Ammonia :: Coniferous woodland

Effects and implications

[Ammonia is one of the key pollutants that contribute to nitrogen deposition. Please read the Nitrogen deposition - Coniferous Woodland record to understand the full impacts effects of nitrogen deposition including ammonia.]

  • Direct damage to spruce and pine tree foliage, for example, leaf discolouration, premature senescence and loss.
  • Increased sensitivity to drought and frost and increased risk of pest and pathogens attack
  • Reduced ability of stomata to close under drought conditions, leading to plant water stress (Van Hove et al. 1991, Erisman and Draaijers1995).
  • Loss of mycorrhiza and fruit bodies.
  • Increased rates of litter loss
  • Changes in the composition of groundflora, bryophyte and lichen communities. Changes in the under storey, increase in grasses and ruderal species.
  • Nitrification will be stimulated, increasing soil acidity.

Overview: evidence, processes and main impacts

Ammonia is a reactive water soluble alkaline gas that will deposit to acid surfaces and where acidic gases are also present in the atmosphere e.g. SO2 (through co-deposition). Coniferous woodlands tend to occur on acid soils and their vegetation also tends to provide an acidic surface, increasing their susceptibility to NH3. Also the rough surface helps increase rates of NH3 deposition especially at the woodland edge. The low N status of the foliage will also lead to enhanced deposition of NH3 to coniferous woodland.

Ammonia exposure significantly increases foliar N concentrations predisposing trees to biotic and abiotic stress.  Stomatal control appears to be sensitive to NH3 especially in Pines. High NH3 concentrations promote rapid uptake and accumulation of toxic ammonium ions in plant tissue. Severe damage has been frequently found in woodland edges adjacent to fields with high manure applications in the Netherlands and Belgium (van Herk 1999, 2002). Exceedance of the NH3 critical level is a local issue relevant near major sources such as intensive livestock farms, manured fields or even wild bird colonies, but can also occur in predominantly agricultural areas (Sutton et al 2000). Damage to trees has been reported in the vicinity of farms in England and Scotland (UKCLAG 1996, Pitcairn et al. 1998).  Woodland ground flora will also be at risk as the trees only take up a small proportion of atmospheric NH3 (maximum < 20%). Scots pine, Pinus sylvestris, is a relatively low N demanding species growing on nutrient poor often sandy soils. NH3 might stimulate growth but with some reduction in carbohydrates to support ectomycorrhiza, leading to negative impacts on fruit body formation.

Woodlands on more acid soils may be more at risk because of the greater likelihood of deposition In the drier east, water stressed conditions, trees may be less sensitive if stomata work efficiently and close, excluding NH3 uptake. Invasion by ‘casual’ plants will be greater in areas where availability of a seed source for such plants is high. Although, depending of the age of the wood, opportunities for seedling establishment will be restricted by the ‘dark’ conditions.

Pollutant deposition type and risk areas

Type of pollutant

Form of N

Risk areas

Dry deposition

Gaseous

NH3

Woodlands in rural areas with elevated background concentrations for example close to intensive livestock agriculture.

Indicators of NH3 effects

These depend on concentration and deposition

  • Needle % N increase and especially amino acid content.
  • Increased litter production and canopy
  • Decreases in bryophyte and herb species richness
  • Under-storey with increased Ellenberg scores
  • Changes in under-storey species, with sensitive mosses and lichens likely to decline e.g.  increases in acid tolerant nitrophilic species (e.g. Deschampsia flexuosa) in non-fertilised Scots Pine stands over the last 20 to 40 years and decreases in Calluna vulgaris and Vaccinium vitis-idaea (Rodenkirchen 1992).
  • Algae growing on the trees
  • Reduction in faunal and floral biodiversity as dominant species take over.
  • Reduction in large sporocarps and diversity of mycorrhizal fungi.
  • Change in soil pH but depends on level of nitrification.
  • Increase in N content of upper soil horizons, with subsequent effects on soil processes, e.g. mineralization.

Examples of species specific responses

Some examples of specific responses are given in the table below. This does not represent a comprehensive review of all species impacts. 

Species

Response

Reference

Pinus sylvestris

Needle damage

Dueck et al 1990

P. nigra

Needle damage by Brunchorstia pineae and Sphaeropsis sapina (NH3)

Roelofs et al 1985

Critical Load/Level: 
Habitat/ Ecosystem Type Critical Load/ Level Status Indication of exceedance Reference
Higher plants

3 µg NH3 m-3 annual mean (uncertainty of 2-4 µg NH3 m-3)

UNECE, 2007

Direct visible injury; species composition changes. Ecosystems where sensitive lichens and bryophytes are an important part of the ecosystem integrity, the critical level is set at 1 µg NH3 m-3.

860
References: 
Dueck, T.A.; Dorèl, F.G. ; R.T., Horst ; Van der Eerden, L.J.M. 1990 Effects of ammonia, ammonium sulphate and sulphur dioxide on the frost sensitivity of Scots pine (Pinus sylvestris L.) Water Air Soil Pollution 54 35-49
Erisman, J.W.; Draaijers, G.P.J. 1995 Studies in Environmental Science 63
Hove, L.W.A.; van Kooten, O. ; van Wijk, K.J ; Vredenberg, W.J.; Adema, E.H.; Pieters, G.A. 1991 Physiological effects of long term exposure to low concentrations of SO2 and NH3 on poplar leaves. Plant Physiology 82 32-40
Pitcairn, C.E.R.; Leith, I.D.; Sheppard, L.J.; Sutton, M.A.; Fowler, D.; Munro, R.C.; Tang, S.; Wilson, D. 1998 The relationship between nitrogen deposition, species composition and foliar nitrogen concentrations in woodland flora in the vicinity of livestock farms. Environmental Pollution 102 41-48
Roelofs, J.G.M.; Kempers, A.J. ; Houdijk, A.L.F.M. ; Jansen, J. 1985 The effects of air-borne ammonium sulphate on Pinus nigra in the Netherlands Plant Soil 42 372–377
Sutton, M.A.; Dragosits, U.; Tang, Y.S.; Fowler, D. 2000 Ammonia emissions from non-agricultural sources in the UK. Atmospheric Environment 34 855 - 869
Van Herk, C.M.; Nimis, (Eds) P.L.; Scheidegger, (Eds) C.; Wolseley, P.A. 2002 Monitoring with Lichens - Monitoring Lichens Nato Sciences 285-290

This page was accessed on Saturday, July 21, 2018 12:32