Afforestation is an important greenhouse gas (GHG) mitigation strategy but the efficacy of commercial forestry is disputed. Here, we calculate the potential GHG mitigation of a UK national planting strategy of 30,000 ha yr−1 from 2020 to 2050, using dynamic life cycle assessment. What-if scenarios vary: conifer-broadleaf composition, harvesting, product breakouts, and decarbonisation of substituted energy and materials, to estimate 100-year GHG mitigation. Here we find forest growth rate is the most important determinant of cumulative mitigation by 2120, irrespective of whether trees are harvested. A national planting strategy of commercial forest could mitigate 1.64 Pg CO2e by 2120 (cumulative), compared with 0.54–1.72 Pg CO2e for planting only conservation forests, depending on species composition. Even after heavy discounting of future product substitution credits based on industrial decarbonisation projections, GHG mitigation from harvested stands typically surpasses unharvested stands. Commercial afforestation can deliver effective GHG mitigation that is robust to future decarbonisation pathways and wood uses.
Achieving the ambition of the Paris Agreement to limit global warming to 1.5 °C above pre-industrial levels requires rapid implementation of negative emissions technologies1, in particular increasing forest carbon sinks2. Afforestation on land spared from agriculture3 is proposed as an integral element of greenhouse gas (GHG) mitigation4,5, but mitigation efficacy is highly context specific and depends on, inter alia, climate, tree species, management and product substitution. In tropical regions, fast-growing commercial forests managed for wood production have been unfavourably compared to restoration of natural forest6 but these conclusions are not transferable to a temperate context. There remains a gap in evidence determining the most effective type of temperate forestry for achieving GHG mitigation. The role of sustainable wood harvesting is recognised in GHG mitigation strategies5,7,8 and could be enhanced through cascading use of wood9, but recent modelling indicates that future mitigation from product substitution will diminish owing to decarbonisation of substituted materials and energy10,11. In coniferous temperate forests, bioenergy harvest breakeven times can range from 30 to 70 years assuming coal is being replaced, depending on the scale of the assessment and whether the stands are damaged12. Meanwhile, dynamic life cycle assessment (LCA) studies indicate that it can take up to 100 years for CO2 released from current bioenergy generation to be fully compensated by forest regrowth13,14.
To fully understand the role of new commercial forests in future GHG mitigation, there remains a need for coherent modelling of GHG mitigation across the four life cycle stages (production, use, cascading use and end-of-life) of hierarchical wood value chains15 in the context of decarbonised material and energy systems4. We fill this gap through comparison of 100-year mitigation achieved by newly planted commercial and conservation (i.e., unharvested) forests in the UK, a country with high afforestation potential3,16,17. Although prioritising GHG mitigation in afforestation strategies will involve complex trade-offs with other ecosystem services18,19,20,21, such as biodiversity conservation, the purpose of this paper is not to explore these. Rather, it aims to generate robust evidence on the efficacy of alternative afforestation options for the primary strategic aim of mitigating GHG emissions. We apply dynamic consequential LCA22 to 33 what-if scenarios representing a range of commercial Sitka spruce (Picea sitchensis) forests with different harvested wood product (HWP) value chains, and conservation forests, across representative growth rates, and in the context of different decarbonisation pathways (Table 1).
Under typical conditions, one hectare of newly planted commercial forest could achieve cumulative GHG mitigation of up to 2.27 Gg CO2e ha−1 within a core decarbonisation pathway projected for the UK4 by 2120—up to 269% more mitigation than delivered by newly planted broadleaf conservation forests, and 17% more than achieved by leaving a newly planted fast-growing conifer forest unharvested. Harvesting reduces long-term terrestrial carbon storage by 61%, but this is more than offset by HWP carbon storage, and concrete and energy substitution—even with near total decarbonisation of the energy sector within the 100-year study horizon. Projected wide deployment of carbon capture and storage (CCS)4 contributes up to 45% of cumulative 100-year mitigation benefit, but also reduces the energy substitution credits realised by future wood energy. Consequently, the efficacy of mitigation is surprisingly similar between hierarchical and bioenergy uses of wood, and remarkably resilient to CCS deployment assumptions. To contextualise the results in a national planting strategy, we model the UK Committee on Climate Change recommended planting rate of 30,000 ha year−1 from 2020 to 2050. If this strategic target is met with commercial forests, it would cumulatively mitigate up to 1.64 Pg CO2e emissions by 2120, compared with 0.54 Pg CO2e for a semi-natural broadleaf conservation forest, or 1.09 Pg CO2e for an equal planting rate of 15,000 ha year−1 of each forest type. For UK forests and projected decarbonisation pathways, large-scale commercial afforestation could contribute strongly to GHG mitigation targets.
One hundred-year snapshots following a single planting event
Terrestrial carbon sequestration in semi-natural broadleaf, mixed conifer-broadleaf and fast-growing conifer conservation forests planted in 2020 equates to cumulative mitigation by 2120 of 0.62 (0.41–0.82), 1.30 (0.94–1.64) and 1.94 (1.30–2.58) Gg CO2e ha−1, respectively (Fig. 1). Mitigation performance across these conservation forest types is proportionate to yields (Table 1). On average over 100 years, commercial Sitka spruce forests store 61 and 42% less terrestrial carbon than unharvested conifer and mixed conservation forests, respectively, but still 24% more than slow-growing semi-natural broadleaf forests (Fig. 1). However, in addition to terrestrial carbon storage, commercial forests realise ca. 1.7 Gg CO2e ha−1 mitigation by HWP carbon storage, fossil fuel substitution, bioenergy carbon capture and storage (BECCS) and concrete substitution in the Core context, at average growth rates (Fig. 1). Relatively small processing emissions of 0.20 (Bioenergy prioritised wood use) to 0.28 Gg CO2e ha−1 (Hierarchical wood use) are based on the conservative assumption of a very gradual decline in the emission intensity of processing operations (Table 2 and Supplementary Data 1). Overall, one hectare of yield class (YC) 18 commercial forest planted in 2020 will achieve cumulative GHG mitigation of between 2.0 and 2.27 Gg CO2e by 2120, varying by less than 8 and 10% between wood use strategy and decarbonisation context, respectively. Yield variability extends the mitigation range to 1.36–2.96 Gg CO2e ha−1 by 2120. Thus, commercial Sitka spruce forests support between 3% (relative to 100% conifer) and 269% (relative to 100% broadleaf) more GHG mitigation than conservation forests over a 100-year time horizon from establishment.
