Forestry and Peatlands Norway
The importance of forestry
Forest and wooded land cover 12 million hectares and constitute 37% of the land area in Norway. The most important species are Norway spruce (47%), Scots pine (33%) and birch (18%) (1). The productive forest land covers only 24.1 % of total land area. About one third of this area is “mountain forests” where climate restricts growth and reproduction either directly or indirectly. Low temperatures in the growing season and episodes of strong wind are the main restrictions to these forests, while availability of water is regarded adequate or in surplus (8).
Norway has long traditions in forestry and forest management, and for using wood in construction and as a source of energy. Sawn wood and round wood have been important exports for more than 500 years (1).
During the last 80 years the annual harvest has been considerably lower than the annual increment, resulting in both growing stock and annual increment exceeding twice the level documented by the first National Forest Inventory in the 1930’s (1).
Benefits from climate change
Globally, based on both satellite and ground-based data, climatic changes seemed to have a generally positive impact on forest productivity since the middle of the 20th century, when water was not limiting (21).
The tree line is predicted to shift upward by several hundred metres (2). There is evidence that this process has already begun in Scandinavia (3). Warmer temperatures and higher CO2 levels may increase the potential timber harvest in northern Europe. The northward expansion of forests is projected to reduce current tundra areas under some scenarios. There are no obvious climate adaptation options for either tundra or alpine vegetation (4).
The genetic variation in Norwegian forests is large, so the basis for natural selection should be fairly good. Species requiring warm summers will expand at the expense of Norway spruce, while Scots pine, usually growing on shallow and nutrient poor soils, will be more competitive and stay more stable. The mountain forests will respond greatly resulting in improved growth and reproduction (8).
The productive forest area is likely to expand considerably. A significant part of the present deciduous forests above the timberline will become productive as well as a major part of the treed peatlands. Altogether this might increase the productive forest area by more than 30%. The full effects of the estimated climate changes will not eventuate in the projected 60-year period. It is likely that successions must go on for several forest generations. Even so, the perspectives for increased timber production in the next 60 years are fairly good (8).
The overall effects on forestry in Norway are likely to be positive in the end. When the forests have reached their dynamic stability, both forest productive area, genetical selection, species selection, timber production and ecosystem diversity will most likely be improved (8).
Timber production in Europe
Climate change will probably increase timber production and reduce prices for wood products in Europe. For 2000–2050 a change of timber production in Europe is expected of -4 to +5%. For 2050–2100 an increase is expected of +2 to +13% (19).
Vulnerabilities - Overview
The increased vulnerability of forests (and people) with respect to climate change refers to several impacts (10,20):
- Forest cover: conversion of forests to non-woody energy plantations; accelerated deforestation and forest degradation; increased use of wood for domestic energy.
- Biodiversity: alteration of plant and animal distributions; loss of biodiversity; habitat invasions by non-native species; alteration of pollination systems; changes in plant dispersal and regeneration.
- Productivity: changes in forest growth and ecosystem biomass; changes in species/site relations; changes in ecosystem nitrogen dynamics.
- Health: increased mortality due to climate stresses; decreased health and vitality of forest ecosystems due to the cumulative impacts of multiple stressors; deteriorating health of forest-dependent peoples.
- Soils and water: changes in the seasonality and intensity of precipitation, altering the flow regimes of streams; changes in the salinity of coastal forest ecosystems; increased probability of severe droughts; increased terrain instability and soil erosion due to increased precipitation and melting of permafrost; more/earlier snow melt resulting in changes in the timing of peak flow and volume in streams. The capacity of the forest ecosystem to purify water is an important service, obviating the cost of expensive filtration plants.
- Carbon cycles: alteration of forest sinks and increased CO2 emissions from forested ecosystems due to changes in forest growth and productivity.
- Tangible benefits of forests for people: changes in tree cover; changes in socio-economic resilience; changes in availability of specific forest products (timber, non-timber wood products and fuel wood, wild foods, medicines, and other non-wood forest products).
