, MT, Brasil

 

 


ABSTRACT

Studies of plant community dynamics are essential in understanding the demographic patterns of species since changes in demographic rates can affect the floristic composition and future structure. The purpose of the present study was to analyze the changes in the community structure and floristic composition of woody plants in a tropical semi-deciduous forest in Uberlândia in central Brazil, during a 10-years period. The data were collected in 1989 and in 2000 in 50 quadrats (10 m x 10 m) where all trees with a minimum circumference at breast height of 10 cm were sampled. In 1989, 93 species and 1103 individuals were registered. Over a period of 10 years, seven new species were added to the community, although eight disappeared. The main change that occurred during this period in the floristic composition was the replacement of savannah species occurring in forest gaps by those from the forest understory.

Key words: growth, mortality, recruitment, tropical forest


RESUMO

Estudos de dinâmica de comunidades vegetais são essenciais para o entendimento dos padrões demográficos das espécies, uma vez que as mudanças nas taxas demográficas da comunidade podem afetar a composição florística e a estrutura futura das florestas. Portanto, o presente estudo teve por objetivo analisar as mudanças na composição florística e estrutura fitofisionômica da comunidade arbórea de uma floresta tropical semi-decídua em Uberlândia no Brasil central, durante um período de 10 anos. O trabalho foi realizado em 50 parcelas de 10 m x 10 m, onde amostraram-se todas as árvores com circunferência a altura do peito com mínimo de 10 cm em 1989 e novamente em 2000. Em 1989 registrou-se um total de 93 espécies e 1103 indivíduos, enquanto que em 2000, 92 espécies e 1107 indivíduos. Em 10 anos houve a perda de oito espécies e recrutamento de sete. A principal mudança que ocorreu na composição florística nesse período foi a substituição de espécies de savana, que ocorriam nas clareiras, por aquelas de sub-bosque da comunidade florestal.

Palavras-chave: crescimento, floresta tropical, mortalidade, recrutamento


 

 

Introduction

Tropical forests have been seriously altered during the last centuries, through selective deforestation, agricultural activities, construction of dams, progress of urban areas and constructions of highways (Oliveira-Filho et al. 1997, Whitmore 1997). The anthropogenic disturbance processes have been happening on an unprecedented time scale in the ecological and geological history of these forests, causing profound changes on these ecosystems (Primack 1993) modifying their structure and dynamics (Caswell & Cohen 1991).

The modifications caused by anthropogenic disturbance have motivated the establishment of conservation programs for these ecosystems (Laurance & Bierregaard 1997), as well as stimulated studies on community structure and dynamics in the altered environments.

The dynamics of plant communities is influenced by growth, mortality and recruitment of individuals (Lieberman et al. 1985), which could be correlated with several environmental factors that affect the distribution and structure of plant populations (Aquino et al. 1999). Such studies are carried out accompanying the changes that occur in the plant community, using permanent plots, for long periods (Swaine & Lieberman 1987).

Most of the studies on community dynamics of Neotropical forests are reported from preserved or slightly disturbed areas; several studies were carried out in the Amazonian region (Rankin-de-Merona et al. 1990), Federal District (Felfili 1995a) and southern Minas Gerais (Oliveira-Filho et al. 1997). In the Triângulo Mineiro, studies were carried out on the dynamics of plant populations (Aquino et al. 1999, Schiavini et al. 2001). However, there are no published reports on dynamics of plant communities in this region.

Studies on forest community dynamics seek to understand the changes in the floristic composition, tree density and basal area, and other characteristics (Korning & Balslev 1994, Bormann & Berlyn 1981), fundamental for the recovery of tropical forests that undergo disturbances and for the implantation of management programs (Hartshorn 1990). Studies on community dynamics indicated that the forests are in a state of dynamic equilibrium. In spite of the fluctuations in the mortality and recruitment rates of some populations, the communities tend towards stability (Felfili 1995a). Investigations of forest dynamics can provide a basis to predict long term general changes in plant communities.

The principal objective of the present study was to analyze the changes that occurred over a 10-year period (1989-2000) in the species composition and physiognomic structure of a tropical semi-deciduous seasonal forest in Uberlândia, central Brazil, mainly in the number of individuals and basal area, to determine current community conservation status.

