African Journal of
Agricultural Research

  • Abbreviation: Afr. J. Agric. Res.
  • Language: English
  • ISSN: 1991-637X
  • DOI: 10.5897/AJAR
  • Start Year: 2006
  • Published Articles: 6712

Full Length Research Paper

Phytosociological survey of arboreous species in conserved and desertified areas in the semi-arid region of Paraíba, Brazil

Jhony Vendruscolo*
  • Jhony Vendruscolo*
  • Ciência do Solo, Universidade Federal da Paraíba, Areia, PB. Brazil.
  • Google Scholar
Aldrin Martin Perez Marin
  • Aldrin Martin Perez Marin
  • Ciência do Solo, Universidade Federal da Paraíba, Areia, PB. Brazil.
  • Google Scholar
Bruno de Oliveira Dias
  • Bruno de Oliveira Dias
  • Ciência do Solo, Universidade Federal da Paraíba, Areia, PB. Brazil.
  • Google Scholar
Evaldo dos Santos Felix
  • Evaldo dos Santos Felix
  • Ciência do Solo, Universidade Federal da Paraíba, Areia, PB. Brazil.
  • Google Scholar
Allana dos Anjos Coutinho
  • Allana dos Anjos Coutinho
  • Instituto Nacional do Semiárido, Brazil.
  • Google Scholar
Karoline Ruiz Ferreira
  • Karoline Ruiz Ferreira
  • Engenharia Florestal, Universidade Federal de Rondônia, Brazil.
  • Google Scholar

  •  Received: 04 September 2016
  •  Accepted: 27 January 2017
  •  Published: 09 March 2017


The objective of this study is to perform a phytosociological survey of the arboreous composition in conserved and desertified areas of the semiarid region of Paraiba State. Twenty-two conserved areas (CA) with native vegetation (Caatinga) where there has been no clear cut logging since 1984, and Twenty-two desertified areas (DA) having a difficult re-establishment of vegetal coverage over the past 10 years were selected. Plots with 100 m2 were established and the species were identified. The perimeter at 0.30 m ground level (PGL) and at breast height, 1.30 m (PBH) was measured. Subsequently, the absolute density (AD), relative density (RD), absolute frequency (AF), relative frequency (RF), absolute dominance (ADo), relative dominance (RDo), importance value index (IVI) and coverage value index (CVI) were calculated. There were 63 species of trees in CA and 9 in DA. The most frequent species were Caesalpinia pyramidalis and Croton sonderianus in CA, and Mimosa tenuiflora and Croton sonderianus in DA. CA showed an AD (4,845 I ha-1) higher than DA (895 I ha-1). The ADo order was C. pyramidalis > Anadenanthera colubrina > Myracrodruon urundeuva in CA, and M. tenuiflora > C. pyramidalis > Aspidosperma pyrifolium in DA. C. sonderianus (CA) and M. tenuiflora (DA) reached the highest IVI and CVI.

Key words: Caatinga, vegetation, biodiversity, environmental quality.


The desertification process triggers major changes in the floristic composition of the Caatinga (Sousa et al., 2015). This happens mainly due to anthropic  actions  known  as deforestation for firewood purposes, exploration of clay deposits, and intensive use of the land through in appropriate agricultural mechanisms (cutting and burning), salinization, extensive grazing and overgrazing (Nimer, 1988; Galindo et al., 2008; Alves et al., 2009; Costa et al., 2009; Sá et al., 2010; Aquino and Oliveira, 2012). The adoption of strategies is mandatory to minimize this problem (Damasceno and Souto, 2014; Barros, 2011).
The impact of the anthropic action on the physiological dynamics of vegetation causes its features to change to an even lower and thinner Caatinga, with a severe selection of species (Alves, 2009). In this context, it is clear that the phytosociologycal survey provides information about the geographical distribution of the species and about the vegetation structure, depicting the impact of the anthropic action on the vegetation-soil-climate complex. This data can be used for action planning to preserve, conserve and recover the forest ecosystems (Chaves et al., 2013). This consequently leads to the development of more sustainable activities in the semi-arid areas.
Despite the importance of phytosociological studies, the studies carried out in Brazil are still insufficient, and a thorough analysis is necessary so actions on the conservation of natural resources can be taken (Freitas and Magalhães, 2012).
Considering the importance of the vegetal structure for planning the conservation and recovery of the natural resources and for the mitigation of the consequences of the desertification process, this study aimed to perform a phytosociological survey of tree layers in areas of conservation and desertification in the semi-arid region of Paraíba State.


