The Lake Manyara Watershed sub-basin (Figure 1) is located in the north-central part of Tanzania at 3˚25'S - 3˚48'S, 35˚44'E - 35˚53'E and has a catchment area of 7667.1 km². The landscape of this sub-basin is characterised by water divides and several perennial and seasonal rivers from complex of highlands in Karatu, Ngorongoro, Mbulu and Nou Forest that are drained by Lake Manyara. The most prominent tributaries are the Makuyuni, Simba, Kirurumu and Mto wa Mbu rivers. The watershed further extends to Mbulu plateau which elevates at 2135 m forming the western boundary and the southern boundary is featured by the Kwahara Mountain rising to over 2400 m. The eastern boundary lies on Lolkisale hill and the north-eastern boundary extends to the Lossimingori, Burko and Monduli.

The watershed’s average precipitation varies between 700 mm to 1200 mm the east of the plain and top of the plateau respectively. The temperature ranges between 16˚C and 23˚C, and the vegetation pattern is dictated by rainfall and temperature gradients, i.e., the highlands are covered with montane forests whereas the lowland/plains are dominated with sparsely distributed vegetation mostly

savanna type bushes and shrubs.

The boundaries of the study area were delineated using the Lake Manyara Watershed (LMW) polygon supplemented with Digital Elevation Model (DEM) acquired from ALOS PALSAR with spatial resolution of 12.5 m in the QGIS 3.10 used to estimate elevation, slope and delineate the location of rivers streams network within a 30 m buffer.

The recent trends of immigration from other parts of the country in search for opportunities like crop farming and grazing land have continued to increase the population growth in the LMWE. The land use pattern in the LMWE is dominated mainly by rural agricultural landscapes used mainly for crop farming (sugar cane, onion, sunflower, maize, sesame and peas) mixed with livestock keeping, scattered settlement and riparian forest patches. It is a landscape mosaic exploited by crop farmers and livestock keepers, thanks to conducive environment owing to fertile soils and water resources availability. Flat terrains adjacent to the rivers has remained suitable for crop farming due to deposition of alluvial soil, making the land fertile compared to the surrounding areas. The level of agricultural mechanisation is relatively low, hence putting the entire agricultural systems at subsistence level. Pastoralism is also an economic mainstay among community members in the watershed. A previous study by [15] noted a significant change in land use change relating to agriculture whereby farmland had increased by 118% between 1958-1987 and further increased by 44% in 2001 against baseline of 1987.

A buffer of 60 m was established along from downstream to upstream to include areas with different land use categories (i.e., homegardens, crop fields, woodlots, open canopy forest and closed canopy forest) within LMWE. The land use categories have the following descriptions: 1) Homegardens—mainly dominated by agroforestry practices. Tree layers, arable and commercial crop such as banana, yams and maize; 2) Crop fields—these are characterised by both arable and commercial crops such as maize, bean, sugar cane; 3) Woodlots—these are found close to households, growing in small mosaics. Either naturally regenerated or planted; 4) Open Canopy Forest—these are found in areas where there is some decrease of human encroachment, trees are relatively sparsely stocked; and 5) Closed canopy forest—these are found in areas where there is little or no human encroachment, trees are densely stocked.

Sampling clusters were systematically established at an interval of 2 km. Within each cluster, five plots were laid out measuring 20 m × 10 m. Each plot was separated from the other by an interval of 100 m. In each plot, all woody plant equal and greater than 5 cm diameter were identified, their diameters measured at breast height (1.3 m) using a calliper and recorded. Overall, 270 plots were surveyed in the five land use types within the riparian ecosystems of LMWE, composed of closed canopy forest (n = 47 plots), Open canopy forest (n = 56 plots), homegardens (n = 17 plots), woodlots (n = 20 plots), and crop fields (n = 130 plots).

In order to understand the influence of environmental variables on species richness and abundance, and stand parameters (basal area and stock density), the centroid for each of the 270 plots was used; to quantify 1) annual temperature, annual precipitation, WorldClim database (https://www.worldclim.org), 2) elevation from SRTM digital elevation model from the US Geological Survey (https://earthexplorer.usgs.gov), and 3) slope, from DEM using QGIS.

A total of 1954 individuals was recorded comprised of 139 woody plant species out of which only 16 species were exotics. Major vegetation types unveiled were those comprised of Vachellia/Acacia-Combretum-Commiphora in the non-riverine areas and Rauvolfia-Ficus-Albizia in the riverine areas, despite presence of exotic species. The study observations noted low level of exotic species integration especially in the homegardens, crop fields and woodlots, where farmers manage tree planting and retention. The dominant exotic species in the landscape were comprised of Senna spectabilis, Psidium guava and Acrocarpus flaxinifolius.

