Acid deposition :: Standing Open Water and Canals

Effects and implications

  • Effects of acid deposition on standing waters are largely confined to oligotrophic lakes which tend to occur in catchments underlain by lithologies (rock types) such as granites, sandstones and schists which have low weathering rates. In these systems, base cation supply from weathering may be insufficient to balance deposited acidity. Acidification is therefore rarely likely to affect mesotrophic to eutrophic lakes or canals as base cation supply is sufficient to buffer effects of acidification.
  • The acidification of oligotrophic lakes has been shown to influence aquatic biota at all levels of the food chain, from primary producers, such as aquatic algae and macrophytes, to macroinvertebrates, fish and even water birds.
  • Acidification leads to an overall reduction in species biodiversity as well as functional diversity (K. Layer et al., 2010; Mulholland et al. 1986; Jenkins et al, 2013) In some areas acidification has led to major declines in yields of salmonid fisheries including the Galloway region of southwest Scotland (Harriman et al., 1987).
  • Aquatic animals (invertebrates and fish) are vulnerable to increased aluminium, hydrogen ion and heavy metal toxicity ( Stockdale et al, 2014), and changes in food availability and quality.
  • Growth of some plants may be affected by the reduced availability of dissolved inorganic carbon (DIC – required for photosynthesis), macronutrients such as phosphorus, and changes in inter-specific competition.
  • Water pH is often identified as the chemical variable which explains the greatest amount of variance in macroinvertebrate species data in upland regions (Larsen et al., 1996; Murphy et al., 2013) ). Several molluscs, amphipod and mayfly taxa are confined to the less acidic end of the spectrum, whereas more tolerant species, including several stoneflies and chironomids, are often present throughout much of the range. Few acid tolerant species are solely restricted to acidic sites.
  • Acid episodes, driven either by high rainfall events or seasalt episodes, tend to have a less deleterious effect on water acidity in standing waters compared to streams (Acid deposition :: Rivers and Streams) as a result of the buffering effect of the larger volume of standing water, although depressions in pH and increased concentrations of inorganic aluminium can still be seen in smaller water bodies, including several within the UK Upland Waters Monitoring Network (UWMN; formerly known as the UK Acid Waters Monitoring Network AWMN).

Overview: evidence, processes and main impacts

Acid deposition on acid sensitive catchments (mostly overlying rock types with low weathering rates, such as granites, sandstones and schists) can result in chronic acidification of runoff into drainage waters, and particularly headwater streams. Deposited compounds of sulphur and nitrogen, in addition to hydrochloric acid (Evans et al, 2011), derived predominantly from the burning of fossil fuels, contributed to a progressive loss in buffering capacity of catchment soils and consequent reductions in pH and increases in inorganic aluminium in these waters from around the onset of the industrial revolution until the 1970s-80s. The main source of evidence for the timing and magnitude of acidification has come from the palaeoecological analysis of acid sensitive upland lakes as these systems leave an historical archive of environmental change in their sediments. These records tend to show reductions in water pH from the mid-1800s, and it is assumed that the acidity of running waters in the same regions will have followed similar trajectories.

Data from the UWMN demonstrate that sulphate (the primary acidifying anion) concentrations have fallen substantially in lakes across the UK over the past 2 decades (1988 – 2008), pH and Acid Neutralising Capacity (ANC; see below) have risen, and concentrations of inorganic aluminium have fallen sharply in the most acidic lakes (Battarbee et al., 2014; Monteith et al., 2014).

Levels of nitrate (a secondary acidifying anion) show relatively little change and appear to be controlled primarily by inter-annual variations in climate.

Assessments of AWMN data (e.g. Monteith et al., 2014, and supporting palaeoecological evidence (Kreiser et al., 1990)) suggest that AWMN surface waters with managed coniferous forest catchments experience higher acidic loads, through enhanced pollutant interception, and are more acidified than nearby sites without forests. It has been estimated that afforestation of moorland within Kielder Forest increased sulphur and nitrogen inputs by 30% and 90% respectively (Fowler et al., 1989). 

The ability of surface waters to withstand acid deposition is determined by the calculation of Acid Neutralising Capacity (ANC). ANC represents the balance between base cations and strong acid anions, is relatively easy to model (in comparison with pH), and has been shown to be a robust predictor of damage to salmonid populations in Norwegian lakes (Lien et al., 1996). A threshold for healthy brown trout populations of ANC 20 µeq L-1 (or ANC20) has since been adopted internationally as the standard for protection of acid sensitive waters. Relationships with ANC have also been shown for macroinvertebrates (Raddum et al., 1995 ) and diatoms (e.g.Sickman et al., 2013).   A negative ANC (i.e. excess acid anions over base cations) implies elevated concentrations of acid cations, i.e. hydrogen and aluminium ions, and hence acidic water. For water with a positive ANC, the excess of base cations may be accounted for by organic anions (i.e. dissolved organic carbon - DOC), bicarbonate and (at higher values) carbonate.

