MONITORING FOR SUSTAINABLE INDIGENOUS FOREST MANAGEMENT IN THE GARDEN ROUTE NATIONAL PARK

Knysna

2014 ii

CONTENTS

Page

1 INTRODUCTION 1

2 FOREST DYNAMICS MONITORING 2

2.1 Diepwalle Research Areas 2

2.2 Tsitsikamma strip plots 3

2.3 Permanent Sample Plots (PSPs) in nature reserves 3

2.4 National system of forest plots 3

3 FOREST DISTURBANCE AND RECOVERY 4

3.1 Gap dynamics research 5

3.2 Storms River big 5

3.3 Photo-monitoring of burnt forest 6

3.4 Koomansbos fire gap 7

3.5 Forest establishment 7

3.6 Forest succession on a burnt forest margin 7

4 UTILISATION OF FOREST PRODUCTS 8

4.1 Timber utilization 8 Permanent sample plots (PSPs) 9 Post-harvesting audit 11

4.2 Ferns 12

4.3 Bulbine 13

4.4 Bark 13

5 OF CONSERVATION CONCERN 14

6 BLACKWOOD 15

6.1 Incidence of spread monitoring 15

6.2 Success of control action monitoring 16

6.3 Harkerville blackwood plot 16 iii

7 FAUNA 16

7.1 Antelope population monitoring 16

7.2 Rare mammal monitoring 16

7.3 Crowned eagle monitoring 17

7.4 The Knysna elephants 18

8 CULTURAL HERITAGE RESOURCE MANAGEMENT 19

9 SOCIAL MONITORING 19

9.1 Broad Based Black Economic Empowerment 19

9.2 Employment Equity 19

9.3 People and Conservation Park Based Education and Youth Development Programmes 20

9.4 Expanded Public Works Programmes (EPWP’s) 20

10 WASTE DISPOSAL 20

10.1 Hazardous waste 20

10.2 Household waste 21

11 CHEMICAL USAGE 21

12 COSTS, PRODUCTIVITY AND EFFICIENCY OF FOREST MANAGEMENT 21

13 CONCLUSION 22

APPENDIX 1: HARVEST TREE SELECTION CRITERIA APPLIED IN THE INDIGENOUS FORESTS OF THE GARDEN ROUTE NATIONAL PARK 23

APPENDIX 2: TREE LIST FOR THE INDIGENOUS FORESTS OF THE GARDEN ROUTE 24 1

1 INTRODUCTION

The Garden Route National Park (GRNP) consists of a mosaic of diverse terrestrial, freshwater, estuarine and marine ecosystems, landscapes, and cultural heritage. It lies between George and Kareedouw on the narrow coastal strip to the south of the Outeniqua and Tsitsikamma Mountains, in the Western and Eastern Cape provinces. The approximately 157 000 ha includes scattered patches of indigenous forest that cover about 40 500 ha (Figure 1). Management activities within the forests include the sustainable harvesting of forest products, the provision and maintenance of outdoor recreation opportunities and facilities, and invader plant control. Part of the GRNP (41 538 ha of State Forest land, including 35 765 ha of indigenous forests and 5 339 ha of associated , formerly known as the Farleigh, Diepwalle and Tsitsikamma Forest Estates) received international recognition for responsible management with the awarding of Forest Stewardship Council™ (FSC™) certification (Licence code FSC-C019566) in December 2002, which has been retained since.

A forest monitoring programme, which complements programmes in the fynbos, marine and aquatic environments of the park, was developed over more than four decades as an integral part of the management systems to provide information on:  natural changes occurring in the ecosystems,  effects of management activities on the ecosystems, and  effectiveness of management activities.

The monitoring results are used to change or refine the management systems to ensure that the valuable natural resources are managed sustainably, based on reliable scientific data. Several of the projects in the Garden Route were established for long term monitoring, i.e. to gather and provide information for several years, and in many cases, for several decades. This is important because of the slow rates of natural change in the forests, the long periods between management interventions for some activities (e.g. the 10-year felling cycle for timber) and the relatively light impacts of most of the management activities. Some low impact changes may only be detected after several monitoring events, i.e. after several decades. The data emanating from these projects can provide valuable information on the impacts of climate change on the forests over the next few decades.

This purpose of this document is to report mainly on the results of the forest monitoring programme; however some of these results are not restricted to the forests, and cover other terrestrial habitats as well, or even the full extent of the park, reflecting the integrated nature of the management systems and monitoring programmes.

Figure 1: The distribution of indigenous forests managed by SANParks in the Garden Route. 2

2 FOREST DYNAMICS MONITORING

The forest is monitored to observe natural processes, such as long-term changes in the composition of the forest, growth rates, regeneration, mortality and condition of the forest. Several projects are currently underway in various parts of the forest.

2.1 Diepwalle Research Areas

The Diepwalle Research Areas were established during the 1930s. During the early 1970s all with a diameter at breast height (DBH, diameter measured at a height of 1.3m) of ten centimetres and greater, as well as many smaller trees, were numbered and measured. Areas covering a total of 67.7ha have been re-measured periodically since 1972, most recently in 2007 and 2010. More than 50 000 trees are individually numbered in these areas (see Figure 2). This project provides a substantial database on the rates of change of Garden Route forests. The data on increments (growth rates), ingrowth and mortality rates for different tree species and size classes on a variety of different sites have also provided an important basis for the development of a timber yield regulation system for the region. Some of the results for the main canopy species are presented in Table 1.

Table 1: Some results of forest dynamics monitoring in the Diepwalle Research Areas. Species Percentage Mean annual 10 year composition diameter mortality increment percentage (mm) Stinkwood / Stinkhout ( bullata) 2.2 1.496 8.1 Real Yellowwood / Opregte Geelhout (Podocarpus 26.2 1.255 3.2 latifolius) / Ysterhout ( capensis subsp.macrocarpa) 42.6 2.053 8.2 Hard Pear / Hardepeer ( ventosa) 3.1 4.745 3.6 White Pear / Witpeer (Apodytes dimidiata 5.8 0.990 5.2 subsp.dimidiata) Cherrywood / Kershout (Pterocelastrus tricuspidatus) 6.6 1.983 5.0 Assegai / Assegaai (Curtisia dentata) 3.6 1.398 7.1 Quar / Kwar (Psydrax obovata subsp.obovata) 4.6 1.516 9.3 Total / Mean 94.7 6.4 Note: Data for trees with DBH ≥ 30 cm.

A tree senility monitoring project was initiated in October 1990 to monitor species-specific mortality patterns. It is an integral part of the development and implementation of the senility criteria harvesting (SCH) timber yield regulation system, which is applied to select trees for harvesting. A total of 2420 canopy trees of 18 species were inspected for possible visible indications of senility. A set of harvest tree selection criteria was developed for the 8 most common canopy tree species (Yellowwood, Stinkwood, Ironwood, White Pear, Candlewood, Assegai, Quar and Hard Pear) that were calibrated to the known species-specific mortality rates. The selection of trees falling within these selection criteria should produce a harvest equal to the natural mortality. All of the trees were re-evaluated after about 5, 10, 15 and 20 years and the criteria refined. The criteria currently applied to select indigenous trees for harvesting appear in Appendix 1. Preliminary analyses of the data provided information on mortality patterns that support the senility criteria approach to timber yield regulation. The results also revealed the need for further refinement of the harvest tree selection criteria to increase the accuracy of the system. Analysis of the most recent data from the Diepwalle and other research areas in the region will provide further insights into the natural dynamics of the forest ecosystem that will be used to improve the management systems.

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Figure 2: Monitoring of forest dynamics in the Garden Route forests.

2.2 Tsitsikamma strip plots

Strip plots (transects) were established in two areas in the Tsitsikamma (eastern section of the Garden Route forests) during the period 1988 - 1992 to provide data for these forests, as it was not known if the data from the Diepwalle and other research areas to the west were representative for the Tsitsikamma forests. The strip plots are permanently marked 10m wide transects through the forest, divided into plots 20m long. The 1135 plots cover a total area of 22.7ha. All trees with DBH  10cm were measured. Each tree is individually identifiable, so re-measurements provided data on increments, ingrowth and mortality rates. Table 2 provides a summary of the species and size class composition and increments recorded. The population of the Tsitsikamma forest remained relatively stable in terms of stem density, mean diameter and basal area. There appear to be some differences in growth rates and forest structure between the Tsitsikamma forests and forests further west; on-going analysis of the monitoring data will clarify matters.

2.3 Permanent Sample Plots (PSPs) in nature reserves

No harvesting of forest products is permitted in certain parts of the Garden Route forests. These undisturbed areas can be compared with similar areas where harvesting is carried out to assess the impacts of harvesting. In 1985 and 1991 PSPs were established in Lelievlei and Petrus Brand Nature Reserves (108 plots and 30 plots respectively) in sites similar to those used for sustainable timber harvesting. This forms part of the larger PSP monitoring project in timber utilisation areas that is discussed in more detail below.