This study was carried out in 22 conserved areas (CA) and 22 desertified areas (DA) (Figure 1) of the semi-arid region of Paraíba State, Brazil, from October 2015 to May 2016. The region has a semi-arid climate, with a dry period of 6 to 11 months in 85.3% of the area (Nimer, 1979) where the annual precipitation is lower than 800 mm (Sousa et al., 2012).
The conserved areas (CA) were selected considering the non-occurrence of clear cutting since 1984, based on temporal images of the past 30 years, using the Landsat Annual Timelapse 1984-2012. Subsequently, the selected areas were compared with the images of the Landsat satellite 8, and confirmed in the field.
The desertified areas (DA) were selected considering the difficulty of the vegetation cover to re-establish, using temporal images (past 10 years) Landsat 7 (bands 3, 4 and 5) and 8 (bands 4, 5 and 6), with the help of the Earthengine. The period of the images is correspondent with the period of the highest rainfall and low incidence of clouds, which excludes water as a limiting factor for plant growth. After selecting the areas, based on remote sensing techniques, the next step was to locate them, by using Google Earth and Garmin 60CSX GPS navigation, and to evaluate the arboreous coverage of the field.
The evaluation of the arboreous vegetation was carried out in 100 m2 (10 x 10 m) plots. In each plot, the identification of the arboreous species was based on regional knowledge, with the help of a local guide, and on literature (Lorenzi, 1992; Lorenzi, 1998, 2009; Siqueira Filho et al., 2009; NUPEEA, 2010; Castro and Cavalcante, 2011; INSA, 2011; Maia-Silva et al., 2012).  Every  tree whose base of the trunk was in the plot was included, even when the stem and canopy were over the borders.
After measuring the arboreal component, the following phytosociological parameters were calculated:
I - Absolute Density per area proportional (AD): represents the average number of trees of a given species, per unit of area (I ha-1).
ADi = Ni /A                                                                    (1)
Ni = number of units of the species i;
A = total area sampled (ha).
II - Relative Density (RD): Percentage of the number of units of a given species in relation to the total number of sampled units.
RDi = (Ni x 100)/n                                                                          (2)
Ni = number of units of the species i;
N = total number of units.
III - Absolute Frequency (AF): is the percentage of sample units with occurrence of the species, in relation to the total number of sample units.
AFi = (Pi x 100)/P                                                                         (3)
Pi = number of plots in which the species occurred;
P = total number of plots.
III - Absolute Frequency (AF): is the percentage of plots with occurrence of the species, in relation to the total number of plots.
AFi = (Pi x 100)/P                                                                          (4)
Pi = number of plots in which the species occurred;
P = total number of plots.
V - Relative Frequency (RF): obtained from the relationship between the absolute frequency of each species and the sum of the absolute frequencies of all sampled species.
RFi = (AFi x 100) / Æ©AFi                                                  (5)
VI - Absolute Dominance (ADo): occupancy rate of the environment by units of a species (m2 ha-1), calculated from the sum of basal area.
ADoi= BAi / A                                                                (6)
BAi = individual basal area of a species (m2), based on the diameter of the stem from 0.3 m or 1.3 m of the ground, when the units were lower or taller than 1.3 m, respectively;
A = total sampled area (ha).
VII - Relative Dominance (RDo): represents the relationship between the basal area of a species and the total basal area of all sampled species.
RDo = (BAi/TBA) x 100                                                      (7)
BAi = is the basal area of each unit of the species;
TBA = is the sum of the basal areas of all species.
VIII - Importance Value Index (IVI): represents how well the species is established in the community. It is the result of the relative values already calculated for density, frequency and dominance, reaching, therefore, the maximum value of 300.
IVIi = RDi + RDoi + RFi                                                   (8)
IX -Value of Coverage Index (VCI): is the sum of relative values and dominance of each species, up to a maximum value of 200.
VCIi = RDi + RDoi + RFi                                                                (9)
The conserved areas had 5 to 17 species per plot, with an average value of 10 (±2.9), totaling 63 species (Table
1), while the desertified areas presented 1 to 4 species per plot, with an average value of 2 (±1.0), totaling 9 species (Table 2).
The most frequent species found in the conserved areas were Caesalpinia pyramidalis (77.3%), Croton sonderianus (77.3%), Piptadenia stipulacea (68.2%) and Aspidosperma  pyrifolium  (63.6%),  while  the  remainder presented AF below 50% (Table 3). The most frequent species of trees found in the desertified areas were Mimosa tenuiflora (68.2%), C. sonderianus (31.8%), C. pyramidalis (31.8%), Jatropha mollissima (31.8%) and A. pyrifolium (18.8%) (Table 4).
The conserved areas presented a higher AD than the desertified areas, with 4,845 I ha-1 and 895 I ha-1 (Tables 3 and 4), respectively. C. sonderianus had the highest AD (1,345 I ha-1) in the CA, followed by C. pyramidalis (573 I ha-1). The highest AD the in DA were from M. tenuiflora (414 I ha-1) and C. sonderianus (173 I ha-1).
Regarding ADo, it was noted that C. pyramidalis (72.56 m2 ha-1), Anadenanthera colubrina (69.06 m2 ha-1), Myracrodruon urundeuva (49.06 m2 ha-1), Schinopsis brasiliensis (43.06 m2 ha-1), and C. sonderianus (21.56 m2 ha-1) showed the highest values in the conserved areas (Table 3). M. tenuiflora (9.87 m2 ha-1), C. pyramidalis (4.05 m2 ha-1), A. pyrifolium (2.52 m2 ha-1), Prosopis juliflora (2.43 m2 ha-1) and J. mollissima (0.92 m2 ha-1) (Table 4) had the highest ADo values in the desertified areas.
The species C. sonderianus (13.7%), C. pyramidalis (12.6%) and A. colubrina (8.0%) had the highest IVI in the CA, while M. tenuiflora (41.9%), C. pyramidalis (15.9%) and C. sonderianus (12.6%) showed the highest IVI in the AD (Tables 3 and 4, respectively).
The coverage value index (CVI) showed a pattern similar to IVI, with higher values for C. sonderianus (16.6%), C. pyramidalis (14.9%) and A. colubrina (9.7%) in AC, and M. tenuiflora (46.8%), C. pyramidalis (16.3%) and C. sonderianus (11.4%) in AD (Tables 3 and 4, respectively).