National planting programme
In our scenario of a commercial forest planting programme involving 30,000 ha planted every year from 2020 until 2050 (Fig. 2), only 15% of the 100-year mitigation will be achieved by 2050. A 30-year commercial forest planting strategy could achieve cumulative net mitigation of up to 1.64 Pg CO2e at default yield (Fig. 2), with a range across yields and scenarios of 1.13–2.0 Pg CO2e for YC 14 Hierarchical (Further Ambition) and YC22 Bioenergy (Core), respectively (shown in Supplementary Data 2 and Supplementary Data 3). This compares with mitigation of between 0.54, 1.15 and 1.72 Pg CO2e from equal planting of semi-natural, 50:50 conifer-broadleaf mixed or unharvested conifer forests, respectively (Fig. 2), at default yields (Table 1). A mixed planting strategy of 15,000 ha per year each of commercial forest (YC 18) and semi-natural broadleaf forest (YC 4) could achieve 1.09 Pg CO2e mitigation, 34% lower than commercial forestry alone. For commercial forests established after 2040, cumulative mitigation from regrowth and downstream mitigation does not catch up with cumulative mitigation achieved by unharvested conifer conservation forests by 2120, so that the latter forest type outperforms commercial forests for the 30-year planting programme—despite commercial forests achieving more mitigation across two full rotations (Fig. 1). However, mitigation trajectories (Fig. 2) and 100-year mitigation performance (Fig. 1) indicate that commercial forests would achieve considerably more mitigation than conifer conservation forests beyond our 2120 cut-off. Basing the national forest planting programme entirely on a Bioenergy wood use strategy would achieve annual mitigation of 20.2 Tg CO2e by 2050 from YC 18 Sitka spruce, under a Further Ambition context (Supplementary Data 3), equating to 24% of projected gross anthropogenic GHG emissions in the UK if net zero targets are achieved4. Establishing 30,000 ha year−1 of commercial forests could directly supply 3.88 or 14.2 TWh year−1 electricity from thinnings plus first-harvest biomass, from 2070 onwards, based on Hierarchical (Supplementary Data 2) or Bioenergy (Supplementary Data 3) wood use strategies, respectively (end-of-life use of construction wood for bioenergy generates a further 20–43% electricity over the following 50 years—Supplementary Data 2 and Supplementary Data 3).
Wood use and decarbonisation scenarios
For a national planting programme of 30,000 ha year−1, more rapid decarbonisation of the wider economy represented in the Further Ambition (vs Core) context could reduce cumulative national mitigation achieved by Hierarchical or Bioenergy wood use in 2120 by 5% or 2%, respectively (Fig. 2). Meanwhile, a Bioenergy wood use strategy rather than Hierarchical wood use strategy could increase cumulative GHG mitigation achieved in 2120 by 5% (Core context) to 8% (Further Ambition context) (Fig. 2). In the Further Ambition context, future process emissions and fossil fuel substitution credits are minor, concrete substitution credits are diminished relative to the Core context and mitigation by BECCS becomes prominent through time (Fig. 2). In fact, BECCS accounts for 33% of cumulative mitigation by 2120 in the Bioenergy wood use strategy, whilst HWP carbon storage accounts for just 5% of cumulative mitigation (Fig. 2), reflecting the fact that 65% of harvested biomass immediately goes to bioelectricity generation (Table 1). Respective figures for the Hierarchical wood use strategy are 16 and 17% for BECCS and HWP carbon storage (Fig. 1). HWP carbon storage of 69 (53–85) Tg C by 2120 in the Hierarchical value chains (Supplementary Data 2) is likely to increase further following subsequent harvests and cascading use of the circa 140 Tg of wood dry matter remaining within the built environment at the end of the studied time horizon. In both Bioenergy and Hierarchical scenarios, the BECCS pool will also continue to grow as biomass and cascaded products reach their final use.
