Nitrogen deposition

What is it?

Nitrogen (N) deposition describes the input of reactive nitrogen from the atmosphere to the biosphere both as gases, dry deposition and in precipitation as wet deposition. Enhanced reactive nitrogen deposition is a consequence of  global emissions of oxidised nitrogen (NO, HNO3 and NO2 – often referred to as NOy) from fossil fuel combustion (Dignon and Hameed, 1989), and reduced N (NHx) from agricultural sources. Effects of ammonia gas and dry deposition of ammonia (NH3) is addressed in a separate overview.

Emissions and Deposition

Oxidised Nitrogen

Dry deposition of nitrogen oxides is greatest within large conurbations and close to major highways, where annual mean concentrations can exceed 10 ppb. Nitrogen dioxide (NO2) is mostly emitted from motor vehicles and heating sources. Atmospheric oxidation produces nitric acid and particulate and aqueous NO3-, the main NOy components of wet deposition. Since 1986, UK emissions of NOx have declined by 50% (RoTAP 2012). However, annual average nitrate concentrations in rainfall have fallen by only 22% over the period 1986 to 2008. The relatively smaller fall in concentrations / deposition is thought to be due to a significant reduction in NO2 export (62%) (RoTAP 2012).

Reduced Nitrogen

Reduced nitrogen comprises mainly gaseous NH3, aerosol NH4+ and wet deposited NH4+ which are monitored throughout the UK in the wet and dry deposition networks (see UKEAP ). Wet deposition of reduced N comprises fine particulate ammonium (NH4+) salts or aerosols of acidic gases. These components have a relatively long atmospheric residence time, 4 to 15 days, and when removed by precipitation contribute to N deposition in remote ecosystems after long-range transport (Asman et al. 1998). Dry deposition of reduced N shows strong local-scale variability and is closely correlated to emissions from livestock emissions. The concentration of ammonium in wet deposition has fallen by around 35% over the period 1986 to 2005 (RoTAP 2012). Emissions of NH3 in the UK peaked in the 1980s and have decreased by about 15% since then. Relative to trends in emissions of SO2 or NOx, the decline in NH3 emissions is small (RoTAP 2012).

In 2008 the amounts of reduced (175 Gg-N yr-1) and oxidised (178 Gg-N yr-1) forms of N in deposition were approximately equal. However, proportions of NH4+ and NO3- ions in precipitation, like the ecosystems they deposit to, are not equally distributed spatially, reflecting in part the non-uniform distribution of their sources (RoTAP 2012).

In addition, the loading of N in wet deposition depends not only on the amount of N but also the amount of precipitation. In the east, N concentrations can be quite high due to the low rainfall, whereas in the west the rainfall is much higher but the concentrations tend to be lower. Reduced N will dominate deposition in rural areas while oxidised N dominates in urban conurbations.

Nitrogen Deposition effects on habitats and species 

Nitrogen is a major growth nutrient: all plants need N in order to grow. It is a major constituent of assimilatory and structural tissue, facilitating conversion of CO2 to carbohydrate and combining with carbon (C) to form amino acids (Marschner 2005).

Vascular plants take up most of their N through their roots but some can be absorbed above ground via stomata (gases) or the cuticle. Non vascular plants can absorb N through their entire surface (e.g. lichens and bryophytes). Most plants use reactive N, but some can use organic N, e.g. amino acids. If carbon (C) assimilation is restricted, e.g. by insufficient phosphorous (P), light or water, then N can potentially accumulate to excess and become toxic. In other words, N no longer acts as a nutrient rather it becomes a pollutant. Too much N is accepted as one of the main drivers of biodiversity change across the globe (Sala et al 2000).

Communities most at risk from N eutrophication are those rich in bryophytes and where species richness is comprised of slow growing species. Many semi-natural plants do not have the capacity to assimilate nitrogen in the presence of increased N availability (from N deposition) and can be outcompeted by plants that can, e.g. many graminoids (grass) species. This species loss is caused by shading or an inability to compete for other limiting resources. Low growing species such as forbs and non vascular plants are especially at risk. Such species replacements can lead to loss of specialised communities and ecosystems, e.g. heathland transformed into grassland in the Netherlands (Bobbink and Heil, 1993).

Steven et al, 2011 found that changes in both species occurrence and three ecosystem function indices (canopy height, specific leaf area and Ellenberg N) often occur at low levels of N deposition (<10 kgN/ha/yr). This is sometimes lower than established critical loads indicating that they are not set at a level which prevents an impact to all species or ecosystem functions. Changes in species occurrence and indices of ecosystem function also progressively continue as N deposition levels continue rising above the current critical load values. This indicates that ongoing damage occurs above the critical load and there are some benefits from reductions in deposition even if it remains above the critical load.