- Intangible services provided by forests: changes in the incidence of conflicts between humans and wildlife; changes in the livelihoods of forest-dependent peoples (also a tangible benefit); changes in socio-economic resilience; changes in the cultural, religious and spiritual values associated with particular forests.
Climate change is likely to increase the mean temperature in Norway and the frequency of climatic extremes, such as drought, floods, and storms. Under such conditions, there is high probability that forests will be subjected to increased frequency and intensity of stress due to climatic extremes. Some pathogens may increase their importance and new may arrive. More unstable winter climate may in the future give increased fungi attacks on the Norwegian forests. Longer and warmer growth season will give many pathogens and harmful insects better conditions. This might cause severe damage to the forest, resulting in reduced carbon stocks (1,8).
For the forests in northern Europe, the combination of raised mean temperature and a higher frequency of extreme events will have negative effects that could ultimately be of greater importance than the positive outcomes of a warmer climate. The boreal forests, for example, may be severely affected by summer dry spells and droughts, making trees more susceptible to frost damage, windthrow, storms and attacks by pests and diseases (5).
Increased precipitation, cloudiness and rain days and the reduced duration of snow cover and soil frost may negatively affect forest work and timber logging determining lower profitability of forest production and a decrease in recreational possibilities (6).
Differences in precipitation
Precipitation of more than 5000 mm has been measured at some distance from the coastal line in the fjords of southwestern Norway. The precipitation is generally much lower to the east of the mountain range, at some locations even extremely low, only 200-400 mm. The climatic contrasts between coastal and inland sites may increase if the predicted climate changes come true. The timberline can be moved vertically upwards about 200 m, less to the west of the mountain range and more to the east side (8).
The impact of higher CO2-levels
Norwegian forests today have large-scale nutrient deficiencies, especially of nitrogen. It is likely that this restriction will continue even at a changed climate. In addition, water restrictions in the growing season may become more frequent, at least in South-Central Norway. This means that elevated CO2 levels will not be fully effective and the forests will not achieve their potential growth capacity (8).
In Europe, the forested areas are the main source of groundwater, and they absorb precipitation and reduce the risk of excess surface flow and floods and erosion. In this respect, the groundwater resources in northern and western Europe are in no danger as is the case in central and southern Europe. The reduction of forest cover may increase surface flow and floods. In northern Europe, the increasing precipitation may also increase the risk of floods even though the forest cover buffers watersheds (8).
Vulnerabilities - Non-timber products
Increasingly there are concerns about the productivity of non-timber products such as medicines and foods. Relatively little information is available in the scientific literature about the sustainable management of such products, and even less is known about their vulnerability to climate change (10).
In general, management has a greater influence on wood production in Europe than climate or land-use change. Forest management is influenced more strongly by actions outside the forest sector, such as trade and policies, than from within (7).
Increased wind damages, especially in northern and western Europe, may more frequently result in an imbalance in orderly harvesting procedures with increased costs and disturb timber markets with an imbalance between the supply and demand of timber (8).
Vulnerabilities - peatlands
Peatlands cover a large portion of the land area in the Nordic countries. In Finland about 30% of the land area is covered with peat of varying thickness, in Sweden 25%, in Iceland 10% and in Norway 8%. Parts of these peatlands are being used for agriculture, often as grassland for cattle and milk production. In Finland and Sweden, for instance, organic agricultural soils cover 10% and 7% of the agricultural land area, respectively (22).
The development of new drainage techniques at the beginning of the 20th century has accelerated the exploitation of peatland area and altered patterns of use. In the Nordic countries between 3% and 40% of the original peatland area has been drained for agricultural purposes. In some regions, e.g. in Finland, more than 50% of the peatlands are drained for forestry and only 3% for agriculture. Land drainage in all the Nordic countries was largely a government driven policy to mitigate severe socio-economic risks related to emigration to USA, food security, unemployment and poverty (23).