In the national planting programme with Hierarchical wood use, product substitution (concrete) accounts for 0.12–0.32 Pg CO2 (8–20%) of cumulative GHG mitigation by 2120 for Core and Further Ambition contexts (YC 18), respectively. Reducing product substitution by 50% would reduce cumulative GHG mitigation by 5% or 11% for Core or Further Ambition contexts, respectively (Supplementary Data 5). Counterintuitively, concrete substitution makes a greater relative contribution to GHG mitigation in the Further Ambition context than the Core context, because net mitigation is lower and concrete decarbonisation lags energy decarbonisation under the Further Ambition decarbonisation pathway. Alternatively, introducing glulam production (substituting structural steel) alongside development of fibres to substitute oil-derived textile fibres could increase cumulative GHG mitigation achieved in 2120 by 10% or 7% for a national planting programme in a Core or Further Ambition context, respectively (Supplementary Data 5). Potentially, viscose fibre could substitute cotton fibre instead of synthetic fibres, in which case one ha of cotton production could be avoided for every ha of commercial forest planted—which could lead to significant further afforestation and associated GHG mitigation overseas (beyond the scope of this study to quantify). In the pessimistic event of no deployment of CCS technology during the 100-year study time horizon, 100-year mitigation achieved by a commercial forest planting strategy in the UK would be reduced by just 8% (Core) or 6% (Further Ambition) for Bioenergy wood use (Supplementary Data 7) and 6% (Core) or 4% (Further Ambition) for Hierarchical wood use (Supplementary Data 6), respectively. In the absence of CCS, energy and concrete substitution credits are larger than in the base case, counteracting the effects of reduced BECCS and thus reducing the sensitivity of net GHG mitigation to CCS deployment. Across all these alternative product substitutions, commercial forestry remains an effective GHG mitigation strategy, still achieving up to 162% more GHG mitigation than semi-natural conservation forestry in the worst case scenario of reduced concrete substitution.
New evidence presented in this paper emphasises the efficacy of commercial forestry for GHG mitigation, and its resilience to future decarbonisation pathways and wood uses, highlighting the effective and reliable contribution that commercial forestry could make towards the Paris Agreement1 even with projected decarbonisation of marginal materials and energy that are likely to be substituted by HWPs in the future. These results counter the conclusions of recent studies questioning the climate credentials of commercial forestry6,10,23. Our study demonstrates the importance of considering multiple stages of hierarchical wood use, considering, inter alia, consistent time-dependent substitution factors and CCS deployment based on published projections4,24. However, we do find that at equivalent growth rates, commercial forests lag unharvested conservation forests in cumulative GHG mitigation until just before the second harvest cycle (90 years after establishment for typical UK forests).
The magnitude of GHG mitigation achieved by commercial forestry is remarkably resilient to the uses of wood and wider decarbonisation pathways over a 100-year timeframe. Indeed, across all the variables considered, it is clear that tree growth rates have the greatest influence on GHG mitigation, in line with previous studies focussed primarily on terrestrial carbon storage by forests25,26. In this study, the vast majority of product substitution credits attributable to new forest planting are heavily discounted because they arise over 50 years into the future (after first main harvest) when decarbonisation projections indicate much lower emission intensities for substituted energy and materials (Supplementary Data 1). Had current substitution credits been applied throughout, the GHG mitigation achieved by commercial forests would have been considerably greater, and more sensitive to variations in wood use15,27,28. Nonetheless, it remains clear that hierarchical use of timber relies on proven technologies to deliver the majority of 100-year mitigation via HWP carbon storage and displacement of mineral construction materials that are unlikely to fully decarbonise for many decades4,9 (Table 2), maintaining effective mitigation 100 years after first plantings (Fig. 2). Demand for wood is expected to grow as the circular bioeconomy expands and new products are developed (e.g., engineered and modified timber construction products, silvi-chemicals, textiles and biocomposites)4,26. Our results show that commercial forests could supply a large share of these future demands whilst delivering comparable or more long-term GHG mitigation compared with conservation forests.
Somewhat surprisingly, both Hierarchical and Bioenergy value chain GHG mitigation was robust to assumptions about CCS deployment. BECCS features prominently in many climate stabilisation scenarios1,4,5 but depends on commercially unproven technology29. Conservatively, our Core decarbonisation pathway involves widespread deployment of BECCS only after 2085, whilst our Further Ambition pathway assumes widespread deployment from 2050 (Table 2)—though with limited effects until the first main harvests from 2070 onwards (Fig. 2). Most climate change mitigation projections indicate a substantial role for dispatchable bioenergy (with CCS) at least up to the end of this century4,5,17,30. Global requirements for primary energy from biomass to meet Paris Agreement goals range from circa 100 to 400 EJ year−1, and BECCS is expected to play an important role in achieving net zero carbon emissions5,29,30,31. Associated global land requirements have been estimated at between 3 and 7 million km2, with possible negative side effects for biodiversity and food security5,30,32. The UK Climate Change Committee recommends installing circa 67 TWh of BECCS electricity generation by 205033. Based on our Bioenergy value chain, over 7 million ha of land would need to be afforested by 2070 in order to fully meet BECCS ambitions exclusively with forest harvests (excluding high-quality sawn wood)—requiring a rate of planting 4.6 times higher, and continuing 20 years longer, than the 30,000 ha year−1 over 30 years considered in our study based on UK Committee on Climate Change recommendations4. Although a large area, this would bring total UK forest cover to around 42%, close to the European average of 40%34. Whilst purpose-grown bioenergy crops could deliver more rapid fossil fuel substitution using less land33, commercial forests combine the provision of high-quality materials into the circular economy with the delivery of multiple ecosystem services5,20, including medium-term climate regulation by terrestrial C storage35 and HWP C storage in the decades before BECCS is anticipated to become widely deployed4,31 (Table 2). Unlike many purpose-grown bioenergy crops, Sitka spruce can also produce reliable growth on marginal land that could be spared from extensive livestock production in the UK3.
Commercial afforestation can deliver significantly greater GHG mitigation than semi-natural afforestation largely due to the higher growth rate of conifers. Commercial investment in afforestation is based on the expectation of timber harvest and, to match current timber markets in the UK and the benefit of earlier harvest of faster-growing tree species, this generally leads to the planting of conifer rather than broadleaved species. Thus, faster-growing commercial forests deliver more, and longer-term, GHG mitigation than slower growing semi-natural forests. Depending on future decarbonisation and technology contexts, market demand and environmental risks, high yielding conifer forests could be harvested36 for hierarchical wood use or for bioenergy (with CCS), or left in the ground to maximise terrestrial C storage. The latter option can be chosen late in the forestry cycle in response to relevant market, environmental and/or policy signals. Commercial forestry therefore provides a robust strategy for GHG mitigation across a wide range of future contexts, at least in temperate zones, and merits a prominent role in climate policies, including nationally determined contributions under the Paris Agreement, and the forthcoming EU Forest Strategy36.