N deposition can also increase the risk of damage from abiotic factors, e.g. drought (summer and winter) and frost. Where N deposition leads to enhanced foliar N concentrations there is increased risk of damage from pests and pathogens both above and below ground. Detrimental impacts of N below-ground include loss of species diversity with respect to ectomycorrhiza and reductions in decomposer populations, e.g. enchytraeid worms. Nitrogen can also increase litter fall, reducing the amount of light passing through to ground dwelling species.

Habitat management is often used to maintain the balance between slow and fast growing species in some systems. However, getting the balance right between management intervention and N deposition is a complex issue of optimising positive and negative outcomes.  Give link and reference to this recent review.... Review of the effectiveness of on-site habitat management to reduce atmospheric nitrogen deposition impacts on terrestrial habitats 

N deposition can also cause acidification of soils. More details on the effects of acidification can be read here.

While direct toxicity from wet N deposition is less common, except among non-vascular plants, dry deposition of NH3 can cause toxicity (Marschner 1995). Plants can only control uptake through the stomata. However, mechanisms can be damaged by NH3 which facilitate greater uptake (see Ammonia overview).

Does the form of N make a difference?

For assessment of effects it used to be assumed that nitrogen originating from NHy or NOX has the same ecological effect (Sutton and Fowler 1993, Hornung et al. 1995). Currently, critical loads for N deposition do not distinguish between reduced and oxidised N.

UK wide survey work and manipulation studies have shown that the form of N deposition does affect outcomes, but the situation is complex; responses may be species specific or not apparent (i.e. species are insensitive to form and only the N dose matters). Furthermore, both forms can be damaging to species, but the mechanisms underpinning the damage may be quite different, e.g. Sphagnum capillifolium is sensitive to both reduced and oxidised N, the former probably mediated by accumulation and toxicity and the latter via increasing cellular pH (Sheppard et al 2014). In addition, both above and below ground transformations of the deposited N form can occur (Stevens et al 2010).

Smart et al. (2004) applied model estimates of NOy and NHx deposition across the UK for 1996 to explain national scale fine-grained changes in species composition between paired fixed plots from two Countryside Surveys, 1990 and 1998 (Haines-Young et al. 2000). These surveys established a significant positive relationship between NHx and cover weighted Ellenberg fertility scores for semi-natural grasslands, heaths and bogs. Stevens et al. (2006) concluded that, among NVC U4 grasslands, species richness and cover of forbs declined significantly, particularly in response to NH4+-N deposition. However, it should be pointed out that such surveys cannot distinguish between wet and dry NHx. It is predicted that dry deposition presents the greatest threat (Krupa, 2003; Sheppard et al 2011).

Dose Effects

There is global acceptance that once N deposition exceeds the demands of sensitive plants, semi-natural ecosystems are at risk of species loss and changes in structure and function (Bobbink et al 2011). However, what is not always clear is what drives the changes; is the vegetation responding to dose or concentration, and is it the annual or cumulative load that is important, is the response linear or does it show a threshold? Several studies have shown that the concentration of ions in wet deposition, together with application frequency, can exacerbate the effect of dose (Pearce and van der Wal 2008: Sheppard et al 1998).  Non-vascular plants are particularly sensitive to high concentrations and repeated exposures as these challenge their ability to both repair and recover from the damage. Thus N damage must be considered in terms of more than just the load. The role of cumulative N load has been discussed by Phoenix et al (2012) using data from long-term N manipulation experiments undertaken in the UK (UKREATE, 2010). The logic underpinning relationships with cumulative deposition are that N can remain in the soil and soil chemical reactions can respond like a bucket that becomes full and starts to overflow, but different systems may be represented by different size buckets and start at different levels. Factors determining the response to N are thus many and varied.

Modifiers of N responses: climate, other nutrients

Several manipulation studies have shown that N effects exacerbate sensitivities to climate extremes, e.g. drought, freezing stress and winter desiccation. Calluna appears to be particularly sensitive to abiotic stress and winter desiccation following enhanced N deposition (Sheppard et al 2008, Carroll et al 1999). Sensitivity to biotic stress from increased pest and pathogen activities is also much more common, e.g heather beetle (Berdowski and Zeilinga 1987; Berdowski 1993).

