The acidification of the ocean by anthropogenic CO2 absorbed from the atmosphere is now well-recognized and is considered to have lowered surface ocean pH by 0.1 since the mid-18th century. Future acidification may lead to undersaturation of CaCO3 making growth of calcifying organisms difficult. However, other anthropogenic gases also have the potential to alter ocean pH and CO2 chemistry, specifically SOx and NOx and NH3. We demonstrate using a simple chemical model that in coastal water regions with high atmospheric inputs of these gases, their pH reduction is almost completely canceled out by buffering reactions involving seawater HCO3− and CO32− ions. However, a consequence of this buffering is a significant decrease in the uptake of anthropogenic CO2 by the atmosphere in these areas.
 There is considerable concern about the effects of anthropogenic CO2 absorbed by the ocean on its carbonate chemistry, and associated pH-dependent processes, collectively termed ocean acidification (OA) [Caldeira and Berner, 1999; Doney et al., 2009; Orr et al., 2005; The Royal Society, 2005]. This process is independent of human-derived global warming, but shares a common cause. A number of potential effects of OA are recognized, including making calcification of marine organisms more difficult, and altering the availability of CO2 for metabolism, with resultant ecosystem changes [The Royal Society, 2005]. However, as recently pointed out by Doney et al.  other anthropogenic gases can also alter ocean pH by absorption from the atmosphere, specifically oxides of sulfur and nitrogen (which enter the ocean mainly after oxidation to H2SO4 and HNO3 respectively), and ammonia.
Doney et al.  presented a detailed analysis of the impact of these gases on the pH of the global surface ocean. Their approach comprised a 3D circulation model of the ocean combined with estimated regional air-to-sea fluxes of the relevant species. They found that the anthropogenic alkalinity flux is negative (becoming more acidic) in temperate regions of the North Atlantic that are dominated by fossil fuel sources of SO2 and NOx but that the flux is positive (becoming more alkaline) in the tropics because of a dominance of NH3 input. The latter position is reversed if a substantial portion of the ammonia undergoes nitrification. On a global scale, the authors concluded that the alterations in surface water chemistry from anthropogenic nitrogen and sulfur input are rather small, only a few percent at most of those caused by the uptake of anthropogenic CO2. However, they did conclude that more substantial impacts might be expected in coastal waters. Here we examine this possibility in more detail.
 Recently, measurements of pH and chemical compositions of rainfall at Bermuda have confirmed that in this region of the subtropical North Atlantic the contribution to OA from sulfur and nitrogen gases is at most 2% of that caused by anthropogenic CO2 [Bates and Peters, 2007]. While this agrees with the predictions of the global model [Doney et al., 2007], Bermuda is not a heavily impacted region and there appears to be no comparable analysis made for coastal waters or shipping lanes where the impacts of sulfur and nitrogen gases are expected to be greater. It is known that the global distribution of shipping density correlates well with emissions of various pollutants derived from ship exhausts, including SO2, NOx and particulates [Endresen et al., 2005, 2003; Streets et al., 1997, 2000]. Therefore, we have conducted a feasibility analysis on the likely relative impacts of CO2 versus the other anthropogenic gases in such waters, focusing in more detail on these areas than done by Doney et al., as well as considering these impacts in a non-model based framework.
 The theory describing the chemical equilibria of CO2 in seawater are well established, along with the methods for characterizing the CO2 system by measurement [Dickson et al., 2007]. The uptake of CO2 from the atmosphere is governed by the Henry's Law equilibrium
where fCO2 is the fugacity of CO2 in the gas phase and K′H is the Henry's law constant, which is a function of temperature and salinity. The quantity [H2CO3*] conventionally represents the stoichiometric concentration of undissociated CO2, i.e., either CO2(aq) or H2CO3. [H2CO3*] further dissociates to form bicarbonate and carbonate ions:
The corresponding equilibrium constant expressions for these two reactions are expressed in a conditional way, defined in terms of the concentrations of the H2CO3*, HCO3− and CO32− and a suitable pH scale. Reactions (2a) and (2b) can be combined to produce a single equilibrium linking all 3 species of CO2 which is useful for visualizing the fate of atmospheric CO2 taken up by the ocean:
The equilibrium constant for (3) is large (≈103) indicating that anthropogenic CO2 taken up by the ocean will react almost completely with residual CO32− in seawater (provided sufficient CO32− remains). While (3) does not explicitly depend on pH, the consequent increase in the ratio of HCO3− to CO32− means that the pH of the seawater will decrease.