Our results pertain to regions with commercial forest rotations of 50 years (or less). In regions (e.g., boreal) with slower tree growth rates and longer forestry cycles, leaving wood unharvested could be a better mitigation option over the next century5,18,36. We applied a 100-year cut-off to our analysis to maintain a realistic time horizon for climate policy decision making, and to avoid deeply uncertain marginal technologies beyond this time horizon. A longer time horizon is likely to favour harvested commercial forests owing to saturating carbon sequestration in conservation forests (Fig. 2). There is some uncertainty about whether old forests may in fact continue to act as significant carbon sinks19,37,38. Unexpected losses from pests, pathogens, fires, windthrow and drought-caused mortality pose an increasing risk to GHG mitigation from affected areas, but such losses will not necessarily affect commercial forests more than conservation forests. In fact, active management and periodic harvesting of commercial forests can reduce fire risks39,40 and safeguard carbon stocks within HWPs whilst climate change increases environmental risks to old forests.
Whilst results in this paper demonstrate the comparatively high long-term GHG mitigation efficacy of commercial forests compared with unharvested conservation forests, it is imperative to note that commercial and conservation forests deliver different suites of important ecosystem services and should be considered complementary and not conflicting land uses5. Rather than limiting the area of commercial forests in favour of semi-natural forests6, more emphasis should be placed on rapid deployment of both forest types, and on the cascading use of harvested wood to derive maximum economic and mitigation value. Although our modelled commercial forestry system is 100% Sitka spruce, single species forests are not the only commercial option, and there is increasing support for mixed-species conifer forests (or conifer-broadleaf mixtures), under sustainable forest management to deliver both a high yield of wood products and other ecosystem services20,41. Diversification of commercial forestry could also enhance resilience to pests, diseases and climate change effects42,43,44. Nabuurs et al.8 argue for policy changes to encourage such ‘climate-smart forestry’, claiming it could deliver an extra 441 Mt CO2e year−1 mitigation across Europe by 2050. National afforestation strategies should promote a portfolio of commercial, conservation and agroforestry systems tailored to local conditions and adapted to climate change5,45, in order to deliver the range of ecosystem services required by society, in addition to GHG mitigation46. To achieve this there is a strong case to increase the 30,000 ha year−1 UK afforestation area target of the Committee on Climate Change, which is very modest in the context of international ambitions for increased tree canopy cover, such as the 0.9 billion hectares identified by Bastin et al.47, or indeed the EU Forest Strategy objective to plant 3 billion trees by 203036. Successful forest policy will also need to integrate social outcomes, and engage local stakeholders in strategic planning41.
We conclude that fast-growing tree species should be a major component of national afforestation strategies in order to achieve ambitious GHG mitigation targets. Commercial investment will favour such high production forests of species that produce timber matching market demand. The GHG mitigation potential of commercial forestry is robust against future decarbonisation scenarios, and will continue to deliver mitigation well beyond the 100-year timeframe considered in this study, when conservation systems have reached their peak capacity. Furthermore, commercial forestry can deliver similar long-term mitigation when wood is used in either hierarchical or bioenergy value chains, potentially contributing to future circular bioeconomy, energy security and carbon removal objectives as required at the time of harvest. However, it takes time to establish large areas of new forest. In addition to the time lag between forest establishment and GHG mitigation, especially pronounced when considering mitigation from commercial forest hierarchical value chains, there is a time lag in implementation of national afforestation policies owing to constrained planting rates48. Whilst sustainable intensification3 and curtailed demand for livestock products5,31,49 are projected to free up substantial land for afforestation in the UK and elsewhere over coming decades, our results reveal the urgency of commencing a programme of large-scale tree planting if afforestation is to significantly contribute to Paris Agreement targets for the second half of this century1,48.
Aim and scenarios
This study seeks to determine the most effective afforestation strategy for achieving climate change mitigation in a temperate region. Specifically, it aims to generate new evidence on the comparative long-term (100-year) GHG mitigation efficacy resulting from the establishment of commercial forests and conservation forests on grassland in the UK (baseline). We modelled 33 scenarios representing common temperate commercial and conservation forestry typologies, tree growth rates (m3 ha−1 year−1: ‘yield class’) and HWP value chains (Table 1). Rationale for scenario development commensurate with study objectives and conclusions is fully elaborated in S1, and summarised below.