Species richness (ANOVA, df = 4, F = 4.85, P ≤ 0.004), Species abundance (ANOVA, df = 4, F = 3.74, P = 0.005), stocking density (ANOVA, df = 2, F = 4.62, P = 0.005), and basal area (ANOVA, df = 4, F = 4.59, P < 0.007) varied significantly between all five land use categories (Table 1, Figure 2). Unexpectedly, the mean basal area was found to be higher in the woodlots, homegardens and crop fields compared to the closed and open forest canopy areas. The stocking density and species abundance was higher in the open and closed forest canopy compared to the rest.

Across all land use categories, the tree structure shows an inverted-J shape curve (Figure 3). The curve slopes are steep to all land use categories except for the woodlot. Two patterns of unusual distributions were noted: 1) diameter class 2 (15 - 24.9 cm) in crop field, woodlot and open forest canopy was found to have higher number of stems exceeding class 1 (5 - 14.9 cm), and 2) higher number of stems for diameter class 10 (>95 cm) for crop field and woodlot exceeded their immediate lower classes.

Correlation among stand parameters and environmental variables varied at significant levels. Species richness and species abundance were negatively correlated to annual precipitation but not stocking density and basal area (Table 2). Species richness, species abundance and stocking were negatively correlated to elevation and temperature, except for basal area. On the other hand, species richness, species abundance, stocking and basal area was found to be positively correlated to slope.

Using closed canopy as baseline land use, comparisons were made against other land uses for species richness, species abundance, stocking and basal area. Results indicated that species richness and species abundance in the crop field, home garden, open canopy forest and woodlot were lower compared to baseline land use as expected. However, basal area in the crop field, homegarden, open canopy forest and woodlot were unusually higher compared to baseline land use. Except for open canopy forest, stocking was lower in the crop field, homegarden and woodlot compared to baseline land use.

The riparian landscape in the LMWE contains higher number of woody plants species, that signifies its ecological relevance. The number of woody plant species

recorded was higher, nearly twice as much compared to similar multiple land use sites in other parts of Tanzania, for instance farmlands on the slopes of Mt. Kilimanjaro [19] [20] . This suggests that the riparian forests in the study site remain an important refuge for woody plant species, that merit adequate conservation attention, but also the higher number can be a result of expansive study area. Within the study site itself, the species richness as indicated by Tukey’s HSD test did not significantly differ across land use types (P < 0.05), though in absolute value it was higher in the homegardens compared to all other land uses (Table 1, Figure 2). Species abundance was high in the forests (closed and open canopy forests) compared to farmlands (homegarden, crop field and woodlot) though with no statistically significant differences. Patterns of species richness were not expected to these types of land uses, as forests are likely to be more stocked compared to other land uses in their proximities [5] . Overall, woody plant species density (Table 1, Figure 2) was within the range observed in other parts of Tanzania, where forest protection status is high and where homegardens has high tree stocks. A mean stocking density range observed of 600 to 900 stem ha⁻¹ has been found in protected areas around the country [21] .

The study speculates that the reason for near equal species richness, abundance and tree density value across the land use types in the study site is due to unbiased disturbances: mainly the extractive use (timber, woodfuel and construction material) and non-extractive use disturbances such as grazing, cultivation and settlement expansion. Homegardens and crop fields were found to have a clear pattern of marked boundaries with trees; a design which ensures planting and retention of large number of trees. The riparian forests seem to have higher recruitment potential of woody plant species owing to the more conducive environment for protection than homegardens, crop fields and woodlots. Riparian forests (closed canopy forests and open canopy forests) cover areas that are flood prone and unsuitable terrain for extensive human activities, hence providing good environment for recruitment of woody plant species. However, being outside of individual ownerships, the riparian forests are susceptible to unregulated extraction of the woody plants compared to farmlands (homegardens, crop fields and woodlots). Collective actions for protection of riparian forest are of utmost importance in the entire LMWE. An integrated land management scheme supported by bylaws and other measures could improve the protection of the riparian forests for sustainable utilization.

The diameter class distribution patterns of woody plant species structure in the study area expressed an inverted J-shaped curve (Figure 3). The riparian forests (closed and open canopy forests) in the study site are semi-natural environment, with less disturbances, hence the stand structure exhibited was expected, as also noted by other studies [22] . Our observation implies that the stand structure in the riparian forests of the current study area is characterised by large number of small-sized trees, with more than 30% of trees with dbh measured below 15 cm. Under natural condition, diameter class exhibit inverted J-shape due to natural tree recruitment, survival and growth [6] . The inverted J-shaped curve explains tree succession path, whereby as trees grows in a natural stand they succumb to selective elimination as a result of competition for resources (i.e., light, water, nutrients) and diseases. High mortality rate is experienced for young trees (seedlings and saplings) and the rate diminish as trees grow in size. Therefore, our observation indicate that the structure of the woody plant species exhibited implies a healthy ecosystem as establishment, recruitment and growth are depicted by higher number of juvenile trees across the five land uses.

