International Journal of Biodiversity
Volume 2016 (2016), Article ID 4909158, 11 pages
http://dx.doi.org/10.1155/2016/4909158

Research Article

Diversity, Population Structure, and Above Ground Biomass in Woody Species on Ngomakurira Mountain, Domboshawa, Zimbabwe

Clemence Zimudzi¹ and Christopher Chapano²

¹Department of Biological Sciences, University of Zimbabwe, P.O. Box MP 167, Mount Pleasant, Harare, Zimbabwe
²National Herbarium and Botanic Garden, P.O. Box A889, Avondale, Harare, Zimbabwe

Received 14 April 2016; Revised 8 June 2016; Accepted 23 June 2016

Academic Editor: Alexandre Sebbenn

Copyright © 2016 Clemence Zimudzi and Christopher Chapano. This is an open access article distributed under the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.

Abstract.

The diversity, structure, species composition, and above ground biomass of woody plants on Ngomakurira mountain in Zimbabwe were studied. A systematic random sampling approach was adopted to establish 52 sampling plots measuring 10 × 10 m across 3 study strata in the 1266 ha study area. Woody species occurring in each plot were identified and the circumferences of trees with diameters >8.0 cm at 1.3 m height were measured. A total of 91 species belonging to 74 genera and 39 families were identified in the sample plots. A Shannon-Wiener index mean value of 3.12 was obtained indicating high species diversity on the mountain. The DBH size class distribution showed inverse J distribution patterns across the three study strata, but with only 3 individual plants with DBH > 30 cm. Mean basal area was 15.21 m² ha⁻¹ with U. kirkiana and J. globiflora contributing approximately 30% of the basal area. The estimated above ground biomass ranged from 34.5 to 65.1 t ha⁻¹. Kruskal-Wallis-H test showed no significant differences in species richness, stem density, basal area, above ground biomass, and evenness, across the study strata (). Ngomakurira woodland has potential to regenerate due to the presence of many stems in the small diameter size classes.

1. Introduction

The miombo ecoregion covers approximately 2.7 million km² of southern, central, and eastern Africa [1] and is one of the world’s priority areas for conservation [2]. The woodlands provide ecosystem, socioeconomic, and cultural services that sustain local livelihoods [3]. Miombo woodlands contribute considerably to household livelihoods by providing fuel, construction materials, grazing, medicine, food, materials of cultural importance, and potentially supplementing incomes especially for poor communal and urban dwellers [4]. In Zimbabwe the woodlands cover approximately 42% of the country [5], but the biodiversity composition and structure are mostly poorly documented.

Miombo woodland dynamics is strongly influenced by anthropogenic factors [6–8] and most ecosystems are being threatened by the increased demand for services by the burgeoning human population [9]. Woodland ecosystems and their valuable biodiversity resources are being lost at an accelerated rate [10–12], thereby altering ecosystem function and consequently threatening the provision of services and goods especially to poor rural communities [13].

Knowledge of the biomass of a woodland is important in estimating the carbon stocks of an area. Such information is invaluable in management for coming up with strategies for climate change mitigation [14]. Carbon stocks data can also be used to mobilise financial resources through C-based Payments for Ecosystem Services (PES) [15]. There is limited quantitative information of carbon stocks in southern African forests [15], despite the huge importance of such information. Data on carbon stocks, species composition, and vegetation structure is invaluable to forest management in designing strategies for sustainable management under different disturbance regimes [14].

Ngomakurira means “drums sounding” in the local Shona language and is a mountain located near the Domboshawa Caves, just outside of Harare in Zimbabwe. It forms part of a granitic topography with dome-shaped inselbergs near the village of Domboshawa in the headwaters of the Mazowe river. The mountain derives its name from the traditional African drums that were played during religious festivals. The mountain is considered sacred by the local community and is used for various religious rites. Old San rock art paintings are also found in caves and on the vertical rock face of the main mountain. The mountain is protected and managed by the National Museums and Monuments of Zimbabwe to conserve its cultural and archaeological value, biodiversity and catchment value. Ngomakurira Trust, formed by the Goromonzi Rural District Council in partnership with National Museums and Monuments of Zimbabwe as well as the Environmental Management Agency (EMA), initiated the ecotourism project at Ngomakurira mountain by converting hills, used communally for grazing, fuel wood collection, and harvesting of wild fruits, into a properly managed tourist facility.