Commercial forestry was based on conifer (Sitka spruce) forests, with a conservative default YC of 18 m3 ha−1 year−1 (range 12–24)50, with intermediate forest thinning in year 21 of each rotation when 36% of the harvestable material is removed in HWP. Clear-fell harvest is implemented in year 50 (a conservative average for this species in UK conditions), followed by immediate replanting, enabling a second clear-fell in year 100. Non-merchantable biomass was assumed to be left to decay on site. Two predominant types of wood value chain were modelled, representing different wood use strategies: (i) a Hierarchical wood use strategy, with wood flow based on UK statistics and data from mills that maximise the value of wood products, and embodying the waste hierarchy51 (Fig. 3), i.e., wood is subject to cascading use via a prioritised order: durable wood product manufacturing, extending service life times, re-use, recycling, bioenergy generation and disposal52; (ii) a Bioenergy wood use strategy, in which high-value sawn wood is used in the construction sector (as in the Hierarchical wood use strategy), but all other wood, and end-of-life construction wood, is used for electricity generation to contribute to bioenergy targets4. Dynamic assessment of incurred and avoided emissions during future wood harvest and processing operations, construction material and fossil fuel substitution, and BECCS deployment, was applied based on decadal progression of marginal technologies in line with two sets of projections made by the UK Committee on Climate Change: ‘Core’ and ‘Further Ambition’ pathways4—detailed in Table 2. These pathways involve differing rates of fossil fuel replacement by low carbon and renewable technologies, and differing rates of CCS implementation across industry sectors, representing different future contexts in which forestry value chains could exist. Note that fossil fuels remain the marginal source of dispatchable energy generation well into the future, especially for industrial heat, despite renewable energy technologies predominating24. Very few studies to date consider the timing of GHG emissions41 and avoided GHG emissions in this way.
Forests may be established for varying conservation objectives, from habitat provisioning to terrestrial carbon storage5,7. We represented a diverse range of possible conservation (unharvested) forest types based on different ratios of conifer (Sitka spruce, Corsican pine, Douglas fir) to broadleaf (silver birch, rowan, oak) trees (Table 1). The 100%-conifer conservation forest (YC 18) represents carbon sequestration prioritisation and provides an unharvested comparator for the equal-YC commercial forests. Meanwhile, the semi-natural 100%-broadleaf forest represents prioritisation of habitat provisioning, and delivers much lower rates of carbon sequestration owing to slow growth (YC 4)—representative of broadleaf forests grown on lower grade land in UK50. Among a range of intermediate conservation forests, the default conservation comparator, delivering a mix of carbon sequestration and habitat provisioning, was a 50:50 conifer:broadleaf mix with YC 11. Yield classes for 100% Sitka spruce (18) and 100% broadleaved (4) are for the same site conditions.
Scenarios were analysed at two scales: 1 ha planted in 2020, and a national scenario of 30,000 ha year−1 planted from 2020 to 2050 as per UK climate recommendations4,17 on 900,000 ha of lower-quality grassland that could be taken out of livestock production through intensification3 and/or reduced market demand for livestock products4,49. We assume that social and political change will lead to sufficient land being available, therefore, avoided GHG emissions from reduced livestock production or additional emissions from livestock production displacement are not considered. Analyses were cut off at 2120 in both scenarios, representing a maximum time horizon for climate policy. Climate change impacts on forest productivity were not included due to the already high complexity of the scenarios.
Life cycle assessment goal and scope
We applied dynamic consequential LCA22 to evaluate the GHG emissions balance of afforesting one hectare of grassland in the UK, accounting for terrestrial (soil and biomass) carbon storage, HWP carbon storage, substitution of materials and fossil fuels and long-term sequestration of biogenic carbon via future deployment of BECCS, over a 100-year period. Expanded LCA boundaries (Fig. 4) encompassed: (i) land use change due to afforestation on spared agricultural grassland; (ii) forest establishment; (iii) forest growth; (iv) forestry operations; (v) debarking; (vi) sawmilling (including drying, planning and chemical treatment); (vii) wood panel production; (viii) paper and paperboard production; (ix) bioenergy generation, including BECCS; (x) credits for avoided use of fossil fuels (substituted energy generation and mineral construction material production); (xi) carbon storage in HWPs related to ‘decay’ (retiral) functions53 and (xii) recycling and disposal of retired HWPs, including via (ix). The production and transport of all material and energy inputs were accounted for, as were the construction or manufacture of infrastructure and capital equipment. Full life cycle inventories are provided in Supplementary Data 2 and Supplementary Data 3, with an example for the Hierarchical wood use value chain in Supplementary Table 1 (S1). Material flows were derived using UK data from a combination of forest carbon modelling54, harvest data from over 2,000 ha of commercially managed forests, data form a commercial sawmill that maximises sawn wood output, national recycling data55 and timber-use statistics56—elaborated in S1. Given the focus of this paper on GHG mitigation, only the global warming potential (GWP100) impact category was evaluated, expressed as kg CO2e. Limitations are explored in the Discussion.
Forest growth, decay and harvest volumes were calculated using the Carbon Budget Model for the Canadian Forest Sector (CBM-CFS3)54, because it complies with the Intergovernmental Panel on Climate Change guidance53, was developed for similar climate conditions to the UK and provides default volume to biomass equations for Sitka spruce and Douglas fir (which are native to Canada), and genus equations for the other species in this study. It was parameterised using best-fit yield tables from Forest Yield, the standard yield model for forest management in the UK50. For conservation forests, aggregate group YCs were calculated based on weighted mean YCs for the species mixes described in Table 1. CBM-CFS3 outputs include annual soil and biomass carbon stocks and flows of carbon in harvested timber. Harvested carbon from CBM-CFS3 was converted to merchantable volume based on a 49.95% carbon content in wood dry matter57. Detailed material flows are presented in Supplementary Data 2 and Fig. 3 for the Hierarchical wood use strategy, and in Supplementary Data 3 for the Bioenergy wood use strategy.
