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Deforestation in Ghana has led to a forest loss of almost 20% from 9,924,000 ha in 1990 to 7,986,000 ha today. To restore degraded lands, Forest Landscape Restoration has become a critical approach globally. This study was conducted in Ghana focusing on the examples of two forest landscape restoration projects in the Pamu Berekum Forest Reserve: 10-year-old mixed-stands of two to four native tree species and an exotic species stands, including Triplochiton scleroxylon, Terminalia ivorensis, Ceiba pentandra, Nauclea diderrichii and Cedrela odorata at Pamu Berekum 1 and 4-year-old Tectona grandis and 2-year-old Gmelina arborea monoculture stands at Pamu Berekum 2. Estimates of productivity in the restored forests are described, as well as the effects of the restoration on provision of ecosystem service and benefits obtained by local communities. Stand productivity was assessed as mean annual increment of diameter and height, biomass production, and standing volume. For ecosystem services, carbon stocks were calculated for the restored forests; other ecological benefits, as well as financial benefits, were obtained through interviews with fringe communities. The results indicate that FLR can be implemented successfully using different models provided that local communities are involved during the planning and implementation of interventions. When all stands were projected to 10 years, results show higher productivity in T. grandis (331.77 m3 ha-1) and G. arborea stands (1,785.99 m3ha-1) compared to mixed stand (160.41 m3 ha-1). The Gmelina arborea stand was more productive and had higher carbon stocks (1,350.10 Mg ha-1) relative to the T. grandis stand (159.89 Mg ha-1). Both restoration projects were found to deliver important benefits and ecosystem services at the local and national levels, including direct and indirect benefits. The results provide an example for forest/environmental managers on how FLR might be implemented to create multiple benefits at different le

Deforestation in Ghana has led to a forest loss of almost 20% from 9,924,000 ha in 1990 to 7,986,000 ha today. To restore degraded lands, Forest Landscape Restoration has become a critical approach globally. This study was conducted in Ghana focusing on the examples of two forest landscape restoration projects in the Pamu Berekum Forest Reserve: 10-year-old mixed-stands of two to four native tree species and an exotic species stands, including Triplochiton scleroxylon, Terminalia ivorensis, Ceiba pentandra, Nauclea diderrichii and Cedrela odorata at Pamu Berekum 1 and 4-year-old Tectona grandis and 2-year-old Gmelina arborea monoculture stands at Pamu Berekum 2. Estimates of productivity in the restored forests are described, as well as the effects of the restoration on provision of ecosystem service and benefits obtained by local communities. Stand productivity was assessed as mean annual increment of diameter and height, biomass production, and standing volume. For ecosystem services, carbon stocks were calculated for the restored forests; other ecological benefits, as well as financial benefits, were obtained through interviews with fringe communities. The results indicate that FLR can be implemented successfully using different models provided that local communities are involved during the planning and implementation of interventions. When all stands were projected to 10 years, results show higher productivity in T. grandis (331.77 m3 ha-1) and G. arborea stands (1,785.99 m3ha-1) compared to mixed stand (160.41 m3 ha-1). The Gmelina arborea stand was more productive and had higher carbon stocks (1,350.10 Mg ha-1) relative to the T. grandis stand (159.89 Mg ha-1). Both restoration projects were found to deliver important benefits and ecosystem services at the local and national levels, including direct and indirect benefits. The results provide an example for forest/environmental managers on how FLR might be implemented to create multiple benefits at different le

Almost half of the total organic carbon (C) in terrestrial ecosystems is stored in forest soils. By altering rates of input or release of C from soils, forest management activities can influence soil C stocks in forests. In this review, we synthesize current evidence regarding the influences of 13 common forest management practices on forest soil C stocks. Afforestation of former croplands generally increases soil C stocks, whereas on former grasslands and peatlands, soil C stocks are unchanged or even reduced following afforestation. The conversion of primary forests to secondary forests generally reduces soil C stocks, particularly if the land is converted to an agricultural land-use prior to reforestation. Harvesting, particularly clear-cut harvesting, generally results in a reduction in soil C stocks, particularly in the forest floor and upper mineral soil. Removal of residues by harvesting whole-trees and stumps negatively affects soil C stocks. Soil disturbance from site preparation decreases soil C stocks, particularly in the organic top soil, however improved growth of tree seedlings may outweigh soil C losses over a rotation. Nitrogen (N) addition has an overall positive effect on soil C stocks across a wide range of forest ecosystems. Likewise, higher stocks and faster accumulation of soil C occur under tree species with N-fixing associates. Stocks and accumulation rates of soil C also differ under different tree species, with coniferous species accumulating more C in the forest floor and broadleaved species tending to store more C in the mineral soil. There is some evidence that increased tree species diversity could positively affect soil C stocks in temperate and subtropical forests, but tree species identity, particularly N-fixing species, seems to have a stronger impact on soil C stocks than tree species diversity. Management of stand density and thinning have small effects on forest soil C stocks. In forests with high populations of ungulate herbivor