2.4 National system of forest plots

Permanent plots at Groenkop (established in 1972), Diepwalle (1974), Koomansbos (1988) and Witelsbos (1988) are part of a national system of plots established for long-term monitoring of growth and mortality in indigenous forests. Similar plots were established at sites in the Cape Peninsula, Eastern Cape, KwaZulu-Natal and Limpopo Province. These plots are re-measured every 5 or 10 years and provide data on tree species composition, growth, mortality and recruitment on a range of different sites.

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Table 2: Summary of Tsitsikamma strip plot data Species Stems per Stems per Mean diameter hectare hectare increment for ≥ 10cm ≥ 30cm stems ≥ 10cm diameter diameter (mm/a) Assegai / Assegaai (Curtisia dentata) 37.49 15.20 1.182 Cape Beech / Boekenhout () 5.99 1.94 2.484 Bladder nut / Bostolbos ( whyteana) 12.82 0.13 0.436 False Ironwood / Basterysterhout (Olea capensis subsp.capensis) 11.41 0.53 0.479 Real Yellowwood / Opregte Geelhout (Podocarpus latifolius) 85.15 22.69 1.503 Hard Pear / Hardepeer (Olinia ventosa) 0.93 0.75 5.310 Outeniqua Yellowwood / Kalander (Podocarpus falcatus) 12.29 3.44 2.202 Kamassi / Kamassie (Gonioma kamassi) 80.22 1.59 0.821 Rock Alder / Klipels (Canthium mundianum) 13.39 0.18 0.756 Cherrywood / Kershout (Pterocelastrus tricuspidatus) 66.30 22.47 1.284 Quar / Kwar (Psydrax obovata subsp.obovata) 29.25 10.18 0.811 Malabar Tree / Malbaar ( glabra) 10.88 3.70 2.832 Tree Fuchsia / Notsung (Halleria lucida) 11.72 0.70 0.591 Common Saffron / Gewone Saffraan (Elaeodendron croceum) 16.74 2.64 0.741 Stinkwood / Stinkhout (Ocotea bullata) 26.04 12.11 1.450 Cape Blackwood / Kaapse Swarthout ( peduncularis) 13.17 2.11 0.869 White Silky Bark / Witsybas (Robsonodendron eucleiforme) 20.88 1.45 0.938 Forest Elder / Bosvlier (Nuxia floribunda) 36.92 8.68 0.728 White Alder / Witels (Platylophus trifoliatus) 33.22 15.77 1.864 Wild Pomegranate/ Wildegranaat (Burchellia bubalina) 16.17 0.04 0.503 Cape / Without (Ilex mitis) 17.00 7.09 1.924 White Pear / Witpeer (Apodytes dimidiata subsp.dimidiata) 59.65 24.54 0.912 Ironwood / Ysterhout (Olea capensis subsp.macrocarpa) 76.12 37.09 1.317 Other spp. 9.51 2.46 1.500 TOTAL: All Species 703.39 197.53 1.184 Note: Data from the first re-measurement (1993 - 1997): 1135 plots (22.7 ha)

3 FOREST DISTURBANCE AND RECOVERY

Disturbance plays an important role in the ecology of natural forests, affecting habitat diversity, the regeneration of forest species and biodiversity. Natural forests in the Garden Route generally have a closed canopy, formed by the overlapping crowns of adjacent trees. However, when trees die standing or fall over due to strong winds or other disturbances, gaps are formed in the forest canopy (Figure 3). This allows more light to penetrate to the forest floor. Trees growing next to a gap can expand their crowns into the gap. Seedlings, saplings and small trees growing in the gap grow taller, competing to occupy the available space in the forest canopy. Different species have different requirements for regeneration, so factors such as type and intensity of disturbance and gap size can have a profound effect on the regeneration of forest species. The sustained-use management of forests needs to recognise the regeneration strategies of tree species in relation to gap size in order to maintain species 5 diversity patterns and regeneration processes. The current timber harvesting system practised in the Garden Route forests attempts to minimise gap size. This practice may benefit the more shade-tolerant species and inhibit the regeneration of the less shade-tolerant species. It is therefore necessary to assess the effects of different types of disturbance and gap sizes on the regeneration of forest species.

Figure 3: Canopy gap caused by the death of a tree.

Fire affects the distribution and shape of forest patches and maintains the fynbos-forest boundary. Fires burning in neighbouring fynbos vegetation or commercial timber plantations usually affect the forest edge but only occasionally penetrate the forest interior. However, more extensive disturbance may occur where a natural forest-fynbos ecotone is absent or disturbed.

3.1 Gap dynamics research

Research was initiated in 1995 to assess the influence of gap size on regeneration patterns of forest species. Gaps of different sizes were created in the forest at Diepwalle and Lottering. Seedlings and saplings occurring in the gaps and adjacent forest were counted and measured. The project was extended in 1997 to include the effects of gap size on the stem diameter growth and lateral crown expansion of the gap edge trees. The experiment was re-measured during February 1998, approximately two years after gap creation. At that time no clear patterns had emerged. Very few seedlings in the gaps had developed into saplings. It seems that gaps in the Garden Route forests are usually colonised by existing saplings already present in the understory when the gaps are created. Alternatively, surrounding canopy trees spread their crowns into gaps and may even close smaller gaps. The Lottering gaps established in 1995 were re-measured during 2002/3. Smaller gaps had fewer plant species than larger gaps. Re-measurement during 2013, almost 18 years after gap creation, showed slow recovery and considerable variation in regeneration, that will be assessed further during data analysis. Some gaps were occupied by alien tree species that do not usually regenerate under a closed forest canopy.

3.2 Storms River big tree

On 31 December 1994 one of the "Big Trees" at Plaatbos, Storms River collapsed. The large Outeniqua yellowwood (Podocarpus falcatus) had been leaning for many decades and, weakened by internal stem decay, finally snapped off at a height of about 3 metres. This created a large gap in the forest canopy that adjoined another gap formed a few years earlier by a series of windfalls. During 1995 all trees and regeneration found in the gap were numbered, measured and their position plotted. A diagram of the gap is shown in Figure 4. The gap was re-measured during 2002/3 and again during 2010. 6

The disintegrating yellowwood crown produced a dense mat of debris over large parts of the gap that has hindered growth of tree seedlings. The dense undergrowth, consisting mainly of Hypolepis ferns that colonised the gap soon after it was formed, has also hindered regeneration. Several of the saplings that occur in the gap are growing rapidly to try to occupy a space in the forest canopy.

Figure 4: Diagram of the Storms River big tree canopy gap with the remains of the fallen tree in the background.

3.3 Photo-monitoring of burnt forest

Fire is a natural feature of the fynbos vegetation that occurs in the Garden Route. The indigenous forests are generally fairly resistant to fire, especially if the natural forest margins are intact and free of exotic vegetation. However, in extreme conditions fires can spread into the indigenous forests. This occurred in April 1998 in the Whiskey Creek Nature Reserve, to the north of Plettenberg Bay. A photo-monitoring project was established to provide information on the recovery of these burnt forest areas. Photographs are taken periodically from fixed points, showing how the vegetation develops over time, and records kept of observations.

Many trees survived in areas where the fire intensity was fairly low, even though the undergrowth was largely destroyed. In the areas where the fire was most intense all of the above-ground vegetation was killed. Some of the trees have coppiced from their roots or lower parts of the stems, but the growth of these coppice shoots has generally been slow. The soil-stored of the blossom tree, or keurboom (Virgilia divaricata) germinated profusely in areas where the fire was intense and it is now the most dominant component of the vegetation. A number of exotic and indigenous herbaceous and woody weeds have become established in the burnt areas. At Whiskey Creek two succession paths have been distinguished. In some areas seedlings of the pioneer tree species Virgilia divaricata germinated 6-7 months after the fire, in a one-off event, and have grown to maturity with few other species recruited thereafter. Some dieback and thinning of crowns were to be seen 11 years after the fire. In other areas herbaceous and / or bracken fern (Pteridium aquilinum) dominate with few woody and trees becoming established.

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3.4 Koomansbos fire gap

A ground fire burnt about one hectare of indigenous forest at Koomansbos in the Tsitsikamma during 1989. The area was surveyed in May 1990 and again in September 1992. The fire caused the death of most of the trees, saplings and seedlings and also destroyed the entire soil stored bank and much of the humus layer of the soil. The burnt area was initially colonised by a dense stand of bracken fern (Pteridium aquilinum) that was effectively choking forest regeneration. The regeneration of the forest is expected to be slow. The 20-year re- measurement in 2009 revealed definite changes in the vegetation – thinning of bracken and more forest tree regeneration. Trees recruited successfully into larger size-classes in the gap. The species composition differed between the forest gap and the neighbouring closed forest. Further monitoring should provide interesting data on forest recovery after fire.