Process emissions and carbon storage
All emissions associated with the production and transport of forestry inputs and all primary and secondary wood processing phases were extracted from Ecoinvent v.3.558 using OpenLCA v1.7.4 and scaled in Microsoft Excel using the HWP material flow (Supplementary Data 2 and Supplementary Data 3). Emissions from landfill disposal were calculated according to the IPCC First Order Decay method53. Retirement rates of HWP were calculated according to IPCC methods59, with modified decay factors60. As products retire from the HWP carbon pool, they are recycled or disposed of (by incineration or landfill) in proportions calculated according to UK recycling statsistics55 (Fig. 3). Retired tertiary products (i.e., products that have already been recycled once) are conservatively assumed to be disposed of. Horticultural mulch is assumed to decay at a rate similar to composted municipal solid waste61. Wood fuel is not included in the HWP carbon pools owing to rapid oxidation; return of this biogenic carbon to the atmosphere from the forest ecosystem is represented in the deficit between ecosystem carbon loss at the point of harvest, HWP carbon storage gain and loss from recycled materials.
Fuel-to-energy conversion factors (for coal, natural gas and wood chips) were taken from Ecoinvent unit processes58 to calculate fossil fuel substitution by dedicated biomass energy generation and incineration with energy recovery for wood waste. Emission avoidance through substitution of mineral construction materials was estimated by translating the final mass of construction timber (150 tonnes at 20% moisture per ha thinned forest) into an area of timber-framed wall using industry standard design: 0.0175 m3 of timber per 1 m2 wall (BRE IMPACT database62 accessed via eToolLCD® software—Supplementary Table 1). Then, 1 m2 of timber frame wall replaces 1 m2 of single skin, 140 mm concrete block and mortar (sand:cement ratio 10:3) wall with 10-mm jointing in typical UK house construction. Avoided emissions were then calculated using emission factors from Ecoinvent for the manufacture of concrete blocks, sand and cement. Projected decarbonisation of the cement sector is represented in Core and Further Ambition contexts (Table 2). Assumptions about substitution are elaborated in S1, and reflect marginal changes associated with additional wood supply (e.g., an increase in timber frame construction, hence substitution of mineral construction materials). CCS deployment is gradually increased on a decadal basis, at a faster rate for the Further Ambition context, and applied equally to marginal (substituted) fossil fuel and wood electricity generation (Table 2 and S1).
Recent papers have highlighted the uncertain assumptions inherent in wood product substitution estimates15,27. This study presents a methodological approach that addresses key limitations by considering different value chains and dynamic product counterfactuals under different decarbonisation pathways. To further explore the complexity and uncertainty of future wood value chains, we modelled alternative product substitution assumptions to assess the sensitivity of model results to product substitution. Details of these are provided in S1 and Supplementary Data 5, summarised in Table 3. We also modelled an alternative decarbonisation scenario in which there is no deployment of CCS during the study timeframe (Supplementary Data 6 and Supplementary Data 7), to evaluate the dependency of results on this technology.
Further information on research design is available in the Nature Research Reporting Summary linked to this article.
The authors declare that the data supporting the findings of this study are available within the paper and its supplementary information and data files: S1 for elaboration of scenarios and assumptions, Supplementary Data 1 for projected energy and product emission intensities, Supplementary Data 2 and Supplementary Data 3 for Hierarchical and Bioenergy wood use strategies, respectively, Supplementary Data 4 for graphs, Supplementary Data 5 for sensitivity analyses on substitution effects, Supplementary Data 6 and Supplementary Data 7 for full Hierarchical and Bioenergy inventory results, respectively, without future deployment of carbon capture and storage (sensitivity analyses). Background data were generated using the publicly available CBM-CFS3 model and extracted from the Ecoinvent v.3.5 database. All subsequent calculations were undertaken using standard MS Excel functions.
Masson-Delmotte, V. et al. Global warming of 1.5 °C An IPCC Special Report on the impacts of global warming of 1.5 °C above pre-industrial levels and related global greenhouse gas emission pathways, in the context of strengthening the global response to the threat of climate change, sustainable development, and efforts to eradicate poverty. Summary for Policymakers Edited by Science Officer Science Assistant Graphics Officer Working Group I Technical Support Unit. https://report.ipcc.ch/sr15/pdf/sr15_spm_final.pdf (2019).
Grassi, G. et al. The key role of forests in meeting climate targets requires science for credible mitigation. Nat. Clim. Chang. 7, 220–226 (2017).
Lamb, A. et al. The potential for land sparing to offset greenhouse gas emissions from agriculture. Nat. Clim. Chang. 6, 488–492 (2016).
UK CCC. Net Zero: The UK’s contribution to stopping global warming. https://www.theccc.org.uk/wp-content/uploads/2019/05/Net-Zero-The-UKs-contribution-to-stopping-global-warming.pdf (2019).
IPCC. Climate Change and Land. An IPCC Special Report on climate change, desertification, land degradation, sustainable land management, food security, and greenhouse gas fluxes in terrestrial ecosystems. www.ipcc.ch (2019).
Lewis, S. L., Wheeler, C. E., Mitchard, E. T. A. & Koch, A. Restoring natural forests is the best way to remove atmospheric carbon. Nature 568, 25–28 (2019).
Nabuurs, G. J. et al. Forestry. In Climate Change 2007: Mitigation. Contribution of Working Group III to the Fourth Assessment Report of the Intergovernmental Panel on Climate Change (ed. Nabuurs, G. J.) 1–44 (Cambridge University Press, 2007).
Nabuurs, G.-J. et al. By 2050 the mitigation effects of EU forests could nearly double through climate smart. Forestry. For. 8, 484 (2017).
Brunet-Navarro, P., Jochheim, H., Kroiher, F. & Muys, B. Effect of cascade use on the carbon balance of the German and European wood sectors. J. Clean. Prod. 170, 137–146 (2018).
Harmon, M. E. Have product substitution carbon benefits been overestimated? A sensitivity analysis of key assumptions. Environ. Res. Lett. 14, 065008 (2019).