 

Material and methods

Study area, climate and soil of the region – The study was carried out in a semi-deciduous seasonal forest, according to Veloso et al. (1991) classification, at the "Estação Ecológica do Panga" (EEP) owned by the "Universidade Federal de Uberlândia". The reserve covers an area of 410 ha located in the southern section of the Uberlândia municipal district, 35 km from city downtown (19°10' S e 48°23' W). All main cerrado physignomies are found in the reserve (Schiavini & Araújo 1989).

The semi-deciduous forest studied has approximately 15 ha and is adjacent to a cerradão (a forest formation) and a gallery forest. It underwent a selective cutting in the early 1960s. In 1990, during the recovery phase, it presented Lithraea molleoides with highest importance value (Araújo & Haridasan 1997). This species, considered to be a heliophyte by Longhi (1987), possibly occupied the area when the forest had smaller canopy covering. At present the forest has a canopy covering of more than 80% and trees up to 15 m high.

The climate of the area is of the tropical savanna type, with dry winter and rainy summer, with average temperature of the coldest month greater than 18 °C. The annual rainfall varies from 1,400 to 1,700 mm; and the average maximum temperatures from 27 °C to 30 °C (Rosa et al. 1991).

The predominant soil of the area is Acric Red Latosol ("Latossolo Vermelho ácrico") – according to the Brazilian system of soil classification, with low organic matter content and exchangeable bases. The soils of the region originated from the Adamantina formation, Bauru group that prevail in the Uberlândia municipal district (Lima & Bernardino 1992).

Successive inventories (1989-2000) – The first inventory (T1) was carried out from August to October 1989. In one ha of the forest, 50 plots of 10 m x 10 m were randomly positioned, all trees with a minimum circumference at breast height (CBH) of 10 cm were tagged with aluminum labels. The circumference of the stem was measured at 1.30 m or, in forked individuals, below the first live branch. The results of this first inventory are published in Araújo & Haridasan (1997).

The second sampling (T2) was carried out from January to March 2000, following the same procedure of the first survey. The perceptibly old individuals and those that did not present labels (embodied or expelled) were marked again. The individuals that were recruited (I), the ones that were not marked in T1, also received labels and were measured and identified. The trees that were not found, even after a thorough search, were considered dead.

Variables of arboreal community dynamics – the variables of the community dynamics were obtained for the period between 1989 and 2000, corresponding to 10 years and five months. The number of dead individuals (M); the number of recruits (I); the total basal area lost (BAL) (determined by the basal area of the dead individuals); and the basal area gained (BAa), determined by the sum of the basal area of the recruits (BAr) plus the growth of the surviving individuals (BAs) were calculated.

These parameters were used to calculate the mortality and half-life, recruitment and time of duplication, the increase in population and replacement and stability.

Mortality – the annual mortality rate (Me) was calculated using an exponential model, following the recommendations of Swaine & Lieberman (1987), according to the equation: Me = - {Ln [(N1-M) N-1]} Dt-1, in which: N1 = number of individuals in the first sampling; M = number of dead individuals and Dt = time interval (in years) between the samplings.

Half-life taking as starting point the value of the mortality rate, the "half-life T(½)" was calculated; in other words, the time necessary for the community to reduce the number of individuals by half, considering that the present mortality rate is maintained: T(½) = Ln (0.5) Me-1.

Recruitment – the annual recruitment rate of the community (Ic), was estimated according to Sheil & May (1996): Ic = {(N2 Dt-1)-Ln [1-(I N2-1)]} N2-1 , in which N2 = number of individuals in second sampling; I = number of recruited individuals (for basal area this value was substituted by ABg).

Duplication time duplication time (T2) was calculated from the recruiting rate, the time required for the number of individuals in the community to double if the same rate of recruiting is maintained. This calculation followed the model adapted by Korning & Balslev (1994), where T2 = Ln (2) Ln (1 + Ic)-1.

Replacement and stability – to calculate the replacement (R) and stability values, the model suggested by Korning & Balslev (1994) was used, in which: R = (T(½) + T2) 2-1 and E = |T(½) - T2|

Increment of community individuals – the increment (r) indicates the increase in the number of individuals in the community over the year, and it was determined using the following equation:

To test the relationship between the mortality rates and the individuals size, estimates of the dynamic parameters were made for different diameter classes, with intervals of 5 cm (from 3 to 58 cm).

The t-test (Zar 1999) was used to test the difference between Shannon diversity indices obtained in 1998 and 2000.