Almost half of the total organic carbon (C) in terrestrial ecosystems is stored in forest soils. By altering rates of input or release of C from soils, forest management activities can influence soil C stocks in forests. In this review, we synthesize current evidence regarding the influences of 13 common forest management practices on forest soil C stocks. Afforestation of former croplands generally increases soil C stocks, whereas on former grasslands and peatlands, soil C stocks are unchanged or even reduced following afforestation. The conversion of primary forests to secondary forests generally reduces soil C stocks, particularly if the land is converted to an agricultural land-use prior to reforestation. Harvesting, particularly clear-cut harvesting, generally results in a reduction in soil C stocks, particularly in the forest floor and upper mineral soil. Removal of residues by harvesting whole-trees and stumps negatively affects soil C stocks. Soil disturbance from site preparation decreases soil C stocks, particularly in the organic top soil, however improved growth of tree seedlings may outweigh soil C losses over a rotation. Nitrogen (N) addition has an overall positive effect on soil C stocks across a wide range of forest ecosystems. Likewise, higher stocks and faster accumulation of soil C occur under tree species with N-fixing associates. Stocks and accumulation rates of soil C also differ under different tree species, with coniferous species accumulating more C in the forest floor and broadleaved species tending to store more C in the mineral soil. There is some evidence that increased tree species diversity could positively affect soil C stocks in temperate and subtropical forests, but tree species identity, particularly N-fixing species, seems to have a stronger impact on soil C stocks than tree species diversity. Management of stand density and thinning have small effects on forest soil C stocks. In forests with high populations of ungulate herbivor

Almost half of the total organic carbon (C) in terrestrial ecosystems is stored in forest soils. By altering rates of input or release of C from soils, forest management activities can influence soil C stocks in forests. In this review, we synthesize current evidence regarding the influences of 13 common forest management practices on forest soil C stocks. Afforestation of former croplands generally increases soil C stocks, whereas on former grasslands and peatlands, soil C stocks are unchanged or even reduced following afforestation. The conversion of primary forests to secondary forests generally reduces soil C stocks, particularly if the land is converted to an agricultural land-use prior to reforestation. Harvesting, particularly clear-cut harvesting, generally results in a reduction in soil C stocks, particularly in the forest floor and upper mineral soil. Removal of residues by harvesting whole-trees and stumps negatively affects soil C stocks. Soil disturbance from site preparation decreases soil C stocks, particularly in the organic top soil, however improved growth of tree seedlings may outweigh soil C losses over a rotation. Nitrogen (N) addition has an overall positive effect on soil C stocks across a wide range of forest ecosystems. Likewise, higher stocks and faster accumulation of soil C occur under tree species with N-fixing associates. Stocks and accumulation rates of soil C also differ under different tree species, with coniferous species accumulating more C in the forest floor and broadleaved species tending to store more C in the mineral soil. There is some evidence that increased tree species diversity could positively affect soil C stocks in temperate and subtropical forests, but tree species identity, particularly N-fixing species, seems to have a stronger impact on soil C stocks than tree species diversity. Management of stand density and thinning have small effects on forest soil C stocks. In forests with high populations of ungulate herbi