Ngomakurira mountain is surrounded by communal areas and such areas are vulnerable to anthropogenic activities and edge effects [19] as local communities continue to depend on the woodlands for sustenance. A participatory forest management approach (PFM), which involves locals in management decisions, has recently been implemented for an ecotourism project at Ngomakurira mountain. The success of the project will depend on an understanding of the woodland dynamics and especially the role of disturbance factors in shaping the woodland structure.

This study seeks to determine the following: (a) the species composition, structure, and diversity and biomass accumulation of woody plants on Ngomakurira mountain, (b) the variability of these diversity indices across the sample plots, and (c) the relationships between species diversity, richness, basal area, and above ground biomass.

2. Materials and Methods

2.1. Study Area

Ngomakurira is a large granite mountain located in the Goromonzi district, in Chinamora communal lands, approximately 30 km NE of Harare in Zimbabwe. It is located between 17°32′46.46′′S–17°35′34.92′′S latitudes and 31°14′21.61′′E–31°15′51.89′′E longitudes. Altitude varies from 1307 to 1638 metres above sea level. The total area covered by the mountain is 1266 ha.

Ngomakurira mountain is located in agroecological zone IIa [20] with rainfall fairly reliable falling from November to March/April and mean annual rainfall ranging from 750 to 1 000 mm/year. Mean annual temperature range is 15–20°C. The soils are shallow and generally classified as paraferralitic soils [21]. Deep soils are found at the base of the hill, getting shallower and rocky to absent at the higher levels. Ngomakurira lies in a communal area with poor rural households mainly involved in subsistence farming, though some are involved in horticulture to supply urban markets in Harare.

The study area falls under the deciduous miombo savanna woodland [22], a vegetation type dominated by Brachystegia spp. and Julbernardia globiflora. Reference [23] described this type of vegetation as dry miombo. The vegetation on the mountain is concentrated in the lower and middle zone of the mountain with most of the top area consisting largely of bare rock.

2.2. Sampling Design and Data Collection

Field work was conducted in February 2016. An initial study of satellite images of the study area followed by a field reconnaissance survey [24] assisted in making decisions on sampling strategy to use. From the surveys the vegetation of the mountain appears mixed with no obvious vegetation communities. We, however, divided the mountain into three sections: the vegetation at the base, middle, and top of the mountain. In each section quadrats measuring 10 × 10 m were demarcated following the methods by [25]. Random numbers were used to locate the position of plots in each stratum [24]. We sampled 15 quadrats at the base, 25 in the middle, and 12 at the top. Sample plots were distributed according to the relative sizes of the strata.

Global positioning system (GPS) measurements were taken for each sample plot using a Garmin 12XL Global Positioning System. In each plot all woody species were identified in the field and a few were collected and verified at the National Herbarium in Harare. Tree height was visually estimated, and stem circumference at 1.3 m was measured using a tape measure for plants with a circumference ≥ 8 cm [26]. For multistemmed plants, the circumferences were measured separately.

2.3. Data Analysis

2.3.1. Floristic Indices and Biodiversity

The data consisting of plot numbers, species, and circumference was entered into an Excel spreadsheet and the following parameters were calculated:(1)DBH = circumference/π.(2) Basal area = .(3) Relative dominance = (total basal area for a species/total basal area of all species) × 100.(4) Relative density = (number of individuals of a species/total number of individuals) × 100.(5) Relative frequency = (frequency of a species/sum of all frequencies) × 100.(6) Relative diversity = (number of a species in a family/total number of species) × 100.(7) The importance value index (IVI) = relative dominance + relative density + relative frequency.(8) The family importance value (FIV) = relative dominance + relative density + relative diversity.(9) Shannon-Wiener’s index of diversity , where ; is the number of individual trees present for species , and is the total number of individuals [27].(10) Evenness = , where is the Shannon-Wiener index and is the total number of species(11) The Kruskal-Wallis test was done using SPSS statistical package version 16.0 (2007).(12) The Spearman rank correlations between diversity variables were calculated in Excel 2007.