Drainage for agriculture leads to land subsidence
Drained organic soils differ significantly from mineral soils as they subside over a relatively short time period due to compaction, shrinkage, erosion and oxidation. Cultivation in Nordic conditions leads to subsidence rates that can vary from 0.5 cm/year on fields with pasture to 2.5 cm/year on fields with row crops (24). This subsidence leads to loss of organic matter, leaching of nutrients, mineralization of carbon and nitrogen and therefore emission of greenhouse gases carbon dioxide (CO2) and nitrous oxide (N2O).
Agricultural peatlands require repeated lowering of drainage as subsidence alters the effectiveness of the original drainage system with reduced bearing capacity and lower yields. Ultimately, long-term agricultural usage of peatland depends on the possibilities to redrain the peat, and the quality of underlying substrates and its suitability for long-term agriculture (22).
Drained peatlands emit greenhouse gases
Organic soils are responsible for a significant portion of the anthropogenic CO2 and N2O emissions (25). N2O emission is particularly relevant since N2O is a 300 times more effective greenhouse gas than CO2. Drainage of peatlands changes the hydrology and microbiological processes of the peat and therefore impacts gas exchange from the peat dramatically. Greenhouse gases emissions associated with peat extraction, peatland forestry and agriculture have to be accounted for in national inventories on total emissions of greenhouse gases.
And draining peatlands has several other negative effects
Peatlands are important to mitigate regional flooding since they store water from heavy rainfall. Draining peatlands may therefore negatively impact flood protection. Also, ecosystem processes such as carbon sequestration and biodiversity are disturbed. Due to drainage, water flows more vertically through the topsoil layer leaching out nutrients, dissolved organic carbon, and in some cases metals (26).
The genetic variability of most common tree species is probably large enough to accommodate the mean changes in temperature and precipitation. Problems may be encountered with the changes in the frequency and amplitude of extreme events such as drought, wind and spring and summer frost. Currently there is a tendency to prefer native tree species and a more nature-oriented approach in management. Simulation studies in northeastern Germany suggest that there is a considerable potential to improve climatic adaptation of forests by means of adaptive forest management strategies (9).
Adaptation strategies - Forest management measures in general
The establishment of migration corridors from south to north between fragmented landscapes is reported as a means of aiding the migration of species responding to changed climatic conditions. Changing the species composition to form more stable forests is reported as a management option; an example is changing the species in southern Finland from spruce and pine to birch. In a similar context, Sweden has been working on a breeding programme aimed at developing trees that would be adapted to the projected future climate (11).
To adapt to shorter winter harvesting periods as well as soft soils and roads, new harvesting techniques that better suit new conditions need to be developed. It is also reported that in some regions increasing population levels of large game, in particular moose, will increase the need for game management (11).
Replacement of needle-leaved tree species by broad-leaved species
The boreal forest is experiencing higher rates of warming than any other forested region on the planet (33). Boreal forest fires not only impact greenhouse gas emissions, they also impact human health and safety, damage physical infrastructure, and result in losses of industrial timber. For instance, the 2010 wildfires around Moscow (Russia) were linked to roughly 11,000 deaths through their effect on air pollution (34). The 2016 Fort McMurray fire in Canada resulted in estimated losses of CAD$4.6 billion (32).
In 2015, needle-leaved forests represented 54% of the boreal biome. It is argued that increasing the broad-leaved tree composition is an effective way to adapt to the increased regional fire risk from climate change (32). Because of their higher leaf moisture content and lower flammability, broad-leaved tree species are less likely to burn than needle-leaved (35). Pure broad-leaved stands are about 24 times less likely to burn in a stand-replacing event than pure needle-leaf stands (36). Reducing the risk of wildfires (with regards to both frequency and spread) in boreal biomes through increased broad-leaved tree composition is therefore a means to reduce greenhouse gas emissions (32). Because of the higher year-round albedos of deciduous broad-leaved forests compared to evergreen needle-leaved forests, the earth would absorb less solar energy, thus having a cooling effect throughout the boreal zone (37).
A shift from mature needle-leaved to mature broad-leaved forest can reduce the fire risk between three to five times for many boreal forest regions (36). This shift can be made as part of regular management activities in actively managed forests. In southern Canada, for instance, converting just 0.1-0.2% of forested area per year, starting in 2020, may even be sufficient to mitigate the expected increase in fires due to climate change, scientists state (38).