Almost half of the total organic carbon (C) in terrestrial ecosystems is stored in forest soils. By altering rates of input or release of C from soils, forest management activities can influence soil C stocks in forests. In this review, we synthesize current evidence regarding the influences of 13 common forest management practices on forest soil C stocks. Afforestation of former croplands generally increases soil C stocks, whereas on former grasslands and peatlands, soil C stocks are unchanged or even reduced following afforestation. The conversion of primary forests to secondary forests generally reduces soil C stocks, particularly if the land is converted to an agricultural land-use prior to reforestation. Harvesting, particularly clear-cut harvesting, generally results in a reduction in soil C stocks, particularly in the forest floor and upper mineral soil. Removal of residues by harvesting whole-trees and stumps negatively affects soil C stocks. Soil disturbance from site preparation decreases soil C stocks, particularly in the organic top soil, however improved growth of tree seedlings may outweigh soil C losses over a rotation. Nitrogen (N) addition has an overall positive effect on soil C stocks across a wide range of forest ecosystems. Likewise, higher stocks and faster accumulation of soil C occur under tree species with N-fixing associates. Stocks and accumulation rates of soil C also differ under different tree species, with coniferous species accumulating more C in the forest floor and broadleaved species tending to store more C in the mineral soil. There is some evidence that increased tree species diversity could positively affect soil C stocks in temperate and subtropical forests, but tree species identity, particularly N-fixing species, seems to have a stronger impact on soil C stocks than tree species diversity. Management of stand density and thinning have small effects on forest soil C stocks. In forests with high populations of ungulate herbi

Key message: There is no one-size-fits-all way to successfully implement forest landscape restoration (FLR). Complex socio-ecological systems present challenges and opportunities that can best be met with a systematic framework for designing, planning, steering, and monitoring FLR projects to meet diverse needs. Project cycle management is an iterative, adaptive, hierarchical framework with recurring consultations among stakeholders that can enhance the likelihood of FLR success.

Terrestrial ecosystems are globally under threat of loss or degradation. To compensate for the impacts incurred by loss and/or degradation, efforts to restore ecosystems are being undertaken. These efforts often focus on restoring the aboveground plant community with the expectation that the belowground microbial community will follow suit. This 'Field of Dreams' expectation - if you build it, they will come - makes untested assumptions about how microbial communities and their functions will respond to aboveground-focused restoration. To determine if restoration of aboveground plant communities equates to restoration of belowground microbial communities, we assessed the effects of four forest restoration treatments - varying in intensity from unmanaged to interplanting tree species - on microbial (i.e. prokaryotic and fungal) community composition and function (i.e. catabolic profiles and extracellular enzyme activities). Additionally, effects of the restoration treatments were compared to both degraded (i.e. active arable cultivation) and target endpoint communities (i.e. remnant bottomland forest) to determine the trajectory of intensifying aboveground restoration efforts on microbial communities. Approximately 16 years after the initiation of the restoration treatments, prokaryotic and fungal community composition, and microbial function in the four restoration treatments were intermediate to the endpoint communities. Surprisingly, intensification of aboveground restoration efforts led to few differences among the four restoration treatments and increasing intensification did not consistently lead to microbial communities with greater similarity in composition and function to the target remnant forest communities. Together these results suggest that belowground microbial community composition and function will respond little to, or will lag markedly behind, intensifying aboveground restoration efforts. Reliance on a Field of Dreams' approach, even if you build i

Terrestrial ecosystems are globally under threat of loss or degradation. To compensate for the impacts incurred by loss and/or degradation, efforts to restore ecosystems are being undertaken. These efforts often focus on restoring the aboveground plant community with the expectation that the belowground microbial community will follow suit. This 'Field of Dreams' expectation - if you build it, they will come - makes untested assumptions about how microbial communities and their functions will respond to aboveground-focused restoration. To determine if restoration of aboveground plant communities equates to restoration of belowground microbial communities, we assessed the effects of four forest restoration treatments - varying in intensity from unmanaged to interplanting tree species - on microbial (i.e. prokaryotic and fungal) community composition and function (i.e. catabolic profiles and extracellular enzyme activities). Additionally, effects of the restoration treatments were compared to both degraded (i.e. active arable cultivation) and target endpoint communities (i.e. remnant bottomland forest) to determine the trajectory of intensifying aboveground restoration efforts on microbial communities. Approximately 16 years after the initiation of the restoration treatments, prokaryotic and fungal community composition, and microbial function in the four restoration treatments were intermediate to the endpoint communities. Surprisingly, intensification of aboveground restoration efforts led to few differences among the four restoration treatments and increasing intensification did not consistently lead to microbial communities with greater similarity in composition and function to the target remnant forest communities. Together these results suggest that belowground microbial community composition and function will respond little to, or will lag markedly behind, intensifying aboveground restoration efforts. Reliance on a Field of Dreams' approach, even if you build i