Sources of evidence showing or predicting N impacts

There is a wealth of information and reviews on nitrogen deposition impacts.  Some examples of these are listed in the table below. 

Reference

Ecosystem

Comments

Bobbink R., Hettelingh J.P. (eds) (2011).  

 

Majority terrestrial including swamps etc

Most recent evidence for setting N critical loads  based on manipulation studies in areas with relatively low ambient N and using realistic annual N doses and surveys.

Dise N.B., Ashmore M., Belyazid S., Bleeker A., Bobbink R., deVries W., Erisman J.W., Spranger T., Stevens C, van den Berg L. (2011)

 

 

Expert overview on N impacts on ecosystems at the European scale.

World Health Organisation (1997)

 

General

Information on form effects and mechanisms

RoTAP (2012)

 

Experts overview of soil and vegetation responses in UK’s ecosystems (up to 2008/9)

Source of atmospheric chemistry data, emissions and deposition

Stevens  C.J., Smart S.M., Henrys P.A., Maskell L.C., Crowe  A., Simkind J., Cheffings C.M., Whitfield C., Gowing  D.J., Rowe E.C., Dore A.J., Emmett B.A. (2012)

Acidic and calcareous grassland, heathland and bogs.

Used British Lichen Society database: presence of all lichen taxa growing in 10 km squares. Modelled (GAMS) probability of a taxa occurring at a given level of N deposition taking into account other drivers e.g. climate, change in sulphur deposition and land-use. Many taxa showed negative responses to N deposition with reductions in probability of presence with increasing N deposition. In all habitats, a mix of terricolous taxa showed negative or no significant relationship with N deposition.

 

Stevens  C.J., Smart S.M., Henrys P.A., Maskell L.C., Walker K.J., Preston C.D., Crowe  A., Rowe E.C., Gowing  D.J. Emmett B.A. 2011.

 

 

Acidic and calcareous grassland, heathland and Bogs.

Statistical analysis of eight independent national vegetation surveillance datasets using a consistent approach, to identify evidence of N deposition impacts. 

Emmett B.A., Rowe E.C., Stevens C.J., Gowing D.J.G., Henrys P.A., Maskell L.C., Smart S.M. (2012)

 

 

 

Used UK National vegetation datasets in relation to modelled N deposition to provide information on individual species sensitivity to N. Evaluated methods used to detect change. Collation of evidence of N impacts (including JNCC report 447) and consequences for UK biodiversity commitments.

Stevens C.J., Thompson K., Grime J.P., Long C.J., Gowing D.J.G.  2010.

 

 

Acid grasslands

The results suggest that soil acidification is the dominant process, as opposed to eutrophication and consequent competition between species, underpinning shifts in species composition and diversity linked to N deposition in calcifuge grasslands. Suggest this is due to soil acidification leading to lowered nutrient availability that prevent N stimulating growth.

Stevens C.J., Dise N.B., Mountford J.O., Gowing G.J.G. (2004)

 

Grasslands

Decline in forbs

Smart S., Ashmore M., Hornung M. et al. (2004)

 

Woodlands, semi-natural grasslands Heaths/Bogs.

Attempts to explain national-scale, fine-grained changes in plant species composition between 1990 and 1998 using model estimates of NOy and NHx deposition across Britain for 1996 (5 km square resolution)

NHx deposition estimates accounted for significant, but small components of between 1 km2 variation in the change in Ellenberg score in grasslands (5.6%) and heath/bogs (9.8%) but not woodland.

Stevens C.J., Manning P., van den Berg L.J.L., de Graaff M.C.C., Wamelink G.W.W., Boxman AW, Bleeker A., Vergeer P., Arroniz-Crespo M., Limpens J., Lamerse L.P.M., Bobbink R., Dorland E. 2011.

 

 

 

Review including effects on soil

van den Berg L.J.L., Vergeer P., Rich T.C.G., Smart S.M., Guest D., Ashmore M.R. (2010)

Calcareous grasslands

Compared permanent quadrat data at >100 sites on nature reserves from 1993-96 with 2006-09. High N deposition led to reduced species diversity and evenness and fewer characteristic and rare species.

Tipping E., P.A. Henrys P.A., Maskell L.C., Smart S.M. 2013.

Acid grassland, bogs, calcareous grassland, deciduous woodland, heath

Related Countryside Survey plant species richness km square data for GB in 1998 to modelled CBED 5x5km N deposition using a broken stick median regression, to estimate thresholds above which N deposition definitely has had an effect. Identified thresholds (kg N ha-1 a-1) at 7.9 for acid grassland; 14.9 for bogs; 23.6 for calcareous grassland; 7.8 for deciduous woodland and 8.8 for heath.