3.5 Forest establishment

The Diepwalle arboretum was established in 1926 on a site where natural forest had been destroyed by fire some 60 years previously. Trees of several species, mainly species occurring naturally in the southern Cape forests, were planted in plots that had been cleared of all trees. Different treatments were applied over a period of several decades. The trees were re-measured at various times, most recently in 2013. The trees have grown very slowly and 60 years after establishment the surviving trees had an average diameter of less than 25cm.

3.6 Forest succession on a burnt forest margin

During 2005 a lightning fire burnt large areas of fynbos and commercial timber plantations in the Tsitsikamma. In places it burnt some distance beyond the natural forest margin into the forest interior (Figure 5a). Plots were established in the burnt forest margins in 2006. The fire had a severe impact on the forest vegetation with high tree mortality and slow recovery. A dense stand of keur (Virgilia divaricata) established on the forest margin to form a nurse stand for the regeneration of climax species. A dense stand of bracken fern (Pteridium aquilinum) suppressed regeneration of forest canopy species in the burnt forest interior areas (Figure 5b). The process of forest regrowth is slow, and it will take many decades for the re-establishment of climax forest. A natural fynbos-forest ecotone is essential to protect the forest from extreme fire damage. Appropriate fire management in neighbouring fynbos and invader plant control on forest margins are important. This is a major challenge in many parts of the Garden Route due to the fragmented nature of the park and land-use practices such as commercial timber plantations in areas bordering natural forests.

a b

Figure 5: Burnt forest margin in (a) 2005, and (b) 2014. 8

4 UTILISATION OF FOREST PRODUCTS

A number of natural resources are harvested from the indigenous forests of the Garden Route. Timber has traditionally been the most important product harvested. The fronds of the seven week fern (Rumohra adiantiformis) have been harvested commercially since the early 1980s and some other fern species have attracted interest during the last few years. There has also been increased interest in the harvesting of medicinal in recent years, although very little is currently harvested.

Long term monitoring of yields, growth rates and regeneration is important to ensure that harvest levels and mixes of products are sustainable. Monitoring provides information vital for ensuring that forest products are harvested sustainably:  Information on the natural rates of change of resources provides the basis for determining sustainable harvest levels.  Information on the response of the resource to harvesting may indicate that adjustments in the rate and method of harvesting are necessary.  Monitoring is carried out to ensure that harvesters are adhering to prescribed harvest levels and other conditions and restrictions put in place to protect the resource.

4.1 Timber utilization

Indigenous timber is harvested from about 600 - 650 ha of forest every year, with harvesting carried out in a particular area only once every 10 years. Individual canopy trees that contain sufficient utilisable timber may be selected for harvesting by experienced markers if they fall within senility selection criteria (see Appendix 1). The application of these criteria should result in the harvesting of dying trees, equivalent to the natural mortality rates. However, due to market constraints not all of the candidate trees of some species are harvested. Specialised methods and equipment are applied during harvesting to limit damage to the forest. The gross incomes from timber sales during the thirteen years 1998 – 2010 are shown in Table 3 and quantities of timber of different species harvested and sold are shown in Table 4. The exotic Australian blackwood (Acacia melanoxylon) contributes significantly to the total volume of timber harvested from the forests and the income earned annually. Timber harvesting was suspended in 2010 and resumed in 2013 following the appointment of a private harvesting concessionaire.

Table 3: Gross income from timber sold from the indigenous forests of the Garden Route: 1998 – 2010 Gross Income (Rand) YEAR Indigenous Blackwood TOTAL 1998 1,425,563.10 1,470,791.80 2,896,354.90 1999 1,321,727.20 922,553.20 2,244,280.40 2000 1,114,473.32 1,125,880.94 2,240,354.26 2001 1,906,961.36 865,064.60 2,772,025.96 2002 1,956,193.99 2,319,366.50 4,275,560.49 2003 2,099,889.41 1,825,958.10 3,925,847.51 2004 874,386.00 1,208,491.00 2,082,877.00 2005 1,035,447.71 1,210,010.00 2,245,457.71 2006 1,674,575.51 1,221,074.50 2,895,650.01 2007 2,332,949.43 1,871,476.50 4,204,425.93 2008 1,286,480.51 1,223,349.50 2,509,830.01 2009 1,262,190.28 1,016,185.40 2,278,375.68 20101 583,452.50 570,705.00 1,154,157.50 Note1: Only 1 auction was held in 2010 before harvesting was suspended.

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The effects of timber harvesting are monitored in timber utilisation areas by means of permanent sample plots and post-harvest audits.

Permanent sample plots (PSPs)

During the mid to late 1980s a total of 829 PSPs were established in selected timber utilization areas, with another 138 in similar areas in nature reserves where no harvesting takes place. A total of 70 compartments, scattered throughout the GRNP, contain PSPs.

Within the harvestable parts of the compartments 400m2 circular plots are laid out in a grid pattern and all trees in the plots with DBH  10cm are measured at a fixed point of measurement. The PSPs provide area-specific information on the species and size class composition. Re-measurements are carried out every ten years, providing data on increments, mortality rates and ingrowth rates for each species and size class. All of the PSPs have been re-measured at least twice since establishment. The next cycle, the 30 year re-measurement, commences in 2014.

The species composition for the sampled areas in the Garden Route is shown in Figure 6 (stems with DBH  10cm) and Figure 7 (stems with DBH  30cm) and the diameter increments in Figure 8 (the tree species and their abbreviations are listed in Appendix 2). There are differences in the relative abundance of species and in the diameter increments between the Southern Cape (western areas) and the Tsitsikamma (eastern areas). Ironwood (YH, Olea capensis subsp. macrocarpa) is the most common species in the southern Cape, with common yellowwood (Geel, Podocarpus latifolius) the second most common. The same pattern holds for the larger size classes In the Tsitsikamma (see Figure 7). However, if all size classes are considered (see Figure 6) the common yellowwood is the most common with ironwood in third place after cherrywood (Kers, Pterocelastrus tricuspidatus). White alder (WE, Platylophus trifoliatus) are a lot more common in the areas sampled in the Tsitsikamma. The mean annual diameter growth rate for all species is 1.091mm, but Figure 8 clearly shows that different species have different growth rates. The stand-level increment of species in the canopy layer (>30cm dbh) is significantly determined by inherent species-specific growth capacities (i.e. species composition of the stand), water availability, forest matrix crowding and age-related deterioration of tree condition. In contrast, stand-level increment of trees of canopy species in the subcanopy layer (10–20cm dbh) is prominently shaped by light availability, as mainly determined by the degree of canopy-level disturbance (due to the mortality of trees >30cm dbh), crowding (canopy-level overhead and forest matrix crowding) and proximity to adults of the same species (within 6–8 m). In addition to species-inherent and resource factors, considerable variation in stand-level growth resulted from site–climate interactions. Forest structure, as described in terms of stem densities and tree size, is largely controlled by resource conditions (moisture and nutrient availabilities) and the degree of resource-level fluctuations, i.e. seasonality. The moist, less seasonal Tsitsikamma forests have relatively high densities of subcanopy trees and comparatively high stem densities of relatively large-sized trees. The cooler, moist and more seasonal Knysna forests have lower densities of relatively large-sized trees at the canopy level, attributed to the lateral growth mode and extended persistence of the largest trees. The warm, seasonal Outeniqua forests, on relatively nutrient- rich soils at the western edge of the GRNP, have high stem densities at the canopy level relative to the subcanopy stratum, attributed to a combination of low subcanopy tree persistence, fast ingrowth of trees into the canopy stratum, and high canopy tree turnover, with trees lost to mortality before they reached large sizes.