The terms adaptation and adaptive management are often incorrectly used interchangeably. The former involves making adjustments in response to or in anticipation of climate change whereas the latter describes a management system that may be considered, in itself, to be an adaptation tactic (13). Adaptive management is a systematic process for continually improving management policies and practices by learning from the outcomes of operational programmes (14). It involves recognizing uncertainty and establishing methodologies to test hypotheses concerning those uncertainties; it uses management as a tool not only to change the system but to learn about the system (15).
Both the climate and forest ecosystems are constantly changing, and managers will need to adapt their strategies as the climate evolves over the long term. An option that might be appropriate today given expected changes over the next 20 years may no longer be appropriate in 20 years’ time. This will require a continuous programme of actions, monitoring and evaluation – the adaptive management approach described above (12).
There is a widespread assumption that the forest currently at a site is adapted to the current conditions, but this ignores the extent to which the climate has changed over the past 200–300 years, and the lag effects that occur in forests. As a result, replacement of a forest by one of the same composition may no longer be a suitable strategy (12).
Adaptation to climate change has started to be incorporated into all levels of governance, from forest management to international forest policy. Often these policies are not adopted solely in response to climate, and may occur in the absence of knowledge about longer-term climate change. They often serve more than one purpose, including food and fuel provision, shelter and minimizing erosion, as well as adapting to changing climatic conditions (11).
Socio-economic and political conditions have significant influences on vulnerability and adaptive capacity. Climate change projections are perceived by many forest managers as too uncertain to support long-term and potentially costly decisions that may be difficult to reverse. Similarly, uncertainty over future policy developments may also constrain action. Finance is a further barrier to implementing adaptation actions in the forest sector (16).
Any community currently dependent on forestry is at risk of destabilization, some more seriously than others. There is likely to be a high level of variation in the ability of forest-dependent communities to adapt to climate change, but there have been relatively few rigorous studies investigating this. One study in northern Europe revealed that the communities in Norrbotten (Sweden), Lappi (Finland) and Arkhangelsk oblast (Russia) differed markedly, primarily because of their varying degrees of dependence on natural resources and their ability to counteract negative effects (17). The greater the diversification of a local economy, the less its vulnerability to climate change is likely to be because of its ‘room for maneuver’ (18).
A country’s ability to adapt to climate change will depend largely on financial, human and institutional capacities; thus the more developed regions may adapt more easily than regions within less developed countries. As the boreal domain consists of comparatively few countries with well- developed economies, there are good grounds for adaptation (11).
Adaptation peatlands: how to stop subsidence and greenhouse gases emissions?
The negative consequences of using peatlands for agriculture as summarized above raise a few pressing questions. Should farming continue on peat soils? Can management choices reduce negative impacts? What alternatives exist and what are their socio-economic and environmental consequences? These questions were addresses in a recent review (22).
Afforestation is not the solution
Some say afforestation of drained peatlands, especially croplands, reduce the overall emissions of greenhouse gases. Indeed, CO2 emission of afforested former croplands can be lower than in arable croplands, although the effect depends strongly on the climatic conditions (27,28). In most cases, however, this is not true for the N2O emissions; these emissions can remain high for decades (29).
One solution: continue cultivation as long as this is profitable
According to the authors of this review there is little or no scientific evidence that changing cultivation methods or growing specific crops can reduce the emission of greenhouse gases. They recommend, therefore, that the sites that are cultivated should continue the cultivation as long as this is profitable. Crops should be managed in such a way as to ensure a maximum return for each CO2 equivalent emitted, they state, and this could be achieved by maintaining biomass levels as high as possible (22).
After cultivation, forestry or biocrops can be an option as an alternative land use, if the soil and drainage is suitable for such vegetation. Forestry or biocrops will not stop CO2 emission from the peatsoils and high N2O emissions may remain, but carbon will be sequestered. Some bioenergy crops can be productive even with a high water table level. For fields too wet to cultivate with agricultural crops, these bioenergy crops could prolong the life of the area as a productive field with the ability to sequester carbon in the biomass. Harvesting these crops on wet soils remains a challenge, however (22).