 Seawater alkalinity AT is defined as the excess of weak bases present in seawater relative to the condition of pure CO2 in water [Dickson, 1981, 1992]. As a result, the absorption of CO2 by the ocean does not involve any initial change in AT. However, the total dissolved inorganic carbon (DIC) of the water will increase with CO2 uptake
 Alkalinity changes will occur if CO2 uptake subsequently gives rise to dissolution of CaCO3. In principle this will happen when [CO32−] has decreased, through reaction (3) to the point when CaCO3 becomes undersaturated. From this derives concerns about the effects of OA on calcifying organisms.
3. Sulfur and Nitrogen Gases
 Large amounts of SO2 and NOx are emitted by human activities, particularly fuel combustion. Shipping is particularly important because ships tend to use heavy bunker oils as fuel which can be rich in sulfur [Tsyro and Berge, 1997] relative to other fuels. In the atmosphere, these gases are rapidly converted to acid species (H2SO4, HNO3) following emission and are the main forms in which these acidic gases eventually leave the atmosphere. The effects of these acids on freshwater systems and on rain composition are well known (acid rain). Significant quantities of these pollutants also make their way into the ocean, especially in coastal waters where shipping is usually more concentrated.
 The effects of H2SO4 and HNO3 absorption by seawater are different from that of CO2 in two essential respects. First, when CO2 is absorbed by seawater, reaction (3) takes place and the DIC of seawater increases by the amount of CO2 absorbed, with alkalinity remaining constant. By contrast, uptake of H2SO4 by seawater causes a decrease in alkalinity, with each mole of H2SO4 causing a decrease in AT by 2 equivalents because of the diprotic nature of H2SO4. Essentially adding H2SO4 increases acidity in the ocean, which means a decrease in alkalinity. Similarly HNO3 formed by oxidation of NOx as a monoprotic strong acid causes a decrease in alkalinity of 1 equivalent per mole of HNO3 absorbed.
 Second, on time scales of a few months to a year, these initial changes in pH and CO2 chemistry brought about by the absorption of strong acid gases induce an increase in seawater pCO2 with the result that CO2 is vented to the atmosphere as the ocean-atmosphere system re-equilibrates [Doney et al., 2007]. Figure 1a shows the calculated change in pH of seawater of typical composition after the absorption of CO2, H2SO4 or HNO3. Despite the fact that CO2 and HNO3 influence the speciation of CO2 in seawater in fundamentally different ways (increasing DIC versus decreasing AT) the consequent initial changes in pH are very similar. This is because HNO3 is a strong acid, and will therefore participate in a reaction similar in nature to (3)
This gives rise to a smaller change in the CO32− to HCO3− ratio than H2CO3, but this is enhanced by the fact that DIC does not increase. By contrast, the decrease in pH caused by H2SO4 is greater than the other two acids because of the diprotic nature of H2SO4.
Figure 1a demonstrates that to decrease ocean pH by 0.1 requires approximately 30 μM of H2SO4 and almost twice as much of CO2 or HNO3. It would be very difficult to detect an increase in surface ocean sulfate of this magnitude because the background sulfate concentration in seawater is 1000 times greater (0.028 M). However, addition of 60 μM of nitrate would be highly significant in terms of this important micronutrient, and easily detectable. Anthropogenic CO2 levels of up to 60 μM are observed in the present-day surface ocean [Feely et al., 2004; Sabine et al., 2004].
 A decrease in surface ocean pH by whatever form of acidification also leads to an increase in surface water CO2 partial pressure pCO2, which then acts to oppose further absorption of atmospheric CO2 by decreasing the partial pressure gradient between ocean and atmosphere. Figure 1b shows the pCO2 changes resulting from the initial acidification observed in Figure 1a. These results cannot be directly compared with the actual changes in atmospheric CO2 except in a rough manner because the calculations have only been performed at one temperature. However, Figure 1b shows that a 100 ppmv increase in pCO2 results from an increase in DIC of about 60 μM, and is consistent with the observed increase from 280 ppmv in 1750 to 390 ppmv at the present-day.
 As surface waters with this enhanced pCO2 re-equilibrate with the atmosphere over time scales of a few months, the equilibrium pH increases again. The dotted curves in Figure 1a show that after allowance is made for re-equilibration, the final pH decrease induced by the strong acid gases is essentially negligible compared to that arising from anthropogenic CO2, as indicated originally [Doney et al., 2007].