Cunha A., Power S.A., Ashmore M.R., Green P.R.S, Haworth B.J., Bobbink R. 2002.

Forests and components species rich grasslands wetlands heathlands

Good source of detailed information and references

References: 

Asman, W.A.H.; Sutton, M.A.; Schjoerring, J.K. 1998 Ammonia: emission, atmospheric transport and deposition New Phytologist 139 27-48
Berdowski, J.J.M.; Zeilinga, R. 1987 Transition from heathland to grassland: damaging effects of the heather beetle. Journal of Ecology 75 159-175
Berdowski, J.J.M. 1993 The effect of external stress and disturbance factors on Calluna dominated heathland vegetation. Heathlands: Patterns and Processes in a Changing Environment. 85-124
Bobbink, R.; Heil, G.W. 1993 Atmospheric deposition of sulphur and nitrogen in heathland ecosystems. Heathlands: Patterns and Processes in a Changing Environment. 25-50
Carroll, J.A.; Caporn, S.J.M.; Cawley, L.; Read, D.J.; Lee, J.A. 1999 The effect of increased deposition of atmospheric N on Cv in upland Britain. New Phytol 141 423-431
Cunha, A. ; Power, S.A. ; Ashmore, M.R.; Green, P.R.S. ; Haworth, B.J. ; Bobbink, R. 2002 Whole ecosystem N manipulation: An updated review
Dignon, J. ; Hameed, S. 1989 Global Emissions of Nitrogen and Sulfur-Oxides from 1860 to 1980 Japca-the Journal of the Air & Waste Management Association 39 180-186
Dise, N.B.; Ashmore, M.R.; S, Belyazid ; Bleeker, A.; Bobbink, R.; Vries, W.; Erisman, J.W.; Spranger, T. ; Stevens, C.J.; Van Den Berg, L.J.L. 2011 Nitrogen deposition as a threat to European Terrestrial Biodiversity European Nitrogen Assessment 463-494
Emmett, B.A.; Rowe, E.C. ; Stevens, C.J.; Gowing, D.J.; Henrys, P.A. ; Maskell, L.C. ; Smart, S.M. 2011 Interpretation of evidence of nitrogen impacts on vegetation in relation to UK biodiversity objectives
Haines-Young, R.H.; Barr, C.J.; Black, H.I.J ; Briggs, D.J.; Bunce, R.G.H.; Clarke, R.T.; Cooper, A.; Dawson, F.H.; Firbank, L.G. ; Fuller, R.M.; Furse, M.T.; Gillespie, M.K.; Hill, R.; Hornung, M.; Howard, D.C.; McCann, T.; Morecroft, M.D.; Petit, S.; Sier, A.R.J.; Smart, S.M.; Smith, G.M. ; Stott, A.P.; Stuart, R.C. ; Watkins, J.W. 2000 Accounting for nature: assessing habitats in the UK countryside.
Hornung, (Eds) M.; Sutton, (Eds) M.A.; Wilson, [Eds.] R.B. 1995 Mapping and modelling of critical loads for nitrogen - a workshop report.
Krupa, S.V. 2003 Effects of atmospheric ammonia (NH3) on terrestrial vegetation: a review Environmental Pollution 124 179-221
Marschner, H. 2005 Mineral Nutrition of Higher Plants Mineral Nutrition of Higher Plants 2 672
Phoenix, G.K. ; Emmett, B.A.; Britton, A.J.; Caporn, S.J.M. ; Dise, N.B.; Helliwell, R. ; Jones, M.L.M.; Leake, J.R.; Leith, I.D.; Sheppard, L.J.; Sowerby, A. ; Pilkington, M.G. ; Rowe, E.C. ; MR, Ashmore ; Power, S.A. 2012 Impacts of atmospheric nitrogen deposition: responses of multiple plant and soil parameters across contrasting ecosystems in long-term field experiments Global Change Biology 18 1197-1215
Sala, O. E.; Chapin, F. S.; Armesto, J. J.; Berlow, E. ; Bloomfield, J. ; Dirzo, R. ; Huber-Sanwald, E. ; Huenneke, L. F.; Jackson, R. B.; Kinzig, A. ; Leemans, R. ; Lodge, D. M.; Mooney, H. A.; Oesterheld, M. ; Poff, N. L.; Sykes, M. T.; Walker, B. H.; Walker, M. ; Wall, D. H. 2000 Biodiversity - Global biodiversity scenarios for the year 2100 Science 287 1770-1774