The diversity of species is the main feature that determines the ability of a system to survive during and after a period of adversity, that is, the resilience of the system (Salgado-Laboriau, 1994). In this context, we can say that the present anthropic activities promote the reduction of the arboreous diversity in the desertified areas, lowering, consequently, the environmental quality of the Caatinga biome in the semi-arid region of Paraíba State. This corroborates the work of Costa et al. (2009).
The anthropic action, in addition to reducing the number of species, also affects the distribution of those remaining in the desertified areas, affecting the emergence of those adapted to stricter requirements, such as M. tenuiflora (Lima, 1996), J. molissima, A. pyrifolium and C. pyramidalis (Silva et al., 2004). It is also noted that some characteristics of the former three species reduce the impacts of pressure of use by population and by domestic animals (Souza et al., 2015), showing low density for building and firewood usage, or toxicity to animal consumption (Souza, 2008; Lima and Soto-Blanco, 2010; Dantas et al., 2012).The highest AD in conserved areas suggests a greater protection of the soil against erosion processes, especially by water, decreasing soil and nutrients losses (Martin Filho et al., 2009; Ramos et al., 2014), and consequently increasing the vegetation resilience. The highest density of species in conserved areas also increases the production of litter, levels of organic matter, infiltration capability and storage of water in the soil, thus reducing the susceptibility to water scarcity (Mendonça et al., 2009). The highest values of ADo of the species in CA relate to a number of factors, including the potential of some species, such as M. urundeuva and A. colubrina, which can reach 14 and 15 m in height in the Caatinga (Lorenzi, 1992). Other factors are better conditions for plant growth and development, as previously seen, and time to accumulate biomass, as these areas did not suffer clear cutting for at least 32 years. Although C. pyramidalis reaches only 10 m high, that is, 66% of M. urundeuvas and A. colubrina’s height, it has characteristics that counterbalance that of the latter in biomass production, such as tolerance to periods of water stress (xerophile) and easy regeneration after cutting (Lorenzi, 2002; Lorenzi, 2009). In the DA, the best-adapted species to the water stress conditions reached the highest values of ADo. The species adapted to these conditions have some advantages in relation to those not adapted, which tend to face greater difficulties to getting established and disseminated. The IVI expresses numerically the importance of a given species amongst the trees of a community (Poggiani et al., 1996). Therefore, the maximum value of 13.7% (C. sonderianus) indicates a better distribution of the IVI amongst the species in the conserved areas, that is, a better balance between the species and, consequently, a higher quality of vegetation. Regarding DA, M. tenuifloras IVI of 41.9% points this species out as the most ecologically important for this environment, corroborating data from Freitas et al. (2007). According to this author, M. tenuiflora’s ability to dominate the environment is due to its high capacity to regrow, revealing a good adaptation to the degraded environments of the Caatinga.
The parameter CVI conveys the ecological importance of the species in horizontal distribution terms so that the maximum value of 16.6% (C. sonderianus) also gives evidence of a more balanced importance among the species in the CA than in the DA. As much as the IVI, this parameter reflects the effect of the anthropic action in the Caatinga biome, where the number of arboreous species is low and where there is an environmental imbalance, a more severe water scarcity and the predominance of species more adapted to these desertified conditions.