10 Table 4: Timber volumes (m3) harvested and sold in the indigenous forests of the Garden Route: 1998 – 2010 TIMBER VOLUMES SOLD(m3): 1998 - 2010 SPECIES YEAR 1998 1999 2000 2001 2002 2003 2004 2005 2006 2007 2008 2009 2010 Stinkwood / Stinkhout (Ocotea bullata) 260.00 72.30 165.28 51.82 180.60 192.91 68.72 88.76 164.92 264.03 105.92 80.31 27.42 Real Yellowwood / Opregte Geelhout (Podocarpus latifolius) 848.00 715.40 384.99 789.93 445.22 456.83 335.28 254.91 446.23 660.89 611.66 493.46 118.41 Outeniqua Yellowwood / Kalander (Podocarpus falcatus) 32.80 27.70 44.05 25.44 5.44 49.04 84.91 31.51 48.30 64.26 53.24 51.31 30.38 White Alder / Witels (Platylophus trifoliatus) 132.60 87.30 40.69 99.96 119.57 146.95 125.13 130.05 73.55 65.61 49.81 12.95 2.80 Ironwood / Ysterhout (Olea capensis subsp.macrocarpa) 313.00 650.20 45.66 205.36 169.15 294.03 197.04 78.44 213.51 202.45 132.56 169.79 42.94 Hard Pear / Hardepeer (Olinia ventosa) 124.20 137.60 108.45 39.35 76.79 136.33 53.75 76.45 41.42 126.29 42.11 70.54 42.44 Cape Beech / Boekenhout (Rapanea melanophloeos) 20.50 40.70 23.09 23.14 15.19 82.14 34.14 30.24 36.91 70.09 14.17 71.66 11.59 Cape Ash / Essenhout (Ekebergia capensis) 0.30 0.50 1.12 2.49 0.50 1.18 1.34 1.42 2.57 2.63 Cape Holly / Without (Ilex mitis) 29.50 31.00 8.25 15.97 11.39 21.73 17.36 4.33 31.35 18.27 1.58 16.52 White Pear / Witpeer (Apodytes dimidiata subsp.dimidiata) 93.90 184.00 23.20 82.13 51.37 88.42 41.85 33.93 45.84 60.66 32.18 62.96 15.82 Forest Elder / Bosvlier (Nuxia floribunda) 16.80 20.20 6.44 4.54 6.18 12.31 0.82 7.29 14.31 4.21 1.82 1.66 Cherrywood / Kershout (Pterocelastrus tricuspidatus) 36.10 78.50 35.27 29.88 14.89 51.23 24.22 16.46 40.19 55.59 29.56 50.00 15.88 Assegai / Assegaai (Curtisia dentata) 28.50 26.80 12.68 24.00 17.59 18.28 15.00 12.41 12.38 23.70 13.14 20.82 6.59 Common Saffron / Gewone Saffraan (Elaeodendron croceum) 6.90 3.90 0.21 2.14 0.30 0.66 1.01 0.22 0.39 0.45 0.44 0.60 Cape Blackwood / Kaapse Swarthout (Maytenus peduncularis) 7.00 3.10 2.14 2.37 0.98 3.95 0.81 2.57 3.60 2.03 White Silky Bark / Witsybas (Robsonodendron eucleiforme) 2.80 3.60 0.56 0.79 0.43 0.34 0.16 0.76 0.36 0.53 Rock Alder / Klipels (Canthium mundianum) 0.80 0.10 3.28 0.51 Wild Peach / Vaderlandsrooihout (Kiggelaria africana) 2.40 3.80 0.17 0.42 2.07 1.25 4.44 0.53 Blossom Tree / Keurboom (Virgilia oroboides subsp.ferruginea) 1.70 0.64 0.41 1.07 0.32 Kamassi / Kamassie (Gonioma kamassi) 2.80 7.60 1.46 4.25 2.14 1.74 0.54 0.84 0.11 3.54 0.58 1.69 Red Alder / Rooiels (Cunonia capensis) 5.30 6.30 1.40 3.11 0.83 12.69 4.94 6.49 3.51 Red Currant / Bostaaibos (Rhus chirendensis) 0.50 0.70 Quar / Kwar (Psydrax obovata subsp.obovata) 8.00 26.70 1.92 4.25 2.18 4.53 1.77 4.81 5.60 5.85 4.40 1.37 Red Pear / Rooipeer (Scolopia mundii) 0.50 0.60 0.83 0.86 2.57 2.77 False Cabbage Tree / Basterkiepersol (Schefflera umbellifera) 0.70 0.56 Knobwood / Perdepram (Zanthoxylum davyi) 0.70 1.30 White Ironwood / Witysterhout (Vepris lanceolata) 0.66 0.85 Malabar Tree / Malbaar (Brachylaena glabra) 12.30 0.56 0.46 3.18 0.54 0.70 1.31 3.51 0.48 Cheesewood / Witboekenhout (Pittosporum viridiflorum) 0.52 Common Turkey-berry / Bokdrol (Canthium inerme) 0.85 White Stinkwood / Witstinkhout () 1.00 0.15 TOTAL (Indigenous species) 1988.90 2129.30 907.42 1410.07 1123.18 1576.10 1016.49 770.26 1171.38 1650.73 1110.10 1115.59 320.15 Australian Blackwood (Acacia melanoxylon) 1601.50 1414.80 1365.75 918.16 1416.23 1706.75 917.33 552.59 885.16 1127.97 1021.38 991.68 377.14 Oak (Quercus spp.) 3.10 6.93 4.94 Match Poplar 5.12 Californian Redwood (Sequoia sempervirens) 1.40 0.79 4.83 2.28 Camphor / Kamfer (Cinnamomum camphora) 26.20 TOTAL VOLUME (All species) 3590.40 3570.30 2273.17 2328.23 2542.51 3289.37 1933.82 1323.64 2061.37 2780.98 2138.41 2112.21 697.29 11

160.00

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V N YH Saf Kw SH Sw KE Kal Sy BH HP Geel Kers Kam Ass WP WE Btol WG BYH WH

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Figure 6: Tree species distribution in PSPs (Stems per ha with DBH  10cm)

60.00

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V N YH Saf Kw SH Sw KE Kal Sy BH HP Geel Kers Kam Ass WP WE Btol WG BYH WH

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Figure 7: Tree species distribution in PSPs (Stems per ha with DBH  30cm)

4.500

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2.000 Total Increment 1.500

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Figure 8: Diameter increment (mm/a) for all trees with DBH  10cm in PSPs.

Post-harvesting audit

Harvesting and extraction operations have the greatest potential for environmental damage of any forest operation. Post-harvesting audits were introduced in the Garden Route forests for the first time in 2002 to identify any obvious environmental impacts caused by harvesting, including damage to remaining trees, erosion, disruption of drainage patterns, harvesting in environmentally sensitive areas and chemical pollution. This should lead to the timely implementation of corrective actions. Harvesting impacts currently appear to be at acceptable levels. The audits have focussed attention on methods and procedures applied during harvesting, resulting in improved practices. 12

4.2 Ferns

The seven-weeks fern (Rumohra adiantiformis) occurs in forests throughout South . It has been harvested from the indigenous forests of the Garden Route since 1982. The fronds are used extensively in arrangements because of their long cut-life. When harvesting first began very little information was available on the ecology, phenology or response of Rumohra to harvesting. This lack of knowledge led to over-exploitation. Research soon showed that Rumohra is adapted to a nutrient-poor environment with associated life history characteristics. These include the slow production of long-lived, unpalatable leaves with a low photosynthetic efficiency, inability to compensate adequately for partial defoliation and slow or even sporadic recruitment. Rumohra responds to harvesting by producing smaller fronds and less sori while total defoliation can lead to mortality. These research findings were used to change the harvesting system for Rumohra. Initially total defoliation of all merchantable fronds was allowed on a five-week rotation. In contrast, the current harvesting system ensures that a certain percentage of the population will always escape harvesting. Only 50% of all the pickable fronds (length  25cm and insect or other damage  10% of the frond area) per plant may be harvested. This means that plants with only one pickable frond will escape harvesting, and that only one frond can be removed where a plant has two or three pickable fronds. The harvesting cycle was also extended to 15 months to give the plants adequate time to recover and to stagger harvesting time.

Various goal-orientated monitoring projects were initiated in the Garden Route. They include monitoring in nature reserves to gather baseline data on natural fern growth and population development, and monitoring in picking areas to assess harvest impact on the resource.

Analyses of monitoring results produced the following findings:  The current harvest prescriptions are scientifically sound and provide for the sustainable harvesting of the species.  There was general decline in the resource use potential of fern populations in harvest areas, based on variables such as the number of plants with pickable fronds, plants with only one pickable frond, etc.,.  Fern yield declined significantly over harvest cycles. There was a gradual increase in the length of harvested frond, but not significantly so.  The decline in resource use potential was also recorded in nature reserves never subjected to harvesting. The decline in harvest areas can therefore not be attributed to over-harvesting, but rather a natural long-term change synchronised with natural disturbance patterns and forest succession. Considering the widespread decline in the resource, other natural drivers of change could also be in play.  The species are thus dynamic with long-term spatio-temporal variation in population structure and productivity. This needs to be taken into consideration when defining harvest areas.  Phenology monitoring, in which individual plants were monitored monthly over a 5½ year period, provided detailed information on the life-cycle of Rumohra, including the number of fronds produced annually, the length of time that fronds remain pickable, seasons when the ferns are most sensitive to disturbance, etc.

Forest guards accompany fern pickers on a daily basis when picking occurs. Their main tasks are to:  make sure that fern pickers stay within the fern picking area / compartment;  record the number of fronds picked, per area per day;  make sure that the fern pickers stay within the prescribed harvesting intensities; and  monitor the length of fronds and the presence of spores on sample of the picked and remaining pickable fronds.

There is currently no fern harvesting taking place, but long-term monitoring continues. 13

4.3 Bulbine

Bulbine latifolia is a succulent plant species that occurs along the southern and eastern coasts of (Figure 9). It is harvested and sold for its medicinal qualities by the Rastafarian community from the Knysna area and is used for stomach and renal ailments as well as an aphrodisiac. It was harvested illegally in the Sinclair Nature Reserve at Harkerville. Discussions were held with representatives of the Rastafarian community and they expressed interest in the continued utilisation of the species on SANParks land.