A comparison of diatom species collected annually in lake sediment traps with the historical diatom record preserved in lake sediment cores, demonstrates that diatom communities in most lakes on the UWMN remain very different from  the communities that characterised the sites before they began to acidify around 200 years ago (Battarbee et al., 2014).

Inorganic aluminium concentration (often referred to as labile aluminium to distinguish it from organically bound, and therefore less biologically available aluminium) is not routinely measured by most environmental laboratories. However, where data are available it is often found to be a strong predictor of the assemblage in spatial studies in addition to assessments of temporal variation in monitoring studies (e.g. Monteith et al., 2005). Inorganic aluminium concentration has been found to be the most sensitive overall indicator of acid impacts on brown trout populations across the UWMN (Malcolm et al., 2014).

Pollutant deposition type and risk

Type of  deposition

Form of Pollutant

Risk areas

Dry deposition

Gaseous

Sulphur and nitrogen species

The risk areas are often far from potential dry deposition sources of pollutant.

 



Wet deposition

precipitation and occult

(cloud, mist)

Sulphate, nitrate. ammonium, and hydrochloric acid

Predominantly upland headwater lakes draining organic mineral soils such as peaty podzols, overlying acid sensitive geologies.

Indicators of lake acidification

  • Detectable levels of inorganic aluminium (concentrations greater than circa 10 µg L-1 rarely encountered in non-acidified upland streams)
  • Negative or low Acid Neutralising Capacity
  • Low diatom diversity, dominated by acid loving Tabellaria species.
  • Low diversity of higher plants, and particularly elodeid species that extract inorganic carbon and nutrients from the water column rather than from sediments
  • Low macroinvertebrate diversity with mayfly and mollusc species largely absent
  • Salmonids at low density or absent

Examples of species specific responses

Species

Response

Reference

Salmonids

-ve

Harriman et al., 1987; McCartney et al., 2003

What factors modify acid deposition impacts?

  • Buffering capacity of catchment soils and waters
  • Soil thickness and presence of wetlands
  • Catchment slope – greater slopes resulting in less opportunity for neutralisation.  

Evidence of recovery

Despite the chemical improvements there has been relatively little biological recovery to date [10], possibly reflecting the continued depleted base status of catchment soils, biogeographic limitations on the dispersal of acid sensitive species that may have been lost during acidification, and internal ecological inertia to recolonisation resulting from acid tolerant generalist taxa having taken over functional niches previously occupied by acid sensitive taxa (Ledger et al., 2005; Monteith et al., 2005).

Some recovering acidified lakes on the UWMN have shown more marked declines in some acid-loving diatom species (i.e. unicellular siliceous algae), the appearance of some aquatic macrophyte species that do not occur in very acid water, and gradual increases in certain macroinvertebrate species (including caddis, stonefly and mollusc taxa) that are indicative of less acidic water. 

Recovery from acidification has been accompanied by a marked increase in the concentration of dissolved organic carbon (DOC) in lakes, which is thought to be a consequence of rising solubility of catchment soil organic matter in response to reduced acid deposition (Monteith et al., 2007; Evans et al., 2006).]. This is likely to have substantially reduced the transparency of some lakes, resulting in reductions in photic depth and potentially a reduction in whole lake productivity [16], while also providing additional protection to aquatic organisms from UVB radiation.

Critical Load/Level: 

Habitat/ Ecosystem Type Critical Load/ Level Reliability Indication of exceedance Reference
Freshwaters

Value varies depending on species of interest and mineralogy, size & other characteristics of the waterbody and its catchment.

quite reliable i.e. the results of some studies are comparable

Decline in fish population and changes in diatom, invertebrate and nacrophyte assemblages.

803

References: 