Sheppard, L. J.; Leith, I. D.; Mizunuma, T. ; Leeson, S. ; Kivimaki, S. ; Cape, J. N.; Dijk, N.; Leaver, D. ; Sutton, M. A.; Fowler, D.; Van den Berg, L. J.L.; Crossley, A.; Field, C. ; Smart, S. 2014 Inertia in an ombrotrophic bog ecosystem in response to 9 years' realistic perturbation by wet deposition of nitrogen, separated by form. Global Change Biology 20 566-580
Sheppard, L.J.; Leith, I.D.; Crossley, A.; Dijk, N.; Fowler, D.; Sutton, M.A.; Woods, C. 2008 Stress responses of Calluna vulgaris to reduced and oxidised N applied under 'real world conditions' Environmental Pollution 154 404-413
Sheppard, L.J.; Crossley, A.; Harvey, F.; Parrington, J.; White, C.C. 1998 Early effects of acid mist on Sitka spruce planted on acid peat. Phyton (Horn Austria) 39 1-25
Sheppard, L.J.; Leith, I.D.; Mizunuma, T. ; Cape, J.N.; Crossley, A.; S., Leeson ; Sutton, M.A.; Fowler, D.; Dijk, N. 2011 Dry deposition of ammonia gas drives species change faster than wet deposition of ammonium ions: evidence from a long-term field manipulation Global Change Biology 17 (12) 3589-3607
Smart, S.M.; Ashmore, M.R.; Hornung, M. 2004 Detecting the signal of atmospheric N deposition in recent national-scale vegetation change across Britain Water, Air and Soil Pollution: Focus 4 269–278
Stevens, C.J.; Thompson, K. ; Grime, J.P. ; Long, C.J. ; Gowing, D.J.G. 2010 Contribution of acidification and eutrophication to declines in species richness of calcifuges grasslands along a gradient of atmospheric nitrogen deposition. Functional Ecology 24 478-484
Stevens, C.J.; Smart, S.M.; Henrys, P.A. ; Maskell, L.C. ; Crowe, A. ; Simkin, J. ; Cheffings, C.M. ; Whitfield, C. ; Gowing, D.J.G. ; Rowe, E.C. ; Dore, A.J.; Emmett, B.A. 2012 Terricolous lichens as indicators of nitrogen deposition: Evidence from national records. Ecological Indicators 20 196-203
Stevens, C.J.; Dise, N.B.; Mountford, J.O.; Gowing, D.J. 2004 Impact of nitrogen deposition on the species richness of grasslands Science 303 1876-1879
Stevens, C.J.; Manning, P. ; Van Den Berg, L.J.L. ; De Graaf, M.C.C.; Wamelink, G.W.W.; Boxman, A.W.; Bleeker, A.; Vergeer, P. ; Arroniz-Crespo, M. ; Limpens, J. ; Lamerse, L.P.M. ; Bobbink, R.; Dorland, E. 2011 Ecosystem responses to reduced and oxidised nitrogen inputs in European terrestrial habitats Environmental Pollution 159 665-676
Stevens, C.J.; Dise, N.B.; Gowing, D.J.; Mountford, J.O. 2006 Loss of forb diversity in relation to nitrogen deposition in the UK: regional trends and potential controls Global Change Biology 12 1823-1833
Stevens, C.J.; Smart, S.M.; Henrys, P. ; Maskell, L.C. ; Walker, K.J. ; Preston, C.D.; Crowe, A. ; Rowe, E. ; Gowing, D.J.; Emmett, B.A. 2011 Collation of evidence of nitrogen impacts on vegetation in relation to UK biodiversity objectives
Sutton, M.A.; Fowler, D. 1993 Estimating the relative contribution of SOx, NOy and NHx inputs to effects of atmospheric deposition Critical loads: concept and applications. Grange-over-Sands Workshop
Tipping, E. ; Henrys, P.A. ; Maskell, L.C. ; Smart, S.M. 2013 Nitrogen deposition effects on plant species diversity; threshold loads Environmental Pollution 179 218-223
Van Den Berg, L.J.L. ; Vergeer, P. ; Rich, T.C.G. ; Smart, S.M.; Guest, D. ; Ashmore, M.R. 2010 Direct and indirect effects of nitrogen deposition on species composition change in calcareous grasslands Global Change Biology 17 1871-83
WHO, 1997 Effects of atmospheric nitrogen compounds (particularly nitrogen oxides) on plants. Environmental Health Criteria Series 188 115–191