Little was known about the ecology of this plant. A project was carried out from 2003 to 2011 to investigate the potential for the sustainable harvesting of B. latifolia on SANParks land and to develop harvest prescriptions for the species. Research and monitoring produced the following results:  The species are primarily found in dry and very dry scrub forest and is most abundant on the fynbos / forest edge. It has a limited distribution in the SANParks areas.  The population has a skewed bell-shaped size class distribution with only a small percentage of plants larger than 2.5 cm in diameter. Regeneration and recruitment is complex and differs between fynbos / forest ecotone and scrub populations.  Plants are slow-growing with a corm diameter growth of less than 1 mm per annum.  Plants are the most sensitive to harvesting during the period July – November when buds, and seeds are produced.

Considering the habitat specificity of the species, slow growth and the fact that most of the harvestable populations fall outside the area zoned for resource use in the Garden Route National Park, it is unlikely that the demand could be met from wild populations. Alternatives such as the establishment of the species in medicinal plant gardens are currently being explored, with plants cultivated from seed in the Diepwalle nursery made available to the community.

Figure 9: Bulbine monitoring. Figure 10: Bark monitoring.

4.4 Bark

The bark of various indigenous tree species is used in traditional medicines. In some parts of the country bark stripping is carried out on a large scale, often resulting in the death of the trees. The bark harvesting monitoring project was established in the Garden Route forests 14 during 2001 and is of relevance to the sustainable harvesting and management of medicinal bark species. The objective is to assess, through experimental harvesting, the response of different species to bark stripping. Three species were initially selected for this study, viz. Ocotea bullata, Curtisia dentata and Rapanea melanophloeos, and expanded to Ilex mitis, chirindensis and Prunus africana in 2003. Different treatments are applied to assess the effects of the season of harvest, size of tree, width of bark strip removed and the use of wound sealer 9Figure 10). Data recorded during annual assessments are extent and rate of bark regrowth, damage through fungal and insect damage, etc.

The monitoring produced the following results:  There is a differential response of species in terms of extent and rate of bark regrowth, as well as susceptibility to fungal and insect attack following bark stripping.  Although some bark regrowth was recorded for Curtisia dentata, Ilex mitis, and Searsia chirindensis, only Ocotea bullata and Prunus africana showed sufficient regrowth through phelogen edge and/or sheet development to allow for sustainable strip harvesting.  Little bark regrowth was recorded for Rapanea melanophloeos. The species is also the most susceptible to fungal and insect damage.  The response of trees and tree species to season of bark stripping varied. For C. dentata, O. bullata and P. africana, the dry season treatment resulted in significant faster bark regrowth through edge development. For C. dentata and P. africana, sheet development was significantly better following rainy season treatment. The variety of environmental and other factors that influence the response of trees when debarked during different season, however, do not allow for easy interpretation of experimental results that could influence harvest prescriptions.  The occurrence of edge or sheet growth is not affected by strip width as such, but strip width could affect the rate of wound closure. Significantly better sheet and edge development was recorded for bigger trees, while a higher incidence of tree die-back was recorded for smaller trees following bark stripping. Smaller trees with a wide strip width are more severely affected than larger trees with a narrow strip width. A minimum tree diameter and maximum strip width should thus be set for bark harvesting.  Various harvest options to meet the demand for medicinal bark have been formulated for the different species.

Further studies are investigating the incidence and extent of stem decay associated with bark stripping.

5 PLANT SPECIES OF CONSERVATION CONCERN

Species of Conservation Concern (SCC) are those that are important for South Africa’s conservation decision-making processes. Several SCC occur in the Garden Route National Park and its immediate surrounds. The reasons for their status vary.

Species lists and status are continually updated as species are found and identified in the Park area. New species (to ) may either be collected from the field during routine herbarium collections, formal vegetation surveys, or by the Custodians of Rare and Endangered Wildflowers (CREW). CREW is a volunteer group that monitors rare plant species. CREW works under the auspices of SANBI and has a program whereby species are searched for in their flowering months and various aspects about the species’ ecology are recorded. Monitoring consists of searching for, or visiting known populations of threatened plants to ascertain their distribution, abundance and performance. The data feed into SANBI’s Red List assessments but are also recorded in the local SANParks GIS and plant species list, adding to this project.

All SCC were individually evaluated to determine the priority for routine monitoring by SANParks personnel. A pragmatic approach was followed. Species are prioritized into those 15 that need monitoring and are accessible. All occurrences are recorded in the GIS database. Possible locations for SCC are determined by working out the vegetation type and habitat. Where such habitat is located on GRNP land and if it is a it is searched for during the flowering season. When a species is found the habitat and potential threats are assessed. This knowledge makes it possible to leverage management action and allows monitoring planning, e.g. post fire monitoring (a second type of monitoring), to determine regeneration success or if a species is not well adapted to fire, if it survived. Some species may demand more detailed monitoring, especially when the species’ dynamics are poorly understood, the populations are very small or its Red List status is high. Three orchid species are currently monitored to better understand their population dynamics. The seedlings of Prunus africana, a forest tree, are currently monitored to get insight into poor recruitment.

Approximately 116 plant species from the GRNP have IUCN Red List status. The increase of 26 species since 2009 is due to effort in collection and identification of species, not increased threats. During the same period several species were removed from the GRNP species list, mainly due to earlier incorrect identification or reclassification of their Red List status. While forest species contribute 28% of the GRNP plant species list and fynbos 49%, the SCC list contribution from the two vegetation types are 14% and 80% respectively.

Two new projects are envisaged to start late 2014. Bark stripping incidences will be recorded to measure possible increase in this threat and forest tree SCC’s numbers will be analyzed to track any decrease in numbers.

6 BLACKWOOD

Acacia melanoxylon (Australian Blackwood) is an alien species introduced to the Garden Route in 1856. It is now well established in the natural forests and surrounding open areas and has become an important timber tree in the region (refer to Table 4 to see the volumes of blackwood timber harvested annually). A comprehensive management plan for blackwood was compiled and a monitoring programme established to ensure a conclusive knowledge base for sound decision making on aspects of blackwood control and utilisation. During 2014 an evaluation of monitoring results provided support for a review of the blackwood policy, with greater emphasis on effective control of the species. The blackwood monitoring programme, comprising the following projects, will be re-evaluated as part of this review process.

6.1 Incidence of spread monitoring

The aim of this project is to determine the incidence of spread and re-establishment of blackwood in timber utilisation areas as well as in areas where no blackwood control takes place. Different levels of infestation and different habitats, such as the forest interior, forest margins and rivers are covered. Since 1997/98 all blackwood trees with DBH  5 cm in the effective areas of selected timber utilisation compartments have been recorded while marking trees for harvesting. In all other timber utilisation compartments all blackwood trees with DBH 20 cm have been recorded. This enumeration will be repeated after 10 years, when trees are marked for harvesting in the next cycle. The incidence of spread monitoring was expanded in 2000/01 to include areas that are not timber utilisation compartments. There are three monitoring areas on each of the three Forest Estates (Diepwalle, Farleigh and Tsitsikamma) that include different infestation intensities and habitats (forest interior, forest margins, and riverine areas). No control or harvesting was to be done in these areas. All blackwood trees with DBH  5 cm were measured and given a unique number. Re-measurement of these sites has been completed and preliminary findings provided support for a review of the blackwood management policy.

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6.2 Success of control action monitoring

This monitoring commenced in 2000/02 in nature reserves and other areas where blackwood eradication takes place. The monitoring areas include different habitats (forest interior, forest margins, and riverine areas). The objective is to quantify the success of blackwood control and to validate the time and money spent. The re-infestation by blackwood of areas where eradication takes place is monitored to see if re-establishment is decreased by the control operations.

6.3 Harkerville blackwood plot

In 1984 fifteen blackwood saplings 1.4 – 3.6 m tall were found growing beneath the forest canopy at Harkerville where a large mother tree had been felled a decade before. The blackwoods and a number of indigenous tree saplings have been measured annually since then to see how well they survive and grow beneath the forest canopy. In October 2004 the remaining 5 blackwood saplings were still stunted and showing signs of severe stress. A gap was subsequently created in the forest canopy above the saplings to see if they would be able to respond to increased light. It remains to be seen if any of them will be able to take a place in the forest canopy.

7 FAUNA

7.1 Antelope population monitoring

Faecal pellet group counts have been used since 1970 as an index to monitor the relative density of bushbuck (Tragelaphus scriptus) and blue duiker (Philantomba monticola) populations in the forests. This is the most effective method in dense forests because of the preserving influence of the microclimate on the pellet groups. It is also relatively simple and cost effective. The project was initiated in 1970 when 70 plots were laid out in Diepwalle State Forest. These plots were revisited in 1980, 1990 and 2000. During the period 1990 – 1992 fifty plots were laid out in each of the following nature reserves: Ysternek, Lelievlei, Sinclair, Whiskey Creek and Plaatbos. Re-measurements were carried out 10 years later. The program was extended to include Jubilee Creek Nature Reserve during 2002.