2.3.2. Classification of Sample Plots

Classification of the sample plots was done using Agglomerative Hierarchical Cluster Analysis in SPSS statistical package version 16.0 (2007). Classification was done using weighted species composition data with weighting achieved using the number of stems of each species measured in each plot. Euclidean distance was used to compute distances between plots.

2.3.3. Above Ground Biomass

Three allometric equations (Table 1) were used to estimate tree biomass. The equations show relationships between biomass and DBH. These equations are general for all species as previous studies have already shown that species specific equations are not necessary in estimating biomass [14, 28]. The equations were generated from neighbouring countries with similar ecosystems, climate, and soils. References [12, 14, 29] used a similar approach in estimating biomass. Biomass estimations were made only for trees with DBH ≥ 5 as the equations were developed to estimate biomass within these DBH ranges.

Table 1: Allometric equations used to estimate above ground biomass.

Equation(s)
Source country
Notes
Reference

Zambia
Trees < 10 cm DBH
[16]

Zambia
Trees > 10 cm DBH
[16]

Tanzania
For trees ⩾ 5 cm DBH
[17]

Tanzania
For trees ⩾ 5 cm DBH
[18]

= DBH, = biomass (Kg).

3. Results

3.1. Tree Species Composition

A total of 91 species belonging to 74 genera and 39 families were recorded (see Appendix). In terms of the number of species, the Rubiaceae is the largest family with 11 species, followed by the Caesalpiniaceae (8 species), Phyllanthaceae (6 species), Papilionaceae and Combretaceae (5 species each), Lamiaceae, Mimosaceae and Anacardiaceae (4 species each), Burseraceae, Myrtaceae, Proteaceae, and Sapindaceae (3 species each), Clusiaceae, Dipterocarpaceae, Ebenaceae, Moraceae, Ochnaceae, and Strychnaceae (2 species each), and the remainder have one species each. The number of species were 59 at the bottom, 62 at the middle, and 48 at the top of the mountain.

Table 2 shows the five dominant species at each stratum in decreasing importance value index (IVI). Julbernardia globiflora dominates at the bottom, Uapaca kirkiana at the middle, and Brachystegia glaucescens at the top of the mountain. In the three strata the common dominant species were J. globiflora, B. glaucescens, U. kirkiana, and Euphorbia matabelensis with mean IVI values of 39.5, 28.43, 25.2, and 19.9, respectively.

Table 2: The five species with the highest importance value index (IVI) in each stratum at Ngomakurira mountain.

Mountain strata
Species
Relative frequency (%)
Relative density (%)
Relative dominance (%)
Species important value index/300

Bottom
J. globiflora
8.064
25.478
22.830
56.372

L. discolor
6.452
6.879
5.333
18.663

E. matabelensis
2.688
9.427
6.268
18.383

U. kirkiana
2.151
5.733
10.460
18.343

P. maprouneifolia
3.763
3.057
8.465
15.286

Middle
U. kirkiana
3.833
9.269
20.665
33.767

J. globiflora
6.620
11.765
11.848
30.233

B. glaucescens
6.272
9.002
12.161
27.435

E. matabelensis
2.091
9.804
9.896
21.790

L. discolor
5.575
4.724
6.048
16.347

Top
B. glaucescens
6.154
18.878
19.234
44.265

J. globiflora
7.692
11.905
12.374
31.971

U. kirkiana
2.308
8.674
12.473
23.454

E. matabelensis
3.078
10.034
6.299
19.410

S. guineense
1.539
6.633
9.140
17.312

Some species increased in dominance with increasing altitude whereas others decreased. Combretum molle, Elephantorrhiza goetzei, Monotes engleri, Parinari curatellifolia, Strychnos spinosa, Zanha africana, and B. glaucescens increased up the mountain whereas C. mossambicensis, E. matabelensis, Margaritaria discoidea, Pseudolachnostylis maprouneifolia, Tapiphyllum velutinum, and J. globiflora showed a decrease.