 

Results

Ninety-three species and 1,103 individuals were sampled in T1 and 92 species and 1,107 individuals in T2 (table 1). During the interval between T1 and T2 (10 years and five months), there was a change of 16.13% in the specific composition due to the loss of eight species: Agonandra brasiliensis, Apeiba tibourbou, Byrsonima basiloba, Cardiopetalum calophylllum, Caryocar brasiliense, Eugenia moraviana, Guapira cacerensis and Senna sylvestris (table 2) and the recruitment of seven: Phyllanthus acuminatus, Piper arboreum, Siparuna guianensis, Tabebuia impetiginosa, Trichilia catigua, Trichilia pallida and Unonopsis lindmanii (table 2). The diversity indices of Shannon did not vary among T1 (3.72 nats ind-1) and T2 (3.73 nats ind-1).

 

 

In the period between the two inventories there was a 34.2% death toll among the 1,103 individuals marked initially, with an annual mortality rate of 4.01% (table 1). The species that contributed most to the mortality rate were Lithraea molleoides, followed by Alibertia sessilis, Campomanesia velutina, Chrysophyllum marginatum and Myrcia rostrata (table 2). The mortality rate was strongly influenced by the diameter classes. Trees with smaller diameters, mainly from 3 to 8 cm, presented larger mortality rate (figure 1a).

The loss of 59.7% in basal area (table 1) was represented by individuals belonging to the first three diameter classes (figure 1b). The species that contributed most to this reduction were Lithraea molleoides, Campomanesia velutina and Ocotea pulchella (table 2).

The community presented a recruitment rate of 34.4% of the total number of individuals in the second inventory. The annual recruitment rate obtained for this study was of 4.04% (table 1). The majority of the recruited individuals (95.3%) belonged to the first diameter class (figure 1c), with an annual recruitment rate of 7.21%. The species that had the greatest number of recruited individuals in the community were Alibertia sessilis, Bauhinia ungulata, Faramea cyanea, and Erytrhoxylum subracemosum (table 2), which occupy preferentially the lower canopy in the forest.

In the investigated period 0.71 m2 of the total basal area increase was due to the contribution of recruitment and 2.94 m2 due to the growth of surviving individuals (table 1). The growth in basal area in the intermediate classes (figure 1d) was due mainly to the growth of the surviving individuals of Anadenanthera colubrina and Terminalia brasiliensis which occupy the upper strata of the forest.

In terms of number of individuals, the annual recruitment was almost equal to the annual mortality observed in the community. As a consequence, the values of half-life, duplication time and basal area were very similar. The replacement time was greater in terms of basal area and the stability values were low for number of individuals and basal area, respectively (table 1).

In the two surveys, a larger number of individuals was observed in the smaller diameter classes, resulting in a frequency distribution in the form of inverted J (figure 1e).

The distribution of basal area in the different diameter classes was more similar in the second survey (figure 1f). The species that contributed most to the increment in recruited individuals were Alibertia sessilis and Matayba elaeagnoides and, among the survivors, Anadenanthera colubrina, Terminalia brasiliensis, Hymenaea courbaril and Terminalia phaeocarpa (table 2).

 

Discussion

The changes observed in relation to the number of species and individuals, basal area, and diversity in the study area were low when compared with values reported for others tropical forests (Lang & Knight 1983, Korning & Balslev 1994, Oliveira-Filho et al. 1997). The greatest change observed was in relation to floristic composition, but the species that disappeared or were recruited were represented by just one or a few individuals. Species that were not abundant in the initial survey had a greater probability of disappearing locally, between a survey and the next one (Kellman et al. 1998, Nascimento et al. 1999), being able to reappear in a subsequent survey through migration or recruitment of individuals from the seed bank and seedlings or from the growth of young individuals that did not reach the minimum criterion for inclusion in the first survey (Pedroni 2001). The greater the time interval between the samplings, the larger the possibility of changes in floristic composition. The species that disappeared (Agonandra brasiliense, Byrsonima basiloba, Cardiopetalum calophyllum, Caryocar brasiliense and Senna sylvestris) were, in their majority, found in the forest formation of cerradão and the savanna formation of cerrado sensu stricto (Costa & Araújo 2001). Possibly, these species occupied more open areas in the forest due to a selective cutting of trees that happened approximately 30 years ago (Araújo & Haridasan 1997). The species sampled in T2, in general, already occurred in the understorey of the EEP forest (Araújo & Haridasan 1997). As long as most of the species that disappeared and that were recruited had only one individual, these changes were not reflected in the Shannon diversity indices in the two inventories.