Bushbuck populations increased from 1970 to 1990, but have since declined again. Blue duiker populations declined during the 1970s and have remained low since. These changes appear to be related to climatic fluctuations. Bushbuck favour moister forest sites, while the blue duiker are more common in drier sites. Monitoring was conducted again since 2010, with preliminary results supporting previous trends. Trail cameras were deployed in the same areas to allow for comparison of different methods.

7.2 Rare mammal monitoring

This project was initiated in 1992 with the aim to get more information on leopard numbers and distribution, but it was extended in 1995 to include all other mammals excluding bushbuck and baboons. All reported sightings are recorded. The mammal species most commonly seen are , baboon, bushbuck, small grey mongoose, bushpig, caracal, honey badger, large-spotted genet and leopard. Trail cameras have recently been deployed in various sites to evaluate the most effective methodologies in the dense forest environment.

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7.3 Crowned eagle monitoring

The crowned eagle (Stephanoaetus coronatus) is a large raptor that is restricted to the forested and heavily wooded areas of Tropical Africa from Guinea eastwards to western and southwards through the subtropical region to the temperate region of South Africa. The population in the southern Cape represents the most southern and western (with the exception of one pair at Grootvadersbosch) distribution of this species in South Africa. Of the ten known crowned eagle nests in the southern Cape, nine occur on land managed by SANParks, while the other is situated on adjoining State Forest land managed by Cape . SANParks thus has a leading role to play in the conservation of this rare raptor. The aim of this project is to gather information on all crowned eagle sightings. Regular sightings of eagles in a particular area can then be investigated further to look for nests. The various nests in the southern Cape have been visited from time to time to assess the breeding frequency and success as well as to collect remains of prey items. Members of the Western Cape Nature Conservation Board (now Cape Nature) initiated a formal nest-monitoring programme in 1999 and co-ordinated visits to the nests annually.

Visits to all the nests in October 1999 produced no confirmed breeding for that particular year. The reason for the lack of breeding (or any other type of) activity at the nests could not be established. It is known that crowned eagles make use of alternate nests and as there are large tracts of forest available, the possibility exists that there are still a few undetected nests. The Beervlei nest was the only active nest in the 2000-breeding season. A fully-fledged juvenile was regularly seen in the vicinity of the nest up to April 2001. Visits to all the nests in December 2001 showed that both the Whiskey Creek and Witteklip nests might be in use. Visits to the known nests in December 2002 failed to reveal any breeding activity. In 2003 breeding was successful at the Beervlei nest. An egg was laid in the Gouna nest, but breeding was not successful. One chick was raised successfully at the Gouna nest in 2004, but no new breeding activity was recorded in 2005. Chicks were raised at both the Gouna and Beervlei nests at the end of 2006, but no further breeding activity has been noted since. Searches to locate additional active nesting sites have, to date, been unsuccessful. Efforts to locate additional nesting sites will be renewed following the training of field rangers.

Figure 11: Crowned Eagle. Figure 12: Knysna elephant

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7.4 The Knysna elephants

The Knysna elephants and their chances for survival have been a topic of concern and debate for over a century. Scientists estimated that about 3 000 elephants once roamed the Cape Floristic Region in pre-colonial times, of which about 1 000 occupied the Outeniqua- Tsitsikamma area. In the late 1800s between 400 and 500 elephants remained and by 1900, only 30 to 50 elephants were left in the Knysna area. This small population dwindled even further and recent attempts to determine the elephant population status included a genetic study, photographic identification, surveys and sightings, with varying results, ranging between 1 and 5 elephants. Although SANParks has been able to identify one elephant, this data are not treated as evidence for the absence of other individuals.

A popular belief that the Knysna elephants are genetically unique, was challenged by recent studies showing that these elephants once belonged to a larger, continuous southern African population, of the same sub-species as the , Loxodonta africana. These elephants’ genetic uniqueness, or rather lack thereof, has been used by some as a measurement of their conservation value. Basing elephants’ conservation value on their genetic status alone, however, ignores their potential role as an ecological role player. Elephants are a ‘keystone species’, essential for the integrity of the ecosystem. Elephants affect ecological processes through their feeding, digging and movement, and contribute to biodiversity by dispersing seeds, opening thickets, making browse more available to smaller herbivores, making water accessible in dry river beds, and promoting nutrient re-cycling.

The estimated 1000 elephants that historically roamed the Outeniqua-Tsitsikamma area, most certainly played an ecological role. Data on, and therefore an understanding of, the ecological role of elephants and their potential impact on biodiversity in the southern Cape is sparse, and the few scientific studies that were conducted, took place after the elephants were confined to the forest habitat. It is believed that the historical southern Cape elephant population’s range was confined to the forest parts around Knysna as a result of human settlement and agricultural development. The Knysna elephants may therefore have been cut-off from other habitat types that they historically visited, over a century ago. The absence of elephants in these habitats today may carry negative consequences for the elephants’ forage needs and for biodiversity.

SANParks’ scientists are currently conducting research in an attempt to determine historical diet shifts and identify habitat types that were historically preferred by elephants, but inaccessible to them today. Once identified, the ecological roles that elephant may have played in these habitats will be assessed. Elephants’ ecological roles in the current forest/fynbos range will also be assessed. Consequences for biodiversity, due to the present- day absence or low numbers of elephants in previously and currently used habitats, will be considered. In addition to this research, SANParks conducts a continuing elephant monitoring programme which aims to gather information on the current elephant population status, the current age/sex structure of the population, elephant spatial distribution and behavioural and movement patterns, investigating current landscape use and causes for recent range shifts. The monitoring techniques are non-intrusive to the elephants and involve gathering data on elephant signs, for example dung circumference measurements, notes on feeding signs and dung sample taking for elephant hormone studies.

There is a significant stakeholder (public, tourist, media, landowners etc) interest in elephants in this region. Following the strategic directions of SANParks (set out in the draft GRNP Elephant Management Plan), appropriate elephant management requires assessment of the roles that elephant play on both biodiversity (ecological roles) and stakeholders. SANParks therefore plans to define stakeholder values, perceptions and expectations regarding the Knysna elephants through public forums and surveys.

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8 CULTURAL HERITAGE RESOURCE MANAGEMENT

Several sites of cultural heritage importance occur on land managed by SANParks, including rock art, middens, gold mining shafts and workings, historical buildings, and graveyards. Site management plans are developed for each site and monitoring is carried out according to an annual monitoring schedule. The details of any new sites discovered are captured on the cultural heritage resources database.

9 SOCIAL MONITORING

9.1 Broad Based Black Economic Empowerment

As per SANParks corporate procurement policies and guidelines, the forest sections of the Garden Route National Park are committed to pursue the principles of Broad Based Black Economic Empowerment (Table 5).

Table 5: Total and BBBEE spending for 1 April 2013 to 31 March 2014 for the GRNP Forest Areas Class Description Grand Total Non-BEE Non-BEE BEE Value BEE % Value % Grand Total R 4 169 784.95 R 726 823.27 17.43% R 3 442 961.68 82.57% Contractors R 56 751.72 R 0.00 0.00% R 56 751.72 1.36% Contractors with CIDB cert R 5 680.00 R 0.00 0.00% R 5 680.00 0.14% Government R 620 806.85 R 0.00 0.00% R 620 806.85 14.89% Individuals (Not Companies) R 202 963.23 R 0.00 0.00% R 202 963.23 4.87% Petty Cash R 13 708.26 R 13 708.26 0.33% R 0.00 0.00% Staff Creditors R - 5 364.37 R-5 364.37 -0.13% R 0.00 0.00% Sundry Creditors R 2 574 628.02 R 452 364.29 10.85% R 2 122 263.73 50.90% Trade Creditors R 700 611.24 R 266 115.09 6.38% R 434 496.15 10.42%

9.2 Employment Equity

The employment equity figures for the forest sections of the Garden Route National Park are provided in Table 6.

Table 6: Employment equity statistics for the forest sections of the GRNP Occupational Male Female White Foreign TOTAL Levels Male Nationals A C I A C I W W Male Female (F – BAND) 0 0 0 0 0 0 0 0 0 0 (E – BAND) 0 0 0 0 0 0 0 0 0 0 0 (D – BAND) 0 0 0 1 0 0 0 2 0 0 3 (C – BAND) 1 2 0 0 2 0 1 1 0 0 7 (B- BAND) 6 58 0 1 5 0 0 1 0 0 71 (A – BAND) 0 18 0 4 4 0 0 0 0 0 26 TOTAL 7 78 0 6 11 0 1 4 0 0 107 PERMANENT Non – permanent employees GRAND 7 78 0 6 11 0 1 4 0 0 107 TOTAL 20

9.3 People and Conservation Park Based Education and Youth Development Programmes

Participants in Calendar Campaigns, Education and Youth Development Programmes in the GRNP during the first half of the 2014/15 financial year are shown in Table 7.