There were some species confined to only one stratum of the mountain. Acacia goetzei, Afrocanthium lactescens, Commiphora mollis, Diospyros natalensis, and Psydrax livida were only recorded at the top of the mountain. Brachylaena discolor, Combretum apiculatum, Combretum collinum, Empogona kirkii, Erythrina abyssinica, Ficus natalensis, Psidium guajava, Rhus leptodictya, and Vitex payos were found at the middle and Cussonia arborea, Dombeya rotundifolia, Faurea rochetiana, Ficus sur, Gardenia ternifolia, Maesa lanceolata, Monotes glaber, Mussaenda arcuata, Pericopsis angolensis, Protea welwitschii, Strychnos madagascariensis, and Ximenia caffra were found at the bottom. The number of species confined to a particular stratum decreased from the bottom to the top.

A number of fire tolerant species like P. maprouneifolia, Pterocarpus angolensis, Combretum sp., Burkea Africana, Terminalia stenostachya, and Diplorhynchus condylocarpon were also recorded on the mountain.

3.2. Shannon-Wiener Diversity and Evenness

Shannon-Wiener values for the bottom, middle, and top of the mountain were 3.07, 3.32, and 2.96, respectively, with a mean of 3.12 (Table 3). Kruskal-Wallis test results of the Shannon-Wiener values show no significant differences () across the study strata. The following species contributed most to the high diversity at the mountain: J. globiflora (0.85), E. matabelensis (0.72), B. glaucescens (0.67), U. kirkiana (0.59), and Lannea discolor (0.46). Species evenness is highest at the middle and lowest at the top of the mountain, but no significant differences () were observed across the study strata (Table 3).

Table 3: Kruskal-Wallis H test results of the study variables at the bottom, middle, and top of Ngomakurira mountain (values in brackets show least values).

Variable
Median (range)

Bottom
Middle
Top
value

Basal area (m²/ha)
14.23 (4.28)
12.40 (3.38)
18.99 (6.01)
0.161

Shannon-Wiener index
3.07
3.32
2.96
0.299

Above ground biomass (t/ha)
34.49 (7.48)
46.64 (5.66)
65.17 (9.36)
0.165

Species richness
59
62
48
0.479

Evenness
0.80 (0.63)
0.86 (0.56)
0.78 (0.56)
0.115

Stem density/ha
4900 (2700)
4400 (1000)
4850 (2100)
0.646

3.3. Stem Density and DBH

A total of 2495 stems were measured in the sample plots. About a quarter of the trees (25.7%) were multistemmed and accounted for slightly over half of the stems (1770 stems). Mean stem density for stems with DBH ≥ 5 cm was and stem ha⁻¹ for DBH < 5 cm. For stems with a DBH ≥ 2.5 cm stem density was highest at the bottom and least in the middle of the mountain. The mean diameter was  cm, with the majority of trees (91%) with DBH < 10 cm. Figure 1 shows the diameter class distribution of the trees at Ngomakurira showing an inverse J distribution. Only three individual trees had DBH > 30 cm and these were species of S. guineense, B. boehmii, and B. glaucescens. U. kirkiana had more members in the higher size classes between 20 and 29 cm DBH.

Figure 1: Diameter class distribution of the woody plants at the bottom, middle, and top of Ngomakurira mountain.

3.4. Basal Area

The basal area across the plots ranged from 3.38 to 41 m² ha⁻¹ with a mean of 15.21 m² ha⁻¹. The following species contributed most to the basal area: U. kirkiana (15.6%), J. globiflora (14.9%), B. glaucescens (12.4%), E. matabelensis (8.0%), L. discolor (5.5%), S. guineense (5.3%), M. engleri (4.1%), P. maprouneifolia (3.9%), and B. boehmii (3.8%).

3.5. Above Ground Biomass

Above ground biomass increased from the bottom to the top of the mountain but showed no significant difference between the study strata. Mean AGB among plots ranged from 5.7 to 134.4 tonnes ha⁻¹. Mean AGB ranged from 34.5 to 65.1 tonnes ha⁻¹ among the study strata (Table 3). The top ten trees that contributed most to the above ground biomass were U. kirkiana (19.5%), J. globiflora (13.3%), B. glaucescens (12.9%), E. matabelensis (6.6%), S. guineense (6.5%), L. discolor (5.4%), M. engleri (5.3%), P. maprouneifolia (4.3%), B. boehmii (4.0%), and P. curatellifolia (3.5%).