Exceptional case was found in the homegarden, crop field and woodlot land use types due to sharp rise of the graph at the diameter class 10 (dbh ≥ 95). This unusual sharp rise is due to high concentration of trees with large diameters. Consistently, the large-sized trees with exceptionally huge diameters have been retained to these land use types owing to their limited use in terms of extractable woody material. The ecological advantage of the large-sized trees in highly disturbed landscapes due to human modifications is to act as a reliable seed source for forest species and connecting forest patches [23] . Farmlands are normally are a result of clearance of forested land to pave way for expansion of agricultural activities and/or infrastructure development leading to dwindling of forest cover [24] . These anthropogenic pressures are considered to be the main driver of biodiversity loss and/or modification of habitats as well as influence the hydrology of landscapes [25] .

Higher basal area in the farmlands (homegardens, crop fields and woodlots) (Table 1, Figure 2) in LMWE depict a common phenomenon noted by other studies in Tanzania [21] , where, farmlands tend to retain large trees for multiple uses. In the LMWE, the higher basal area in the farmlands (homegardens, crop fields and woodlots) was contributed by the presence of large-sized trees mostly being Ficus sycomorus, Ficus sur and Adansonia digitata whose diameters were formidably large, measuring 100 - 600 cm. While exploitation of these tree species is limited due to unsuitability as a woody material, they rather play important ethnobotanical and provision of the non-wood forest products e.g., baobab seed oil and pulp. Additionally, tree of less significance in terms of timber extraction were also dominating the landscape which includes Rauvolfia caffra, Albizia gummifera, Senna spectabilis, Vachellia tortilis and Vachellia nilotica. On the other hand, the lower basal area in the riparian forest (closed canopy forests and open canopy forests) can be explained by growth competition among woody plant species, which restrict adequate diameter increment. Furthermore, close proximity to the rivers makes the riparian forests vulnerable from sand mining and brick making activities: causing both vegetation clearance and firewood extraction for baking; hence removal of trees of certain sizes and general deprival for adequate tree growth in size.

Environmental gradients (slope, elevation, precipitation and climate) tend to influence forest stand properties and results in stand dynamics, composition, recovery and structure [26] . However, the influence of elevation, slope and temperature on stand structure tend to vary in different way on the direction and magnitude of its effects [27] . In the LMWE, there are multiple and compounding environmental and anthropogenic factors that influence land use change like limited land use planning, rapid urbanisation and mushrooming of peri-urban areas/centers. Commercial farming has increased with intensive use of pesticide and industrial fertilizer application that cause pollution and lead to habitat degradation and hydrologic alteration. This observation coincides well with findings from [25] study which examined the effects of land use and environmental gradients on the diversity assemblage in lakes in China.

Species richness, species abundance and stocking density indicated negative correlation with temperature and elevation in the study site (Table 2). Temperature has been reported to have negative relationship with species and abundance, especially by causing water scarcity [28] . The implication of negative relationships caused by temperature is the decline of forest health as only few trees will be able to withstand the higher temperature levels. The LMWE being within the East African Rift Valley, has some areas under semi-arid (dryland) condition, which experience excessive temperature and heat waves, especially during dry season. This dry condition has direct consequence on germination, recruitment and growth of tree species. [29] attributed that high temperature tend to depress tree species as it triggers negative growth responses. Similarly, other studies have further documented that temperature (and other climate change parameters) has affected trees species range [30] . Despite warm temperature to be indispensable for higher species richness and abundance, yet excessive warm conditions become unsuitable altogether as it exceeds tolerable local minimum milder climates [31] .

Basal area increased with slope, precipitation, and land use (Table 2), which reflect the intensity of competition among individual trees whereby large sized ones has potential contribution as result of reduced removal and/or mortality at higher versus lower slopes. This finding is in line with the observation from other studies such as [32] which investigated the influence of temperature and stand basal area interaction on the growth of tree species. The role of basal area in forest management and ecology is closely related to forest stand and volume competition that dictates the health of the tree vegetation [33] . There have been observations across Tanzania, where a general pattern of basal area increases with increasing elevations due to increase of precipitation especially in mountainous areas [34] [35] .

These observations translate that high temperatures lead to sparse distribution of vegetation, while basal area in large sized trees are positively associated with homegardens, crop fields and woodlots. Rainfall variability and slope are primary factors limiting basal area patterns, while temperature, elevation and land use tend to influence the stocking density, species richness and abundance in decreasing ways.