Table 7: Participation in Park based Education and Youth Development Programmes during 2014/15 in the GRNP ACTIVITY Year to Date TARGET September (6 months) (12 mths) Guided Groups 92 80 Other P&C Events 15 20 No of Children 5719 8500 No of Adults 4676 3500 No of free entries 5732 6000

9.4 Expanded Public Works Programmes (EPWP’s)

The GRNP is an implementing agent for the following EPWP’s that are active in the forest areas:  Working for Water (WfW)  Working for the Coast (WftC)  Wilderness Nursery  Working on Land

A summary of targets achieved for the 2014/2015 financial year appears in Table 8.

Table 8: Summary of EPWP targets achieved in the Garden Route National Park for the first six months of the 2014/2015 financial year (April – September 2014) WfW WftC Nursery WoL Total SMME TARGET 45 14 1 4 64 131% ACTUAL 51 26 2 5 84 Ha Initial TARGET 11 137 0 0 0 11 137 27% ACTUAL 2 970 0 0 2 2 972 Ha Follow TARGET 3 283 0 0 15 3 298 79% up ACTUAL 2 609 0 0 6 2 615 Person TARGET 57 103 45 793 1 389 4 502 108 787 80% Days ACTUAL 32 420 51 288 1 461 2 339 87 508 People TARGET 526 158 6 51 741 174% ACTUAL 728 456 6 97 1 287 Budget TARGET 15 220 909 11 433 519 354 886 565 546 27 574 859 77% ACTUAL 9 123 860 11 418 123 362 720 394 537 21 299 240

10 WASTE DISPOSAL

10.1 Hazardous waste

Hazardous waste is disposed in accordance with the “hazardous waste disposal guidelines”. A register is being kept of all hazardous waste being stored in the hazardous waste store as well as copies of certificates issued by Waste Tech when the hazardous waste is collected. 21

10.2 Household waste

Diepwalle household waste is removed on a weekly basis making use of the “two bag system” (black and green). All recyclable material is placed in the green bag. The waste is taken to the Municipal waste station in Knysna where the green bags are transported to the recycling center and the black bags loaded into containers and transported to PETROSA’s waste disposal facility where it is landfill.

The removal of Farleigh household waste is also done on a weekly basis with the “two bag system”. The waste is placed in bins and collected by a company called Greens Waste. Greens Waste has an approved and registered recycling and waste management system in place.

Household waste from Tsitsikamma is also done on a “two bag system”. Recyclable waste is transported to the recycling facility in Koukamma and non-recyclable waste is transported to registered landfill site within the Storms River section of the Garden Route National Park.

11 CHEMICAL USAGE

All chemical usage within the forest areas of the Garden Route National Park relates to alien plant clearing operations conducted in the forest, on forest margins, in the surrounding fynbos areas, at terrains and other open areas. Much of the work is carried out by Working for Water contractors (refer to the section on Expanded Public Works Programmes above). A detailed database is kept of all chemicals applied per individual contract issued.

12 COSTS, PRODUCTIVITY AND EFFICIENCY OF FOREST MANAGEMENT

The total budget for the forest areas for the 2014/15 financial year is R42.684 million, R29.454 million on personnel and R13.230 million on operational expenditure (Operating cost, Maintenance cost & Depreciation).

Progress towards achieving the forest management objectives for 2014/15 at the end of the second quarter are reflected in Table 9.

Table 9: Forest Management Objectives in the GRNP for 2014/15 Management Objective Deliverable Q1 Q2 Q3 Q4 Development and implementation of Programme developed and 10% 80% an exit programme in collaboration implemented. with DAFF and Cape Pine. Prioritise and conduct detailed All forest and fynbos areas 100% 100% floristic classification and mapping of in the park mapped and high conservation value areas in the classified forest and fynbos areas of the GRNP. Compilation, maintenance and Updated species lists. 50% 65% expansion of flora and fauna species Number of monitoring lists and implementation of programmes. monitoring programmes and Management prescriptions management prescriptions where developed and required. implemented. Maintaining state of area integrity Report against Corrective 10% 60% Measures Implementation of an FSC (Forestry FSC certification retained. 0% 0% Stewardship Council) audit and review process to ensure sustainable 22 forest management according to national and international standards Development and implementation of Fire Management systems 40% 60% fire management systems for the developed and work Outeniqua Mountain Catchment; shopped with various Tsitsikamma Mountain Catchment; stakeholders. Annual Plan and fragmented plateau and coastal of Operations developed fynbos. and implemented. Preparation of all firebreaks in terms All firebreaks prepared. 20% 35% of legislative requirements and enter Agreements with adjoining into agreements with adjacent land owners in place. landowners. Development and implementation of Management Unit Clearing 100% 100% Alien Invasive Plant control Plan developed. Annual programmes for priority species and Plan of Operations areas in the forest and fynbos compiled and implemented sections of the GRNP with resources assigned. Implementation of rehabilitation Implementation plans 25% 35% plans for areas with excessive compiled and implemented. erosion (including roads, trails, quarries) Maintaining viable populations of Viable populations 100% 100% rare/threatened plant species maintained and monitored. & monitor populations of priority species Developing and implementing Updated cultural heritage 60% 70% management plans to ensure the register with site specific conservation of cultural heritage Management guidelines sites, relics and the related intangible developed for each site. heritage associated with the Forest and Fynbos Areas of the GRNP. Ensuring that resource use is Monitoring and 100% 100% sustainable, in terms of species and implementation of resource products harvested use parameters for resource use projects. To include fern and timber harvesting. Managing and maintaining All management and 20% 35% appropriate management and tourism infrastructure tourism infrastructure maintained. Implemention of human resource Implementation of identified 20% 35% plans and skills development training interventions for strategy of the organisation personnel employed to fulfill functions related to the fynbos and forest sections of the GRNP. Maintaining effective, efficient and Unqualified audit reports. 0% 0% transparent systems of financial and risk management.

13 CONCLUSION

There is still a lot to learn about natural forest ecosystems. Forests are complex dynamic ecosystems undergoing continual change that is often slow and varies from place to place. Changes over time may be too gradual to detect on a 5 to 10-year time scale with the traditionally small sample sizes of most monitoring programs and more intensive sampling is seldom possible due to limited resources. Where changes are noticed it may be difficult to distinguish between natural changes and changes caused by management activities. Small but meaningful changes may not be detected. Few resource managers are lucky enough to 23 have complete and perfect information. The art of land use planning and resource management is to make the best possible use of incomplete and imperfect information. Deficiencies need to be recognised and remedied.

The monitoring programme in the Garden Route forests is well established and should continue to provide a wealth of data on natural forest dynamics and the effects of management for many decades to come, thereby ensuring that the management systems applied are sustainable.

APPENDIX 1: HARVEST TREE SELECTION CRITERIA APPLIED IN THE INDIGENOUS FORESTS OF THE GARDEN ROUTE NATIONAL PARK Ironwood (Olea capensis subsp. 1. Crown dieback  15% macrocarpa) 2. Main shoot lost. 3. Fork lost and remaining crown extremely small. 4. Sporophytes present. 5. Severe basal rot. Yellowwood (Podocarpus 1. Crown dieback  25% latifolius) 2. Main shoot lost. 3. Fork lost ( 50% of crown). Stinkwood (Ocotea bullata) 1. Crown dieback  35% (of total crown). 2. Main shoot or fork broken off/dead and  10% of remaining crown dying back of dead. Cherrywood (Pterocelastrus 1. Crown dieback  15% tricuspidatus) 2. Crown dieback > 5% and agony shoots and severe stem rot. 3. Severe crown damage/loss (main shoot or a major portion of the crown lost) and either (a) crown dieback  10% (of remaining crown), or (b) agony shoots, or (c) severe stem rot. 4. Severe stem rot and crown dieback  10%

White pear (Apodytes dimidiata) 1. Crown dieback  25% 2. Lots of agony shoots and crown dieback  5% 3. Agony shoots and crown dieback  20% 4. Major crown loss ( 50% of crown: main shoot or fork lost). 5. Severe stem rot.