The AGB was highest in the 5–10 cm DBH class and least in the 20–25 cm class (Figure 2). The 5–10 cm DBH class contributed approximately 35% of the total AGB.

Figure 2: Distribution of above ground biomass of species in different DBH classes.

3.6. Relationship among the Variables

Table 4 shows Spearman’s rank correlation coefficients for the different variables assessed at Ngomakurira. Basal area was positively correlated to all the diversity parameters. Stem density was positively correlated to basal area, species richness, diversity, and AGB. Significant correlations were found between basal area and AGB (0.79), stem density and basal area (0.47), species richness and Shannon-Wiener index (0.82), and evenness and Shannon-Wiener index (0.69). Weak correlations were found between basal area and species richness (0.13), species richness and stem density (0.23), and evenness and species richness (0.22). Negative correlations were found between AGB and species richness (−0.33), Shannon-Wiener (−0.09) and evenness (−0.05), and also stem density and evenness (−0.13).

Table 4: Spearman’s rank correlation for diversity parameters ( indicates significance (, df = 50)).

Basal area
Species richness
Shannon
AGB
Stem density
Evenness

Basal area
1

Species richness
0.131
1

Shannon
0.037
0.815
1

AGB
0.7858
−0.035
−0.085
1

Stem density
0.471
0.228
0.049
0.053
1

Evenness
0.061
0.219
0.6889
−0.052
−0.132
1

3.7. Vegetation Communities

The dendrogram in Figure 3 shows sample plots clustering into three vegetation communities.

Figure 3: Hierarchical cluster analysis dendrogram showing classification of vegetation plots (colour of plot numbers—red: at the bottom, black: middle, and blue: the top of the mountain).

The vegetation communities do not correspond to the altitude strata used to sample the species as there is a mixture of plots from the three altitude ranges in each vegetation subtype. The Caesalpinoid species B. glaucescens and J. globiflora and their associated species L. discolor, V. infausta, and Combretum molle occur in all the three vegetations communities. In community A these common species occur mixed mainly with E. matabelensis, T. velutinum, V. payos, C. mossambicensis, and M. discoidea. Community B includes the common elements plus B. boehmii, P. maprouneifolia, M. engleri, R. longipes, O. pulchra, and D. viscosa whilst community C includes U. kirkiana, B. spiciformis, P. curatellifolia, R. longipes, M. engleri, and P. febrifugum.

4. Discussion

4.1. Tree Species Composition

Species diversity assessments are a way of auditing an ecosystem to understand its dynamics and quality and how disturbance factors are impacting on it [30]. The number of species obtained here compares well with those obtained in similar dry miombo woodlands in Zimbabwe [26] and elsewhere [18, 31]. Other studies have, however, recorded lower numbers; for example, [32, 33] recorded 17 species and 59 at Mapembe Nature reserve and Save Runde, respectively, in Zimbabwe and [34] recorded 69 species in Mozambique. Reference [35] recorded numbers as high as 229 from Tanzania. Differences in species richness in miombo woodlands is related to climatic, edaphic, and disturbance factors [31].

The dominance of miombo vegetation by legume families (Caesalpiniaceae, Papilionaceae, and Mimosaceae) is confirmed in this study as similarly observed in other miombo regions [12, 31]. However, observations of high numbers of woody species of the Rubiaceae are unusual as members of this family often dominate among the shrubs [31, 36]. This shows that differences in dominance patterns are possible on a local scale in miombo woodlands.

Across the study strata IVI indices show altitudinal changes in dominance patterns of a number of species. Observations of B. glaucescens being the dominant species at higher altitudes and J. globiflora at lower altitudes have also been made by [37]. The middle altitude peak in species richness observed in this study is a commonly observed phenomenon in studies on species distribution along altitudinal gradients [38]. Several hypotheses have been proposed to explain this, but all are based on the fact that species ranges vary across elevational gradients becoming narrower at the top and hence less richness is observed at those altitudes. At middle altitudes, the species ranges overlap, thereby maximising the number of species [39]. Many studies have shown that altitude is the major determinant of species composition on mountains as such related variables like temperature and edaphic factors vary with altitude [40].