During the period of 10 years and five months, in spite of the small changes in relation to the number of individuals, the forest community was relatively dynamic as far as species richness and diversity was concerned. According to Felfili (1995a), even seemingly stable communities can be dynamic due to the fluctuation between mortality, growth and recruitment that occur over time.

The mortality rate of 4.01%, found in this study, is among the highest values registered for tropical forests (Hubbel & Foster 1990, with 3.94% in Barro Colorado and Nascimento et al. 1999, with 4.5% in Piracicaba, SP). A high mortality rate was related by Phillips (1996) to global changes, such as an increase of CO2, and by Laurance et al. (1998) and Nascimento et al. (1999) to the effects of habitat fragmentation and microclimatic alterations. In EEP, the high rate was strongly influenced by the mortality of the Lithraea molleoides population. This species is considered to be a heliophyte (Longhi 1987) and it probably occupied the area during a period in which the forest was more open (Araújo & Haridasan, 1997). Presently, its population has been reduced to a few young and adult individuals, suggesting that this species is less competitive in more shaded environments.

The results of the present study suggest that trees with smaller diameters (3 to 8 cm) are more susceptible to mortality. Uhl et al. (1988) and Clark & Clark (1992) found higher mortality among individuals of less than 10 cm diameter. According to Felfili (1995b), the greater mortality among individuals belonging to the smallest diameter classes should result from the lower competition capacity in relation to the larger trees, which occupy the upper strata.

The recruitment rate found at EEP can also be considered high, placing itself among the highest values mentioned in literature, 3.08% year-1 for an inundated forest in Añangu in Ecuador (Korning & Balslev 1994), 3.11% year-1 for a seasonal forest in Lavras, Minas Gerais (Oliveira-Filho et al. 1997) and 4.48% year-¹ for a dry forest in Barro Colorado (Hubbel & Foster 1990). The species that contributed most to the recruitment rate were Alibertia sessilis, Bauhinia ungulata and Faramea cyanea in the lower diameter classes, which occupy preferentially, the lower canopy in the forest (Araújo & Haridasan 1997). These species seem to have been favored by the closing of the canopy due to the growth of the surviving individuals of Anadenanthera colubrina, and Terminalia brasiliensis in the intermediate diameter classes. Individuals with larger diameter concentrate gains on live biomass, through lateral growth of the stem and canopy, and may occupy and close spaces in the upper strata (Werneck et al. 2000).

At EEP, the half-life value calculated on the basis of the number of individuals was low in relation to the values found for some forests, which varies from 30 to 106 years (Lieberman & Lieberman 1987, Crow 1980, Uhl et al. 1988, Oliveira-Filho et al. 1997), whereas the duplication time of 17.52 years was among the lowest found in literature (Oliveira-Filho et al. 1997, 18.45 years and Hubbel & Foster 1990, 15.82 years). According to the terminology of Hallé et al. (1978), the study area presents a stable sylvigenic state, since the mortality and recruitment rates, and, consequently, those of half-life and duplication period, are approximately balanced. A community can be considered as stable in relation to its structure when the stability value approaches zero and can be highly dynamic in relation to replacement time (Korning & Balslev 1994).

The stability and replacement values, found in this study, indicate that the sampled arboreal community, in relation to its structure, is stable and seems to be more dynamic than other tropical forests, which were studied in relation to replacement time. The most evident change observed was in relation to its specific composition due to the disappearance of species, which are common to savannah areas, and the recruitment of forest species. These observations and those that show higher mortality of species such as Lithraea molleoides), seem to indicate that the forest community at EEP is recovering from the alterations it suffered and returning to its more typical floristic composition, close to preserved forests in the region of Uberlândia.

Acknowledgement – The first author is grateful to CNPq (Conselho Nacional de Pesquisa) for a scholarship (PIBIC) during the period of this study, to Fernanda Gomide for her help during field collections and Dr. M. Haridasan and Dr. J. Hay for suggestions on the manuscript.

 

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Received: 5/5/2005
Accepted: 21/6/2007

 

 

* Corresponding author: glein@ufu.br