Hudiburg, T., Law, B., Moomaw, W., Harmon, M. & Stenzel, J. Meeting GHG reduction targets requires accounting for all forest sector emissions. Environ. Res. Lett. 14, 095005 (2019).
Lamers, P., Junginger, M., Dymond, C. C. & Faaij, A. Damaged forests provide an opportunity to mitigate climate change. GCB Bioenergy 6, 44–60 (2014).
Röder, M. et al. Understanding the timing and variation of greenhouse gas emissions of forest bioenergy systems. Biomass. Bioenergy 121, 99–114 (2019).
Sterman, J., Siegel, L. & Rooney-Varga, J. Does replacing coal with wood lower CO2 emissions? Dynamic lifecycle analysis of wood bioenergy. Environ. Res. Lett. 13, 015007 (2018).
Leskinen, P. et al. Substitution effects of wood-based products in climate change mitigation (European Forest Institute, 2018).
Forest Research. Forestry Statistics 2019. https://www.forestresearch.gov.uk/tools-and-resources/statistics/forestry-statistics/forestry-statistics-2019/ (2019).
UK CCC. Land use: Policies for a Net Zero UK—Committee on Climate Change. https://www.theccc.org.uk/publication/land-use-policies-for-a-net-zero-uk/ (2020).
Chisholm, R. A. Trade-offs between ecosystem services: Water and carbon in a biodiversity hotspot. Ecol. Econ. 69, 1973–1987 (2010).
Luyssaert, S. et al. Trade-offs in using European forests to meet climate objectives. Nature 562, 259–262 (2018).
Gamfeldt, L. et al. Higher levels of multiple ecosystem services are found in forests with more tree species. Nat. Commun. 4, 1340 (2013).
Hardaker, A., Pagella, T. & Rayment, M. Ecosystem service and dis-service impacts of increasing tree cover on agricultural land by land-sparing and land-sharing in the Welsh uplands. Ecosyst. Serv. 48, 101253 (2021).
Weidema, B. P., Ekvall, T. & Heijungs, R. Guidelines for Application of Deepened and Broadened LCA. https://pdfs.semanticscholar.org/8be5/9252f6790328a6360d506df522de78bbce4c.pdf (2009).
Naudts, K. et al. Forest management: Europe’s forest management did not mitigate climate warming. Science 351, 597–599 (2016).
Vandepaer, L., Treyer, K., Mutel, C., Bauer, C. & Amor, B. The integration of long-term marginal electricity supply mixes in the ecoinvent consequential database version 3.4 and examination of modeling choices. Int. J. Life Cycle Assess. 24, 1409–1428 (2019).
Braakhekke, M. C. et al. Modeling forest plantations for carbon uptake with the LPJmL dynamic global vegetation model. Earth Syst. Dyn. 10, 617–630 (2019).
Doelman, J. C. et al. Afforestation for climate change mitigation: Potentials, risks and trade‐offs. Glob. Chang. Biol. 26, 1576–1591 (2020).
Rüter, S. et al. Climate benefits of material substitution by forest biomass and harvested wood products: perspective 2030 (Johann Heinrich von Thünen Institute, Federal Research Institute for Rural Areas, Forestry and Fisheries, 2016).
Howard, C., Dymond, C. C., Griess, V. C., Tolkien-Spurr, D. & van Kooten, G. C. Wood product carbon substitution benefits: a critical review of assumptions. Carbon Balance Manag. 16, 9 (2021).
Muri, H. The role of large—scale BECCS in the pursuit of the 1.5 °C target: an Earth system model perspective. Environ. Res. Lett. 13, 044010 (2018).
Huppmann, D., Rogelj, J., Kriegler, E., Krey, V. & Riahi, K. A new scenario resource for integrated 1.5 °C research. Nat. Clim. Change 8, 1027–1030 (2018).
Van Vuuren, D. P. et al. Alternative pathways to the 1.5 °C target reduce the need for negative emission technologies. Nat. Clim. Chang. 8, 391–397 (2018).
Huston, M. A. & Marland, G. Carbon management and biodiversity. J. Environ. Manag. 67, 77–86 (2003).
Albanito, F. et al. Mitigation potential and environmental impact of centralized versus distributed BECCS with domestic biomass production in Great Britain. GCB Bioenergy 11, 1234–1252 (2019).
FAO. Global Forest Resources Assessment 2015 Desk Reference. www.fao.org/publications (2015).
Englund, O. et al. Beneficial land use change: strategic expansion of new biomass plantations can reduce environmental impacts from EU agriculture. Glob. Environ. Chang 60, 101990 (2020).
EC. EU Forest Strategy Roadmap. Ares(2020)6146005 − 30 October 2020. https://ec.europa.eu/info/law/better-regulation/ (2020).
Luyssaert, S. et al. Old-growth forests as global carbon sinks. Nature 455, 213–215 (2008).
Gundersen, P. et al. Old-growth forest carbon sinks overestimated. Nature 591, E21–E23 (2021).
Blanco, J. A. et al. Fire in the woods or fire in the boiler: implementing rural district heating to reduce wildfire risks in the forest-urban interface. Process Saf. Environ. Prot. 96, 1–13 (2015).
González-Olabarria, J. R. & Pukkala, T. Integrating fire risk considerations in landscape-level forest planning. Ecol. Manag. 261, 278–287 (2011).
Kurz, W. A., Smyth, C. & Lempriere, T. Climate change mitigation through forest sector activities: principles, potential and prioritiese. Unasylva 67, 61–67 (2016).
Fares, S., Mugnozza, S., Corona, P. & Palahí, M. Five steps for managing Europe’s forests: support resilience and promote carbon storage, say Silvano Fares and colleagues. Nature 519, 407–409 (2015).