4. Effects of Ammonia Input
 The input of nitrogen species to the ocean is not limited to HNO3 formed by atmospheric oxidation of NOx. Ammonia is also found in the atmosphere. Dry deposition of NH3 will increase AT, while wet deposition of NH4+ has the same effect because the formation of NH4+ in rainwater involves formation of OH− as a counter-ion [Doney et al., 2007]. Thus in both cases, the oceanic uptake of ammonia results in an increase in AT. However, subsequent nitrification can change the impact of these NH3 + NH4+ fluxes
This reverses the effect of ammonia input to a decrease in AT. After complete nitrification of deposited ammonia, the net effect is the same as that of an equivalent amount of HNO3 formed from NOx [Doney et al., 2007].
 An additional factor whereby atmospheric processes can alter surface ocean pH is through the prior dissolution of atmospheric limestone dusts by acidic rainwater. This process increases ocean AT by an amount equivalent to twice the flux of Ca2+ entering the ocean, assuming most Ca2+ in rainwater derives from CaCO3 dissolution [Doney et al., 2007].
5. Model for Comparing pH Effects
 We now describe a simple model for comparing the effects of sulfur and nitrogen gases on surface ocean pH with that of anthropogenic CO2. The model is based on the principles used in the global assessment [Doney et al., 2007]. We apply this model to three case studies of coastal waters for which we can make reasonable estimates of the fluxes to the ocean of sulfur and nitrogen gases.
 The effect of anthropogenic CO2 on pH was calculated by using estimates of AT for each case (together with salinity S and temperature T) to calculate pH and CO2 speciation for an initial condition of equilibrium with an atmosphere having a pCO2 of 390 ppmv. Next, the pCO2 was augmented by +1.7 ppmv which is similar to the annual increase in pCO2 as recorded at Mauna Loa, Hawaii over the last few decades (http://co2now.org). The pH and CO2 speciation were then re-computed to obtain the annual pH change resulting from additional CO2 uptake. The CO2 speciation calculations were carried out using the SWCO2 software package (available at http://neon.otago.ac.nz/swco2).
 Next, to assess the impacts of H2SO4, HNO3 and NH3 on pH, the alkalinity of the seawater was adjusted to take account of the effects of these 3 species (both with and without nitrification):
where f[X] is the annual increase in the concentration of X in the affected water mass as a result of uptake from the atmosphere. The adjusted AT was then combined with the final DIC value obtained from the CO2 calculation to re-calculate the new pH. By making these calculations in steps, i.e., setting some sulfur and nitrogen terms to zero, it was possible to assess the effects of the individual species. We calculated the f[X] terms by combining estimates of the atmospheric deposition rate to the sea surface (mol m−2yr−1) of the anthropogenic sulfur and nitrogen gases with a knowledge of the depth of the water mass affected. This represents a worse case scenario in which the rate of flushing of the water mass is much smaller than the increase in [X].
 The results of this calculation represent the initial pH decrease caused by the sulfur and nitrogen gases before re-equilibration with the atmosphere. In the next calculation step, the CO2 composition of the seawater with altered alkalinity was then re-adjusted to be in equilibrium with the current atmospheric pCO2 for each time step in order to restore equilibrium.
 We chose 3 case studies (Table 1). The first is the southern North Sea region between the U.K. and France, Belgium and the Netherlands, which is an area of very dense shipping. Estimates of the oxidized sulfur and nitrogen fluxes into this region in were taken from the EMEP report for 1997 [Tsyro and Berge, 1997]. For oxidized sulfur, a flux of 24 mol S m−2 yr−1 was assumed, which is equivalent to an acidity flux of 48 mol m−2 yr−1, similar to the value of 30 mol m−2 yr−1 assumed by Doney et al.  for average coastal waters. We also assumed the average water depth in this region to be 36 m.
Table 1. Input Parameters Used for Each Case Study
 The second case is the Baltic Sea which is a region of low surface water salinity and AT, making it potentially more susceptible to acidic gases. The data reported by EMEP [Tsyro and Berge, 1997] indicates that the likely H2SO4 deposition rate for this region is about a factor of 10 lower than the North Sea case. Based on published bathymetric data, we chose an average depth of affected water as 55 m.
 HNO3 fluxes for these two regions were estimated from the same data source [Tsyro and Berge, 1997]. However, we could find no data for NH3 inputs. Therefore, we estimated these by assuming that each is twice the corresponding H2SO4 flux (on a molar basis). Doney et al. [2007, Table 1] report this ratio for the anthropogenic coastal water fluxes, while a value of 2.5 can be calculated from data presented by Endresen et al. .