The report by Naudts et al. concludes that forest management in Europe during the last 260 years has failed to result in net CO2 removal from the atmosphere. The authors have reached this conclusion through their failure to consider a key factor in their otherwise comprehensive analysis. The authors present an analysis of net carbon emissions from forest, but omit substitution effects related to the link between forest management and the fossil carbon pool. The link between fossil and terrestrial carbon pools is however critical for modelling climate impacts. To conclude as they do, the authors should have asked: What would the GHG emissions have been in absence of forest management in Europe? The services provided by forest management - increased biofuel and materials production – substitute fossil fuels and materials, which are generally GHG-intensive. The report ignores that sustained yield forest management was developed to meet demands for energy and materials for an increasing population and prevented a complete destruction of Europe’s forest. Particularly since 1850, forest management has increased Europe’s forest area and productivity, and thus also the forest carbon pool as also reported by Naudts et al. By ignoring the link between forestry and fossil carbon pools and not considering development in the absence of forest management, there is no accounting for the effect on GHG emissions, and no basis for estimating the contribution of forest management to cl...

Drawing on state-of-the art scientific knowledge through analysis of restoration case studies and review of scientific literature, IUFRO scientists developed a framework to demonstrate how forest landscape restoration (FLR) can contribute to climate change mitigation and adaptation. One of the major results of this study was the identification and detailed description of the many different ways in which FLR contributes to both mitigating climate effects and helping ecosystems and society to adapt to adverse effects of a changing climate. In addition, this work contributed a stoplight tool aimed at better presenting complex restoration initiatives, and how they may contribute to climate change mitigation and adaptation and vice-versa, in a specific local context.

Drawing on state-of-the art scientific knowledge through analysis of restoration case studies and review of scientific literature, IUFRO scientists developed a framework to demonstrate how forest landscape restoration (FLR) can contribute to climate change mitigation and adaptation. One of the major results of this study was the identification and detailed description of the many different ways in which FLR contributes to both mitigating climate effects and helping ecosystems and society to adapt to adverse effects of a changing climate. In addition, this work contributed a stoplight tool aimed at better presenting complex restoration initiatives, and how they may contribute to climate change mitigation and adaptation and vice-versa, in a specific local context.

Macro-economic decisions determine the resources allocated at an international and a country-level to natural resource management. Micro-economic theory and tools are then used to ensure that this allocation will materialize into desired economic, environmental and societal outcomes. Restoration projects differ in their costs and benefits. The costs may entail operational costs, and those associated with alternative foregone opportunities. The benefits of restoration may reflect biodiversity outcomes or the provision of ecosystem goods and services, such as the supply of water and carbon sequestration. Restoration also has the potential to ensure supply of timber and non-timber forest products such as food and medicines, with potential significance for subsistence livelihoods. We synthesise approaches to valuing the costs and benefits of restoration projects in order to explore the economic consequences of restoration decisions and to prioritise investments. We finish the chapter by outlining economic incentives and policies that might support the implementation of restoration activities.

Floodplain forests are linear forest systems, occupying the lower areas of river catchments. Their boundaries correspond with the areas disturbed by river flooding and they generally have shallow water tables. The ecology of floodplain forests is closely linked to the dynamic physical processes associated with flooding. The regeneration of floodplain forest species is particularly dependent on periodic floods and sediment deposition. River engineering practices and wholesale clearance of natural floodplain forests for agriculture or forestry have made them very rare in Europe, with about 10 % of the original amount remaining, mostly in the larger river systems of Eastern Europe. There are new opportunities for restoration of floodplain forests provided by some areas of European legislation such as the European Habitats Directive, Water Framework Directive and Floods Directive and by a new interest in soft engineering approaches to flood management. However, many constraints remain, often related to competing economic incentives for the use of floodplain land.

Floodplain forests are linear forest systems, occupying the lower areas of river catchments. Their boundaries correspond with the areas disturbed by river flooding and they generally have shallow water tables. The ecology of floodplain forests is closely linked to the dynamic physical processes associated with flooding. The regeneration of floodplain forest species is particularly dependent on periodic floods and sediment deposition. River engineering practices and wholesale clearance of natural floodplain forests for agriculture or forestry have made them very rare in Europe, with about 10 % of the original amount remaining, mostly in the larger river systems of Eastern Europe. There are new opportunities for restoration of floodplain forests provided by some areas of European legislation such as the European Habitats Directive, Water Framework Directive and Floods Directive and by a new interest in soft engineering approaches to flood management. However, many constraints remain, often related to competing economic incentives for the use of floodplain land.