Hof, A. R., Dymond, C. C. & Mladenoff, D. J. Climate change mitigation through adaptation: the effectiveness of forest diversification by novel tree planting regimes. Ecosphere 8, e01981 (2017).
Roberts, M. et al. The effect of forest management options on forest resilience to pathogens. Front. Glob. Chang. 3, 7 (2020).
Dymond, C. C. et al. Diversifying managed forests to increase resilience. Can. J. Res 44, 1196–1205 (2014).
Li, Y. et al. Local cooling and warming effects of forests based on satellite observations. Nat. Commun. 6, 1–8 (2015).
Bastin, J. F. et al. The global tree restoration potential. Science 364, 76–79 (2019).
Brown, C., Alexander, P., Arneth, A., Holman, I. & Rounsevell, M. Achievement of Paris climate goals unlikely due to time lags in the land system. Nat. Clim. Change 9, 203–208 (2019).
Springmann, M. et al. Options for keeping the food system within environmental limits. Nature 562, 519–525 (2018).
Matthews, R. W., Jenkins, T. A. R., Mackie, E. D. & Dick, E. C. Forest Yield: A Handbook on Forest Growth and Yield Tables for British Forestry. https://www.forestresearch.gov.uk/research/forest-yield-a-handbook-on-forest-growth-and-yield-tables-for-british-forestry/ (2016).
European Commission. Directive 2009/31/EC of the European Parliament and of the Council of 23 April 2009 on the geological storage of carbon dioxide and amending Council Directive 85/337/EEC, European Parliament and Council Directives 2000/60/EC, 2001/80/EC, 2004/35/EC, 2006/. Official Journal of the European Union vol. L140/114 114–135 (2009).
Sikkema, R., Dallemand, J. F., Matos, C. T., van der Velde, M. & San-Miguel-Ayanz, J. How can the ambitious goals for the EU’s future bioeconomy be supported by sustainable and efficient wood sourcing practices? Scand. J. Res. 32, 551–558 (2017).
IPCC. 2006 IPCC Guidelines for National Greenhouse Gas Inventories Volume 4 Chapter 4. http://www.ipcc-nggip.iges.or.jp/public/2006gl/pdf/4_Volume4/V4_04_Ch4_Forest_Land.pdf (2006).
Kurz, W. A. et al. CBM-CFS3: a model of carbon-dynamics in forestry and land-use change implementing IPCC standards. Ecol. Modell. 220, 480–504 (2009).
DEFRA. ENV23—UK statistics on waste—GOV.UK. https://www.gov.uk/government/statistical-data-sets/env23-uk-waste-data-and-management (2018).
Timber Trade Federation. TTF Statistical Review 2017: Industry Facts and Figures for the Year 2016. https://ttf.co.uk/download/ttf-statistical-review-2017/ (2017).
Lamlom, S. H. & Savidge, R. A. A reassessment of carbon content in wood: Variation within and between 41 North American species. Biomass. Bioenergy 25, 381–388 (2003).
Wernet, G. et al. The ecoinvent database version 3 (part I): overview and methodology. Int. J. Life Cycle Assess. 21, 1218–1230 (2016).
IPCC. 2006 IPCC Guidelines for National Greenhouse Gas Inventories Volume 4 Chapter 2. http://www.ipcc-nggip.iges.or.jp/public/2006gl/pdf/4_Volume4/V4_02_Ch2_Generic.pdf (2006).
Dymond, C. C. Forest carbon in North America: annual storage and emissions from British Columbia’s harvest, 1965–2065. Carbon Balance Manag 7, 8 (2012).
Bruun, S., Hansen, T. L., Christensen, T. H., Magid, J. & Jensen, L. S. Application of processed organic municipal solid waste on agricultural land—a scenario analysis. Environ. Model. Assess. 11, 251–265 (2006).
BRE. IMPACT database v5 (accessed via etool LCA software) (2018).
Forest Research. Forestry Statistics 2017. https://www.forestresearch.gov.uk/tools-and-resources/statistics/forestry-statistics/forestry-statistics-2017/ (2017).
Waring, R. H. A process model analysis of environmental limitations on the growth of Sitka spruce plantations in Great Britain. Int. J. Res 73, 65–79 (2000).
Price, A. & Macdonald, E. Growing Birch in Scotland for Higher Quality Timber. https://forestry.gov.scot/publications/forestry-business/small-scale-wood-processing/347-growing-birch-in-scotland-for-higher-quality-timber (2012).
BEIS. Cement Sector Joint Industry—Government Industrial Decarbonisation and Energy Efficiency Roadmap Action Plan. (2017).
Hamad, W. Y., Miao, C. & Beck, S. Growing the bioeconomy: advances in the development of applications for cellulose filaments and nanocrystals. Ind. Biotechnol. 15, 133–137 (2019).
This work was funded by the UK Natural Environment Research Council (NERC) Envision Doctoral Training Program. Additional CASE studentship funding was provided by Woodknowledge Wales (Ffarm Moelyci, Tregarth, UK) and Coed Cymru (The Forest Hub, Unit 6, Machynlleth, Powys, UK). The authors are grateful for expert advice received from Gary Newman (Woodknowledge Wales) and Gareth Davies (Coed Cymru) and for expert advice and data supplied by Stephen Ramage (Gresham House) and Rob MacKenna (James Jones and Sons Ltd.).
The authors declare no competing interests.
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Forster, E.J., Healey, J.R., Dymond, C. et al. Commercial afforestation can deliver effective climate change mitigation under multiple decarbonisation pathways. Nat Commun 12, 3831 (2021). https://doi.org/10.1038/s41467-021-24084-x