The prevalence of fire tolerant species on the mountain indicates that fire is one of the drivers of species composition on the mountain. References [41, 42] made similar observations in studies of fire and elephant affected miombo regions in Zimbabwe and Mozambique, respectively.

4.2. Vegetation Communities

The 3 communities shown in the dendrogram in Figure 2 are typical miombo woodlands dominated by the Caesalpinoid species B. glaucescens and J. globiflora and their associated species. References [31, 43] noted that elevation was the most important factor shaping species communities in miombo woodlands. The results from this study support these observations as the spatial distribution of species like B. glaucescens, J. globiflora, and U. kirkiana is influenced by altitude. Presence of species confined to different strata also supports the influence of altitude in shaping communities. Altitude influences water availability, temperature, and soil characteristics which directly affect plant growth performance.

4.3. Shannon-Wiener Diversity and Evenness

The woodland at Ngomakurira mountain has high species diversity as shown by the Shannon-Wiener index values (Table 3). Reference [44] reported that Shannon-Wiener index values fall between 1.5 and 3.5 for tropical woodlands, so the value obtained here is within the expected range. Ecosystems with Shannon-Wiener values greater than 2 are regarded as medium to highly diverse in terms of species [7]. Reference [45] attributed the high species diversity in miombo woodlands to the wide diversity of habitats present. These results are comparable to those found in Zimbabwe by [26] (Shannon 3.42) and [30] (Shannon 3.28) and in Tanzania by [31] (Shannon 3.44). Our results are relatively larger than those found by [46] (Shannon 2.8) in Zambia, [29] (Shannon 1.05) in Tanzania, and [34] (Shannon 1.25) in Mozambique. Higher Shannon values have also been recorded from Tanzanian study [7] (Shannon 4.27). Differences in richness and diversity possibly result from differences in rainfall regimes [12] and disturbance history [1].

The similarity in evenness across the study strata shows that the woodland is dominated by a few species [47].

4.4. Stem Density and DBH

The multistemmed tree architecture observed at Ngomakurira mountain is indicative of a history of disturbance, particularly herbivory [48]. Herbivory is high at Ngomakurira mountain as local communities have free access to graze their animals. The mean stem density obtained in this study ( stems ha⁻¹) was much higher when compared to densities reported from other miombo woodlands (348–1495 stems ha⁻¹) [7, 14, 33, 34, 47]. Ngomakurira mountain is therefore well stocked. Our results, however, compare with those obtained by [31, 46] in Tanzania and Zambia, respectively.

The DBH distribution (Figure 1) shows a common trend obtained in natural forests where stem densities decrease with increasing diameter. Forests with this inverse “J” shaped curve DBH distribution pattern are generally said to show active regeneration and recruitment [12]. Recent studies have questioned reliance on inverse J distributions in forest management as they are based on a biologically unrealistic assumption of equal mortality among size classes [49]. Declining populations may also show the classic “inverse J” shape and some stable populations may not show this shape due to differences in growth rates among size classes [50]. Most of the common miombo woody species reach much larger DBH sizes in mature forests [26]. The lack of larger size classes may be due to harvesting of such trees for sale in the urban areas as evidenced by numerous stumps in the study area. Exploitation for local consumption must be minimal as studies elsewhere show preference for small size classes for firewood, poles, and house construction [44]. Fire may also be a factor as few seedlings may survive to reach mature size classes [31].

4.5. Basal Area

The estimated basal area obtained in this study (15.21 m² ha⁻¹) compares with that of [31] () and [49] (15–15.6) in Tanzania and [14] in Zambia. References [25, 51] reported lower basal areas. Differences with our results may be due to species composition and site differences.