 The third case study we chose is the South China Sea, for which measured and model-based estimates of the deposition fluxes of all 3 anthropogenic species are available [Wang et al., 2008]. In this case the separate wet and dry fluxes for SO42−, NO3− and NH4+ were combined together. For the South China Sea we chose an average mixed layer depth of 100 m as the depth of water affected by the annual input of sulfur and nitrogen. It should be noted that atmospheric S and N inputs into the North and Baltic Seas have been declining because of air-quality controls, whereas this is probably not the case yet for the South China Sea.
 The input data used for the calculations are summarized in Table 1. Salinity S and temperature T were estimated from hydrographic data, although values are quite variable in the Baltic Sea. However, test calculations showed that the final results are rather insensitive to these parameters. For the North Sea and South China Sea, alkalinity AT was estimated from S and T using reported algorithms for surface waters [Lee et al., 2006]. For the Baltic Sea, we adopted a value of 900 μmol kg−1 based on measured values. Because of the way our model is initialized to a fixed pCO2, it is not particularly sensitive to the actual AT value chosen in that while the absolute pH may not be accurate, the changes in pH after a small increment of CO2 are not strongly affected.
6. Results and Discussion
 The results of our model calculations are presented in Table 2. The results show that the annual decreases in pH resulting from anthropogenic CO2 are quite similar in all three regions, both before and after re-equilibration. They are slightly larger in magnitude for the Baltic Sea because of the lower AT and DIC in these waters. It is interesting that all three sites behave in very similar ways. While the North Sea and South China Sea regions are ones of very intense shipping activity [Streets et al., 1997, 2000], and have correspondingly large atmospheric fluxes of sulfur and nitrogen, the effects on the Baltic Sea are comparable because of the much lower DIC and CT of the latter system. This also underlines the fact (which can be demonstrated using the model) that the effects on pH are not particularly sensitive to S, T or AT (when the system is at equilibrium with the atmosphere).
Table 2. Annual pH Changes, Total H+ Scale, Resulting From Absorption of Different Gaseous Species in the Three Case Studiesa
South China Sea
Both the initial pH change and the change after buffering by re-equilibration with the atmosphere are shown.
CO2 +SOx +NOx
CO2 +SOx +NOx +NH3
 While initial pH changes are comparable to measured or calculated pH changes at several oceanic sites, including BATS and HOTS resulting from CO2 uptake [Bates et al., 1996; Byrne et al., 2010] the pH changes after re-equilibration induced by the sulfur and nitrogen gases in addition to anthropogenic CO2 are negligibly small. What this means is that the strong acid gases have effectively shut down much of the ocean uptake of anthropogenic CO2. This is demonstrated graphically in Figure 2 which shows the change in seawater DIC resulting from the net uptake of atmospheric CO2 in the presence of acidic gases at different ratios f of the fluxes of strong acid and CO2 respectively after re-equilibration. In this analysis, sulfur and nitrogen acids were combined as a single stoichiometric source of strong acid. The graph shows specific cases f = 0.1 (South China Sea), 0.25 (Baltic Sea) and 0.91 (North Sea) compared to f = 0 (CO2 only). As the ratio of strong acid flux increases above f = 0.1, the resultant equilibrium DIC is significantly decreased. At a ratio f = 1.15, the system no longer takes up excess CO2, i.e., the effects of the strong acid gases is such that the surface water maintains equilibrium with the increasing atmospheric pCO2 without any net atmosphere-ocean exchange.
 This analysis, while obviously simplistic, shows that the effects of atmospheric inputs of strong acid gases, at fluxes likely to be encountered in coastal waters, is to eliminate the pH reduction which would normally accompany ocean acidification by CO2, but at the expense of the important contribution of surface waters as a sink for anthropogenic CO2. It should be noted that our analysis has focused purely on the effects of atmospheric inputs of N and S on the CO2 system in coastal waters and has not taken into account other processes that may affect this. In particular, Thomas et al.  have shown that anaerobic nitrate and sulphate reduction in shelf sediments stimulated by inputs of land-derived organic matter may be important sources of alkalinity which will offset the acidifying effects described here.
 This paper resulted from the deliberations of GESAMP Working Group 38, The Atmospheric Input of Chemicals to the Ocean. We thank the Global Atmosphere Watch (GAW) and the World Weather Research Programme (WWRP) of the World Meteorological Organization (WMO), the International Maritime Organization (IMO), the ICSU Scientific Committee on Oceanic Research (SCOR), the Swedish International Development Agency (SIDA), the University of Arizona, and the European Commission Joint Research Centre for support of this work. We thank both reviewers for very helpful comments.
 The Editor thanks Scott C. Doney and an anonymous reviewer for their assistance in evaluating this paper.