The process of desertification reduces the diversity of the arboreous  species   in   the  semi-arid region  of  Paraíba State. The most frequent species in the conserved areas are Caesalpinia pyramidalis (77.3%), Croton sonderianus (77.3%), Piptadenia stipulacea (68.2%) and Aspidospermapyrifolium (63.6%), while in  the  desertified  areas  Mimosa  tenuiflora (68.2%), C. sonderianus (31.8%), C. pyramidalis (31.8%) and Jatropha mollissima (31.8%) are more frequent.C. sonderianus, J. mollissima, Caesalpinia pyramidalis and Aspidosperma pyrifolium  both occur in conserved and desertified areas.
The absolute density (AD) in the conserved areas is higher than in the desertified, reaching 4,845 I ha-1 and 895 I ha-1, respectively. The absolute  dominance   (ADo)   followed   the  order C. pyramidalis (72.56 m2 ha-1) > Anadenanthera colubrina (69.06 m2 ha-1) > Myracrodruon urundeuva (49.06 m2 ha-1) in the conserved areas, and Mimosa tenuiflora (9.87 m2 ha-1) > C. pyramidalis (4.05 m2 ha-1) > and A. pyrifolium (2.52 m2 ha-1) in the desertified areas.
The highest importance value index (IVI) and coverage value index (CVI) were observed for C. sonderianus (13.7  and  16.6%)  and  M. tenuiflora (41.9 and 46.8%), in the conserved and desertified areas, respectively, indicating a more balanced importance between the species in the conserved areas.


The   authors   have   not  declared  any   conflict   of interests.


Alves JJA (2009). Caatinga do Cariri Paraibano. Geonomos 17(1):19-25.


Alves JJA, Souza, EN, Nascimento SS (2009). Núcleos de desertificação no estado da Paraíba. Rev. RA’E GA 17:139-152.


Aquino CMS, Oliveira JGB (2012). Avaliação de indicadores biofísicos de degradação/desertificação no núcleo de São Raimundo Nonato, Piauí, Brasil. Rev. Equador 1(1):44-59.


Barros JDS (2011). Mudanças climáticas, degradação ambiental e desertificação no semi-árido. Polêmica 10(3):476-483.


Costa TCC, Oliveira, MAJ, Accioly, LJO, Silva, FHBB (2009). Análise da degradação da caatinga no núcleo de desertificação do Seridó (RN/PB). Rev. Bras. Eng. Agríc. Ambient. 13:961-974.


Chaves ADCG, Santos RMS, Santos JO, Fernandes AA, Maracajá PB (2013). A importância dos levantamentos florístico e fitossociológico para a conservação e preservação das florestas. Agropecu. Cient. Semiár. 9(2):43-48.


Damasceno J, Souto JS (2014). Indicadores biológicos e sócio-econômicos no núcleo de desertificação do Seridó Ocidental da Paraíba. Rev. Geogr. 31(1):100-132.


Dantas AFM, Riet-Correa F, Medeiros RMT, Lopes JR, Gardner DR, Panter K, Mota RA (2012). Embryonic death in goats caused by the ingestion of Mimosa tenuiflora. Toxicon 59(5):555-557.


Freitas RAC, Sizenando Filho, FA, Maracajá PB, Diniz Filho ET, Lira JFB (2007). Estudo florístico e fitosociológico do extrato arbustivoarboreo de dois ambientes em Messias Targino Divisa RN/PB. Rev. Verde Agroecol. Desenv. Sust. 2(1):135-147.


Freitas WK, Magalhães LMS (2012). Métodos e Parâmetros para Estudo da Vegetação com Ênfase no Estrato Arbóreo. Flor. Ambient. 19(4):520-540.