Another solution: change in land use
Rewetting has been recommended as a practice to protect organic material in former cultivated land from further mineralization by excluding oxygen, and thereby reducing the emission of greenhouse gases (30). It has also been proposed as a method to increase biodiversity. Rewetting must be accompanied by moisture tolerant crops (paludiculture) if one aims to continue agricultural use.
While the goal of rewetting often is to encourage the return of peat forming plants and the ecosystem services they provide such as carbon sequestration, it is not well known if these plants will grow on peat soils that have been altered by the process of drainage and management. Peat extraction followed by rewetting might provide a sustainable option as rewetting is often easier if the nutrient rich topsoil peat is removed, starting the peat accumulation from scratch. Also this provides a way to finance the after-use (22).
In the short term (0-5 years) rewetting can lead to a net increase in the emission of greenhouse gases because stopping drainage may lead to a high but fluctuating water table. A highly fluctuating water table can lead to an increase in CH4 emissions due to submersion of the active rooting layer leading to anoxic mineralization of labile carbon combined with a reduction in CH4 oxidation. In contrast, drained organic soils are only minor sources or even sinks for methane (CH4) (28). Thus it is important to ensure a high and relatively stable water table when drained organic soils are rewetted. Research in the Netherlands has shown that rewetting can restore the carbon sink function of managed peatlands after 15 years (31).
The references below are cited in full in a separate map 'References'. Please click here if you are looking for the full references for Norway.
- Ministry of the Environment of Norway (2009)
- Badeck et al. (2001), in: Alcamo et al. (2007)
- Kullman (2002), in: Alcamo et al. (2007)
- Alcamo et al. (2007)
- MICE (2005), in: Behrens et al. (2010)
- Maracchi et al. (2005)
- Schröter et al. (2005)
- Kellomäki et al. (2000)
- Lindner (2000), in: Kellomäki et al. (2000)
- Innes (ed.) (2009)
- Roberts (ed.) (2009)
- Innes (ed.) (2009)
- Ogden and Innes (2007), in: Innes (ed.) (2009)
- BCMOF (2006a), in: Innes (ed.) (2009)
- Holling (1978); Lee (1993, 2001), all in: Innes (ed.) (2009)
- Keskitalo (2008), in: Roberts (ed.) (2009)
- Lundmark et al. 2008, in: Innes (ed.) (2009)
- Thomas and Twyman (2006), in: Innes (ed.) (2009)
- Karjalainen et al. (2003); Nabuurs et al. (2002); Perez-Garcia et al. (2002); Sohngen et al. (2001), in: Osman-Elasha and Parrotta (2009)
- Kirilenko and Sedjo (2007)
- Boisvenue et al. (2006)
- Kløve et al. (2017)
- Runefeldt 2010), in: Kløve et al. (2017)
- Berglund (1989), in: Kløve et al. (2017)
- Kasimir-Klemedtsson et al. (1997); Maljanen et al. (2010), both in: Kløve et al. (2017)
- Saarinen et al. (2013), in: Kløve et al. (2017)
- Lohila et al. (2011), in: Kløve et al. (2017)
- Maljanen et al. (2010), in: Kløve et al. (2017)
- Maljanen et al. (2013), in: Kløve et al. (2017)
- Smith et al. (2007), in: Kløve et al. (2017)
- Schrier-Uijl et al. (2014), in: Kløve et al. (2017)
- Astrup et al. (2018)
- Gauthier et al. (2015), in: Astrup et al. (2018)
- Shaposhnikov et al. (2014), in: Astrup et al. (2018)
- Kasischke et al. (2010), in: Astrup et al. (2018)
- Bernier et al. (2016), in: Astrup et al. (2018)
- Bright et al. (2017), in: Astrup et al. (2018)
- Girardin and Terrier (2015), in: Astrup et al. (2018)