Assegai (Curtisia dentata) 1. Crown dieback  35% 2. Major crown loss ( 50% of crown: main shoot or fork lost) and either (a) crown dieback  20% (of remaining crown), or (b) severe stem rot. 3. Severe stem rot and crown dieback  20% Quar (Psydrax obovata) 1. Crown dieback  25% 2. Major crown loss ( 50% of crown: main shoot or fork lost). 3. Crown dieback  10% and either (a) severe stem rot or (b) major branches/fork torn off. Hard pear (Olinia ventosa) 1. Crown dieback  20% All species 1. Windfall. 2. Crown broken off completely. 24

APPENDIX 2: TREE LIST FOR THE INDIGENOUS FORESTS OF THE GARDEN ROUTE

No. Abbrev. Scientific Name Family English Name Afrikaans Name Code 002 BV Cyathea capensis Cyatheaceae Forest Tree Fern Bosboomvaring 016 Kal Podocarpus falcatus Podocarpaceae Outeniqua Yellowwood Kalander 018 Geel Podocarpus latifolius Podocarpaceae Real Yellowwood Opregte Geelhout 020 Widdringtonia nodiflora Cupressaceae Mountain Cypress Bergsipres 032 KWP Strelitzia alba Strelitziaceae Cape Wild Banana Kaapse Wildepiesang 038 Myrica serrata Myricaceae Lance-leaved Waxberry Smalblaarwasbessie 039 WSH Celtis africana Ulmaceae White Stinkwood Witstinkhout 049 Ficus burtt-davyi Moraceae Veld Fig Veldvy 050 WVY (BTV) Ficus sur Moraceae Broom Cluster Fig Besemtrosvy 074 Ter macnaughtonii Terblans Beech Terblans 099 PBAS Colpoon compressum Santalaceae Cape Sumach Pruimbas 118 SH Ocotea bullata Stinkwood Stinkhout 134 WBOS racemulosa Forest Bush-cherry Witboshout 139 WBH Pittosporum viridiflorum Pittosporaceae Cheesewood Kasuur, Witboekenhout 140 RE Cunonia capensis Cunoniaceae Red Alder Rooiels 141 WE Platylophus trifoliatus Cunoniaceae White Alder Witels 142 OB crinitus Black Witch-hazel Onderbos 143 Hamamelidaceae White Witch-hazel Wittowerhaselaar 147 RSH Prunus africana Rosaceae Red Stinkwood Rooistinkhout 201 Schotia afra var. afra Fabaceae Karroo Boer-bean Karooboerboon 204 BBB Schotia latifolia Fabaceae Bush Boer-bean Bosboerboon 221 K Virgilia oroboides subsp.ferruginea Fabaceae Blossom Tree Keurboom 221.1 Virgilia divaricata Fabaceae Pink Blossom Tree Pienk Keurboom 253 Zanthoxylum capense Rutaceae Small Knobwood Kleinperdepram 254 PP Zanthoxylum davyi Rutaceae Knobwood Perdepram 256 WK Calodendrum capense Rutaceae Cape Chestnut Wildekastaiing 261 WYH Vepris lanceolata Rutaceae White Ironwood Witysterhout 265 Clausena anisata Rutaceae Horsewood Perdepis 298 Ess Ekebergia capensis Meliaceae Cape Ash Essenhout 307 KH Lachnostylis hirta Euphorbiaceae Coalwood Koolhout 366 YM Laurophyllus capensis Iron Martin Ystermartiens 380 BTB Searsia chirendensis Anacardiaceae Red Currant Bostaaibos 25

380.1 Searsia crenata Anacardiaceae Dune Crowberry Duinekraaibessie 383.2 Searsia glauca Anacardiaceae Blue Kuni-bush Bloukoeniebos 388 TAAIB Searsia longispina Anacardiaceae Thorny Currant Doringtaaibos 388.1 Btaai Searsia lucida forma lucida Anacardiaceae Glossy Currant Blinktaaibos 394 Searsia tomentosa Anacardiaceae Real Wild Currant Korentebos 395 KB Searsia undulata Anacardiaceae Kuni-bush Koenibos 397 WH Ilex mitis Aquifoliaceae Cape Holly Without 398 Rsy Maytenus acuminata var.acuminata Red Silky Bark Rooisybas 399 PD Maytenus heterophylla Celastraceae Common Spike-thorn Gewone Pendoring 399.3 Maytenus nemorosa Celastraceae White Forest Spike-thorn Witbospendoring 401 Sw Maytenus peduncularis Celastraceae Cape Blackwood Kaapse Swarthout 408 RKERS Pterocelastrus rostratus Celastraceae Red Candlewood Rooikershout 409 Kers Pterocelastrus tricuspidatus Celastraceae Cherrywood, Candlewood Kershout 410 SSAF Mystroxylon aethiopicum Celastraceae Kooboo-berry Koeboebessie, Seesaffraan 413 Sy Robsonodendron eucleiforme Celastraceae White Silky Bark Witsybas 414 Bsaf Cassine peragua subsp.peragua Celastraceae False Saffron Bastersaffraan 415 Saf Elaeodendron croceum Celastraceae Common Saffron Gewone Saffraan 418 Hartogiella schinoides Celastraceae Spoonwood Lepelhout 420 Cassinopsis illicifolia Icacinaceae Lemon Thorn Lemoentjiedoring 422 WP Apodytes dimidiata subsp.dimidiata Icacinaceae White Pear Witpeer 423 BAST decipiens False Currant Bastertaaibos 437 Dodonaea angustifolia Sapindaceae Sand Sandolien 438 Hippobromus pauciflorus Sapindaceae False Horsewood Basterperdepis 451 KATD (KD) Scutia myrtina Rhamnaceae Cat-thorn Katdoring 452 BB Rhamnus prinoides Rhamnaceae Dogwood Blinkblaar 457 africana Tiliaceae Cape Stock-rose Kaapse Stokroos 463 KRB Grewia occidentalis Tiliaceae Cross-berry Kruisbessie 479 RH Ochna arborea Ochnaceae Cape Plane Kaapse Rooihout 479.1 Ochna serrulata Ochnaceae Small-leaved Plane Fynblaarrooihout 494 VRH Kiggelaria africana Flacourtiaceae Wild Peach Vaderlandsrooihout, Wildeperske 496 RP Scolopia mundii Flacourtiaceae Red Pear Rooipeer 498 WD (DP) Scolopia zeyheri Flacourtiaceae Thorn Pear Doringpeer, Wolwedoring 503 WMB Trimeria grandifolia Flacourtiaceae Wild Mulberry Wildemoerbei 509 Dovyalis rhamnoides Flacourtiaceae Common Sourberry Gewone Suurbessie 513 HP Olinia ventosa Oliniaceae Hard Pear Hardepeer 520 GONA Passerina falcifolia Thymelaeaceae Outeniqua Gonna Outeniekwagonna 566 BKS Schefflera umbellifera Araliaceae False Cabbage Tree Basterkiepersol 26

568 Heteromorpha trifoliata Apiaceae Parsley Tree Wildepieterseliebos 570 Ass Curtisia dentata Cornaceae Assegai Assegaai 578 BH Rapanea melanophloeos Myrsinaceae Cape Beech Boekenhout 579 WMH inerme Sapotaceae White Milkwood Witmelkhout 599 Euclea racemosa Sea Guarri Seeghwarrie 600 BGW Euclea schimperi var.schimperi Ebenaceae Bush Guarri Bosghwarrie 601 GWAR Euclea undulata var.undulata Ebenaceae Common Guarri Gewone Ghwarrie 603 Tol Diospyros dichrophylla Ebenaceae Monkey Plum, Common star-apple Tolbos, Gewome sterappel 603.1 Diospyros glabra Ebenaceae Blueberry Bush Bloubessiebos 611 Btol Diospyros whyteana Ebenaceae Bladder nut Bostolbos 615 FYH Chionanthus foveolata subsp. Common Pock Ironwood Fynblaarysterhout foveolata 615.1 Chionanthus foveolata subsp. Oleaceae Cape Pock Ironwood Kaapse Pokysterhout tomentellus 617 OH Olea europaea subsp.africana Oleaceae Wild Olive Olienhout 618 YH Olea capensis subsp.macrocarpa Oleaceae Ironwood Ysterhout 619 BYH Olea capensis subsp.capensis Oleaceae False Ironwood Basterysterhout 619.1 Olea exasperata Oleaceae Dune Olive Duine-olienhout 622.1 Azima tetracantha Salvadoraceae Needle Bush Speldedoring 624 Strychnos decussata Loganiaceae Cape Kaapse Kiaat 634 V Nuxia floribunda Loganiaceae Forest Elder Bosvlier 636 WHO Buddleja saligna Loganiaceae False Olive Witolienhout 637 SAL Buddleja salvifolia Loganiaceae Sagewood Saliehout 639 Acokanthera oppositifolia Apocynaceae Common Poison-bush Gewone Gifboom 641 Kam Gonioma kamassi Apocynaceae Kamassi Kamassie 670 N Halleria lucida Scrophulariaceae Tree Fuchsia Notsung 688 WG Burchellia bubalina Rubiaceae Wild Pomegranate Wildegranaat 693 WKP Rothmannia capensis Rubiaceae Wild Wildekatjiepiering 708 BD Canthium inerme Rubiaceae Common Turkey-berry Gewone Bokdrol 710 KE Canthium mundianum Rubiaceae Rock Alder Klipels 711 Kw Psydrax obovata subsp.obovata Rubiaceae Quar Kwar 723 Psychotria capensis Rubiaceae Black Bird-berry Swartvoelbessie 726 Malb Brachylaena glabra Asteraceae Malabar Tree Malbaar 729 Brachylaena neriifolia Asteraceae Water White Alder Waterwitels 733 WS Tarchonanthus camphoratus Asteraceae Wild Camphor Bush Wildekanferbos 736 Chrysanthemoides monilifera Asteraceae Bush-tick Berry Bietou