Battarbee, R.W.; Shilland, E.M. ; Kernan, M.; Monteith, D.T.; Curtis, C. 2014 Recovery of acidified surface waters from acidification in the United Kingdom after twenty years of chemical and biological monitoring (1988–2008) Ecological Indicators 37 267-273
Battarbee, R.W.; Simpson, G.L. ; Shilland, E.M. ; Flower, R.J.; Kreiser, A.; Yang, H. ; Clarke, G. 2014 Recovery of UK lakes from acidification: An assessment using combined palaeoecological and contemporary diatom assemblage data. Ecological Indicators 37 365-380
Evans, C.D.; Monteith, D.T.; Fowler, D ; Cape, J.N.; Brayshaw, S. 2011 Hydrochloric Acid: An Overlooked Driver of Environmental Change. Environmental Science and Technology 45 1887-1894
Evans, C.D.; Chapman, P.J.; Clark, J.M. ; Monteith, D.T.; Cresser, M.S. 2006 Alternative explanations for rising dissolved organic carbon export from organic soils. Global Change Biology 12 2044-2053
Fowler, D.; Cape, J.N.; Unsworth, M.H. 1989 Deposition of atmospheric pollutants on forests Philosophical Transactions of the Royal Society of London Series B-Biological Sciences 324 247-265
Harriman, R.; Morrison, B.R.S.; Caines, L.A.; Collen, P.; Watt, A.W. 1987 Long-term changes in fish populations of acid streams and lochs in Galloway south West Scotland. Water, Air and Soil Pollution 32 89-112
Jenkins, G.B. ; Woodward, G. ; Hildrew, A.G. 2013 Long-term amelioration of acidity accelerates decomposition in headwater streams. Global Change Biology 19 1100-1106
Kreiser, A.M. ; Appleby, P.G.; Natkanski, J.; Rippey, B.; Battarbee, R.W. 1990 Afforestation and Lake Acidification: A Comparison of Four Sites in Scotland. Philosophical Transactions of the Royal Society of London. Series B, Biological Sciences 327 337-383
Larsen, J. ; Birksl, H.J.B ; Raddum, G. ; Fjellheim, A. 1996 Quantitative relationships of invertebrates to pH in Norwegian river systems. Hydrobiologica 328 57-74
Layer, K. ; Hildrew, A. ; Monteith, D.O.N. ; Woodward, G.U.Y. 2010 Long-term variation in the littoral food web of an acidified mountain lake. Global Change Biology 16 3133-3143
Lien, L.; Raddum, G.G.; Fjellheim, A.; Henriksen, A. 1996 A critical limit for acid neutralizing capacity in Norwegian surface waters, based on new analyses of fish and invertebrate responses Science of the Total Environment 177 173-193.
Malcolm, I.A. ; Bacon, P.J. ; Middlemas, S.J. ; Fryer, R.J. ; Shilland, E.M. ; Collen, P. 2014 Relationships between hydrochemistry and the presence of juvenile brown trout (Salmo trutta) in headwater streams recovering from acidification Ecological Indicators 37 351-364
McCartney, A.G. ; Harriman, R.; Watt, A.W.; Moore, D.W. ; Taylor, E.M. ; Collen, P.; Keay, E.J. 2003 Long-term trends in pH, aluminium and dissolved organic carbon in Scottish fresh waters; implications for brown trout (Salmo trutta) survival Science of The Total Environment 310 133-141
Monteith, D.T.; Hildrew, A.G. ; Flower, R.J.; Raven, P.J.; Beaumont, W.R.B. ; Collen, P.; Kreiser, A.M. ; Shilland, E.M. ; Winterbottom, J.H. 2005 Biological responses to the chemical recovery of acidified fresh waters in the UK. Environmental Pollution 137 83-101
Monteith, D.T.; Evans, C.D.; Henrys, P.A. ; Simpson, G.L. ; Malcolm, I.A. 2014 Trends in the hydrochemistry of acid-sensitive surface waters in the UK 1988–2008. Ecological Indicators 287-303
Monteith, D.T.; Stoddard, J.L.; Evans, C.D.; De Wit, H.A. ; Forsius, M. ; Hogasen, T. ; Wilander, A. ; Skjelkvale, B.L. ; Jeffries, D.S. ; Vuorenmaa, J. ; Keller, B. ; Kopácek, J.; Vesely, J. 2007 Dissolved organic carbon trends resulting from changes in atmospheric deposition chemistry. Nature 450 537-539
Mulholland, P.J. ; Elwood, J.W. ; Palumbo, A.V. ; Stevenson, R.J. 1986 Effect of Stream Acidification on Periphyton Composition, Chlorophyll, and Productivity. Canadian Journal of Fisheries and Aquatic Sciences 43 1846-1858
Murphy, J.F. ; Davy-Bowker, J. ; McFarland, B. ; Ormerod, S.J. 2013 A diagnostic biotic index for assessing acidity in sensitive streams in Britain. Ecological Indicators 24 562-572
Raddum, G. ; Skjelkvale, B.L. 1995 Critical limits of acidification to invertebrates in different regions of Europe. Water Air and Soil Pollution 85 475-480
Sickman, J.O. ; Bennett, D.M. ; Lucero, D.M. ; Whitmore, T.J. ; Kenney, W.F. 2013 Diatom-inference models for acid neutralizing capacity and nitrate based on 41 calibration lakes in the Sierra Nevada, California, USA. Journal of Paleolimnology 50 159-174
Stockdale, A. ; Tipping, E. ; Fjellheim, A.; Garmo, O.A. ; Hildrew, A.G. ; Lofts, S. ; Monteith, D.T.; Ormerod, S.J.; Shilland, E.M. 2014 Recovery of macroinvertebrate species richness in acidified upland waters assessed with a field toxicity model Ecological Indicators 37 341-350