4.6. Above Ground Biomass

The AGB of woody trees is the largest carbon pool of a forest [29] and can be used to calculate the carbon stock density as 50% of AGB is assumed to be carbon [34]. The carbon stock estimate of a woodland is of importance to management for consideration of strategies that promote carbon storage. Knowledge of carbon stocks is also important in the development of a payments system to reduce emissions from deforestation and degradation [15]. The estimates for above ground biomass for Ngomakurira mountain (34.5–65.1 t ha⁻¹) are comparable to those reported by [23] from Zambia and Zimbabwe (52 t ha⁻¹), [29] from Tanzania (46.4 t ha⁻¹), and [15] from Mozambique (42.2 t ha⁻¹). Any differences may be due to differences in growth conditions [42], species composition, allometric equations, and plot sizes [29]. Reference [12] in a study of sites of different utilisation levels in Tanzania reported carbon stocks of 14.6 t ha⁻¹ in high utilisation sites, 33.1 t ha⁻¹ in sites of medium utilisation, and 28.5 t ha⁻¹ in areas of low utilisation. Using these values as a benchmark we can conclude that the woodland utilisation at Ngomakurira is low, despite the many signs of human disturbance like wood cutting and grazing. For management this means that moderate utilisation should be promoted to enhance carbon stocks. AGB of Ngomakurira mountain, however, must be higher than estimates presented here as the allometric equations used only included trees with DBH ≥ 5 cm, thereby excluding all trees with DBH < 5 cm.

4.7. Relationship among the Diversity Variables

The positive correlation between basal area, species richness, diversity, stem density, AGB, and evenness means that to get the best basal area in a woodland each of the diversity parameters must be at its maximum. This of course in not achievable due to disturbance factors, competition among species, and variability of environmental factors. Reference [15] made similar observations in Mozambique. A significant correlation between basal area and biomass observed in this study has also been observed in similar studies elsewhere [52]. Basal area integrates both the number and size of trees and is a good predictor of biomass [52]. The correlation coefficient of 0.7858 is, however, slightly lower than expected since a positive linear relationship was expected. This variation may be a result of the fact that the allometric equations used were not generated locally or differences in species composition between our study area and the areas where such equations were generated. High correlations between Shannon and species richness and evenness were expected as these measures of diversity in a way represent the same phenomenon [53].

The observations of a negative correlation between AGB and species richness and diversity and a positive correlation between AGB and stem density corroborate finding by [54].

5. Conclusions

The vegetation at Ngomakurira is typical miombo dominated by the species Brachystegia glaucescens, Julbernardia globiflora, and Uapaca kirkiana. The woodland has high species richness and diversity showing that it is in good condition. This is further supported by the DBH distribution which shows an inverse J shape typical of stable populations. This is good sign of the sustainability of the woodland stock which ensures sustainable supply of goods and services to local communities. Effects of anthropogenic effects were evident and would require management, but detailed studies on levels of resource extraction required for sustainable management of the woodland need to be carried out. This is important in conservation because humans residing next to protected areas need resources from such areas and conflicts often arise when they are prevented from accessing such resources.