Galindo ICL, Ribeiro MR, Santos MFAV, Lima JFWF, Ferreira RFAL (2008). Relações solo-vegetação em áreas sob processo de desertificação no município de Jataúba, PE. Rev. Bras. Ciênc. Solo 32(3):1283-1296.


INSA (2011). Instituto Nacional do Semiárido. Flores da Caatinga. Campina Grande: INSA 114 p.


Lima MCJS, Soto-Blanco B (2010). Poisoning in goats by Aspidosperma pyrifolium Mart.: Biological and cytotoxic effects. Toxicon 55(2-3):320-324.


Lima JLS (1996). Plantas forrageiras das caatingas: uso e potencialidades. Petrolina: EMBRAPACPTASA/PNE/RBG-KEW 28 p.


Lorenzi H (1992). Árvores brasileiras: Manual de identificação e cultivo de plantas arbóreas nativas do Brasil. Nova Odessa: Plantarum 1:368.


Lorenzi H (1998). Árvores brasileiras: manual de identificação e cultivo de plantas arbóreas nativas do Brasil. Vol.2. Nova Odessa: Plantarum 368p.


Lorenzi H (2009). Árvores brasileiras: manual de identificação e cultivo de plantas arbóreas nativas do Brasil. Vol.3. Nova Odessa: Plantarum 384 p.


Maia-Silva C, Silva CI, Hrncir M, Queiroz RT, Imperatriz-Fonseca VL (2012). Guia de plantas visitadas por abelhas na Caatinga. Fortaleza: Editora Fundação Brasil Cidadão 195p.


Martin Filho MV, Liccioti TT, Pereira GT, Marques Júnior J, Sanchez RB (2009). Perdas de solo e nutrientes por erosão num Argissolo com resíduos vegetais de cana-de-açúcar. Eng. Agríc. 29(1):8-18.


Mendonça LAR, Vásquez MAN, Feitosa JV, Oliveira JF, Franca RM, Vásquez EMF, Frischkorn H (2009). Avaliação da capacidade de infiltração de solos submetidos a diferentes tipos de manejo. Eng. Sanit. Ambient. 14(1): 89-98.


Nimer E (1988). Desertificação: realidade ou mito?. Rev. Bras.Geogr. 50(1):7-39.


Nimer E (1979). Um modelo metodológico de classificação de climas. Rev. Bras.Geogr. 41(4):59-89.


NUPEEA (2010). Núcleo de Publicações em Ecologia e Etnobotânica Aplicada. Caatinga: biodiversidade e qualidade de vida. Bauru: Canal6 119 p.


Poggiani F, Oliveira R, Cunha GC (1996). Práticas de ecologia florestal. Universidade de São Paulo pp. 1-44.


Ramos JC, Bertol I, Barbosa FT, Marioti J, Werner RS (2014). Influência das condições de superfície e do cultivo do solo na erosão hídrica em um Cambissolo húmico. Rev. Bras. Ciênc. Solo 38(5):1587-1600.


Sá IB, Cunha TJF, Teixeira AHC, Angelotti F, Drumond MA (2010). Desertificação no Semiárido brasileiro. In. Conferência Internacional: clima. Susten. Desenvolv. Reg. Semiáridas Fortaleza 2:8.


Salgado-Laboriau ML (1994). História ecológica da Terra. São Paulo: Editora Edgard Blucher 320 p.


Silva EC, Nogueira RJMC, Azevedo Neto AD, Brito JZ, Cabral EL (2004). Aspectos ecofisiologicos de dez espécies em uma área de caatinga no município de Cabaceiras, Paraíba, Brasil. Iheringia 59(2):201-205.


Siqueira Filho JA, Santos APB, Nascimento MFS, Espírito Santo FS (2009). Guia de campo de árvores da Caatinga. Petrolina: Franciscana 195 p.


Sousa EP, Silva VPR, Campos JHBC, Oliveira SD (2012). A Teoria da Entropia na Análise da Precipitação no Estado da Paraíba. Rev. Bras. Geogr. Física 5(2):386-399.


Souza BI (2008). Cariri paraibano: do silêncio do lugar à desertificação. Porto Alegre: UFRGS. 198 p. (Tese de Doutorado)


Souza BI, Menezes R, Artigas RC (2015). Efeitos da desertificação na composição de espécies do bioma Caatinga, Paraíba/Brasil. Invest. Geogr. 88:45-59.