Appendix

Woody Trees Recorded at Ngomakurira

Taxa  Anacardiaceae Lannea discolor (Sond.) Engl. Ozoroa reticulata (Baker f.) R. & A. Fern. Rhus leptodictya Diels Rhus longipes Engl. Annonaceae Hexalobus monopetalus (A. Rich.) Engl. & Diels Apocynaceae Diplorhynchus condylocarpon (Müll. Arg.) Pichon Araliaceae Cussonia arborea A. Rich. Asteraceae Brachylaena discolor DC. Burseraceae Commiphora marlothii Engl. Commiphora mollis (Oliv.) Engl. Commiphora mossambicensis (Oliv.) Engl. Celastraceae Gymnosporia senegalensis (Lam.) Loes. Chrysobalanaceae Parinari curatellifolia Benth. Clusiaceae Garcinia buchananii Baker Psorospermum febrifugum Spach Combretaceae Combretum apiculatum Sond. Combretum collinum Fresen. Combretum molle G. Don Terminalia brachystemma Hiern Terminalia stenostachya Engl. & Diels Dipterocarpaceae Monotes engleri Gilg Monotes glaber Sprague Ebenaceae Diospyros natalensis (Harv.) Brenan Euclea natalensis A. DC. Euphorbiaceae Euphorbia matabelensis Pax Fabaceae-Caesalpinioideae Brachystegia boehmii Taub. Brachystegia glaucescens Burtt Davy & Hutch. Brachystegia spiciformis Benth. Brachystegia utilis Burtt Davy & Hutch. Burkea africana Hook. Julbernardia globiflora (Benth.) Troupin Peltophorum africanum Sond. Senna singueana (Delile) Lock Fabaceae-Mimosoideae Acacia goetzei Harms subsp. microphylla Brenan Albizia antunesiana Harms Dichrostachys cinerea (L.) Wight & Arn. Elephantorrhiza goetzei (Harms) Harms Fabaceae-Papilionoideae Bobgunnia madagascariensis (Desv.) J. H. Kirkbr. & Wiersema Dalbergia nitidula Baker Erythrina abyssinica DC. Pericopsis angolensis (Baker) Meeuwen Pterocarpus angolensis DC. Flacourtiaceae Flacourtia indica (Burm. f.) Merr. Heteropyxidaceae Heteropyxis dehniae Suess. Lamiaceae Rotheca myricoides (Hochst.) D. A. Steane & Mabb. Tetradenia riparia (Hochst.) Codd. Vitex mombassae Vatke Vitex payos (Lour.) Merr. Maesaceae Maesa lanceolata Forssk. Meliaceae Turraea nilotica Kotschy & Peyr. Moraceae Ficus natalensis Hochst. subsp. natalensis Ficus sur Forssk. Myrtaceae Psidium guajava L. Syzygium cordatum Hochst. ex C. Krauss Syzygium guineense (Willd.) DC. subsp. afromontanum F. White Ochnaceae Ochna inermis (Forssk.) Penz. Ochna pulchra Hook. subsp. pulchra Olacaceae Ximenia caffra Sond. Phyllanthaceae Bridelia cathartica G. Bertol. subsp. melanthesoides (Baill.) J. Léonard Flueggea virosa (Willd.) Voigt subsp. virosa Margaritaria discoidea (Baill.) G. L. Webster var. nitida (Pax) Radcl.-Sm. Pseudolachnostylis maprouneifolia Pax Uapaca kirkiana Müll. Arg. Uapaca nitida Mull. Arg. var. nitida Pittosporaceae Pittosporum viridiflorum Sims var. Proteaceae Faurea rochetiana (A. Rich.) Pic. Serm. Faurea saligna Harv. Protea welwitschii Engl. Rhamnaceae Ziziphus mucronata Willd. Rubiaceae Afrocanthium lactescens (Hiern) Lantz Catunaregam taylorii (S. Moore) Bridson Coptosperma neurophyllum (S. Moore) Degreef Empogona kirkii Hook. f. subsp. kirkii Gardenia ternifolia Schumach. & Thonn. subsp. jovis-tonantis (Welw.) Verdc. Hymenodictyon floribundum (Hochst. & Steud.) B. L. Rob. Mussaenda arcuata Poir. Pavetta schumanniana K. Schum. Psydrax livida (Hiern) Bridson Tapiphyllum velutinum (Hiern) Robyns Vangueria infausta Burch. subsp. infausta Rutaceae Casimiroa edulis La Llave Sapindaceae Allophylus africanus P. Beauv. Dodonaea viscosa Jacq. Zanha africana (Radlk.) Exell Sapotaceae Englerophytum magalismontanum (Sond.) T. D. Penn. Sterculiaceae Dombeya rotundifolia (Hochst.) Planch. Strychnaceae Strychnos madagascariensis Poir. Strychnos spinosa Lam. Umbelliferae-Apiaceae Steganotaenia araliacea Hochst. Urticaceae  Pouzolzia mixta Solms Verbenaceae Lantana camara L.

Competing Interests

The authors declare that there is no conflict of interests regarding the publication of this paper.

Acknowledgments

The authors would like to thank the Director of the National Museums and Monuments Mr. Bvocho for permission to carry out the study at Ngomakurira Mountain. They are grateful for support in the field by Muteyo Tsitsi, Madondo Kudakwashe, Haurovi Vimbayi, Mazambani Simbarashe, Mapfumo Eustina, Mazivisa Rumbidzai, and Tembo Michelle, staff of the National Herbarium and Botanic Garden. Transport to the study site was provided by the National Herbarium and Botanic Garden and the Biological Sciences Department, University of Zimbabwe.

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