the Creative Commons Attribution 4.0 License.
the Creative Commons Attribution 4.0 License.
Atmospheric Deposition of Reactive Nitrogen to a Deciduous Forest in the Southern Appalachian Mountains
- 1U.S. Environmental Protection Agency, Office of Research and Development, Durham, NC, USA
- 2U.S. Department of Agriculture, Forest Service, Otto, NC, USA
- 3Atmospheric Research and Analysis, Inc., Cary, NC, USA
- 4U.S. Environmental Protection Agency, Office of Air and Radiation, Washington, DC, USA
- anow at: U.S. Environmental Protection Agency, Office of Air Quality Planning and Standards, Durham, NC, USA
- bnow at: RTI International, Durham, NC, USA
- cnow at: Boulder A.I.R. LLC, Boulder, CO, USA
- dnow at: U.S. Department of Agriculture, Forest Service, Albuquerque, NM, USA
- retired
- 1U.S. Environmental Protection Agency, Office of Research and Development, Durham, NC, USA
- 2U.S. Department of Agriculture, Forest Service, Otto, NC, USA
- 3Atmospheric Research and Analysis, Inc., Cary, NC, USA
- 4U.S. Environmental Protection Agency, Office of Air and Radiation, Washington, DC, USA
- anow at: U.S. Environmental Protection Agency, Office of Air Quality Planning and Standards, Durham, NC, USA
- bnow at: RTI International, Durham, NC, USA
- cnow at: Boulder A.I.R. LLC, Boulder, CO, USA
- dnow at: U.S. Department of Agriculture, Forest Service, Albuquerque, NM, USA
- retired
Abstract. Assessing nutrient critical load exceedances requires complete and accurate atmospheric deposition budgets for reactive nitrogen (Nr). The exceedance is the total amount of Nr deposited to the ecosystem in excess of the critical load, which is the amount of Nr input below which harmful effects do not occur. Total deposition includes all forms of Nr (i.e., organic and inorganic) deposited to the ecosystem by wet and dry pathways. Here we present results from the Southern Appalachian Nitrogen Deposition Study (SANDS), in which a combination of measurements and field-scale modeling were used to develop a complete annual Nr deposition budget for a deciduous forest at the Coweeta Hydrologic Laboratory. Wet deposition of ammonium, nitrate, nitrite, and bulk organic N were measured directly. The dry deposited Nr fraction was estimated using a bidirectional resistance-based model driven with speciated measurements of Nr air concentrations (e.g., ammonia, ammonium aerosol, nitric acid, nitrate aerosol, bulk organic N in aerosol, total alkyl nitrates, and total peroxy nitrates), micrometeorology, canopy structure, and biogeochemistry. Total annual deposition was 6.6 kg N ha-1 yr-1, which is on the upper end of Nr critical load estimates recently developed for similar ecosystems in nearby Great Smoky Mountains National Park. Of the total (wet + dry) budget, 50.7 % was contributed by reduced forms of Nr (NHx = ammonia + ammonium), with oxidized and organic forms contributing 41.6 % and 7.7 %, respectively. Our results indicate that reductions in NHx deposition would be needed to achieve the lowest estimates (3.0 kg N ha-1 yr-1) of Nr critical loads in southern Appalachian forests.
- Preprint
(1702 KB) -
Supplement
(1319 KB) - BibTeX
- EndNote
John Thomas Walker et al.
Status: final response (author comments only)
-
RC1: 'Comment on bg-2022-133', Anonymous Referee #1, 19 Jul 2022
The manuscript by Walker et al. presents results from a study investigating atmospheric deposition of reactive nitrogen to a deciduous forest at the USDA Forest Service Coweeta Hydrologic Laboratory in the southern Appalachian Mountains. The authors use several well-established measurement methods to differentiate between oxidized and reduced as well as organic and inorganic compounds found in wet and dry deposition. Finally, they apply a bi-directional resistance-based model driven with the observed measurements of Nr air concentrations, micrometeorology, canopy structure, and biogeochemical parameters to present the full reactive nitrogen budget for the site.
While the character of the paper is a report-style compilation of results from a multitude of methods rather than following a clear scientific question, the authors do a great job in thoroughly describing the complexity of reactive nitrogen field investigations and long-term observation. Though continuous eddy-covariance observations are not included, the study represents the state-of-the-art in Nr monitoring and data interpretation. I particularly appreciate the inclusion of field investigations of the ammonia emission potential of green and senescent leaves as well as from litter, which is crucial for model parameterization and rarely conducted. The results are put into a broader context and discussed with regard to air quality regulations in the past, e.g. reduction in oxidized N is now clearly visible. Method uncertainties are sufficiently considered and presented.
The text is very well written and easy to follow. Figures are clear and easy to grasp. The supplemental material is useful and the selection of graphs and tables that were put into this section is good. This is the most comprehensive single-site study I am aware of and definitely deserves publication.
I only have a few, rather minor, points that should be considered before final presentation in the BG journal:
- With regard to Section 2.2.7, how exactly were the NH3 data from hourly measurements used to impose diurnal variability on the biweekly data to be used as hourly input for the model? It is stated in line 393 that continuous NH3 concentrations were only measured during the last two intensives (in spring and summer, I guess?). The diurnal variability is known to be driven by temperature, humidity, light availability, phenology, etc., how was the amplitude of the variability from these two campaigns transferred to the other – probably much cooler – seasons?
- The method section is very informative, but quite long. I’m wondering whether it would make sense to put all detailed descriptions from 2.2.1 up to 2.2.5 into the supplement, just adding a few sentences to 2.2 what has been done and referring to the respective part in the Supplemental Material. It’s not a must, but would significantly reduce length and better highlight the findings given the potential readership of people who work in conservation and are likely more interested in the results and their interpretation than in every technical detail of the methodology.
Other:
- Introduction: I suggest adding information on measurement period, length, etc.
- Line 41-42: “many areas” and “some regions”, please specify where, e.g. near hotspots of animal husbandry, chemical industry, etc.
- Line 153: Is 8 m the correct height? What was the reason for this height?
- Line 170: What was the selection criteria for the two respective heights?
- Line 178: “to the analytical box for analysis Ion Chromatography (IC)", is there a word missing?
- Line 270: Check for consistency in unit notation: “g-1 tissue” vs. “kg tissue-1”
- Line 312: Delete “is Ra” after “z0”
- Line 449: Is RH defined before?
- Line 505-506: Do two decimal places reflect the measurement accuracy?
- Line 605-606: 61.4% wet plus 38.7% dry deposition equals 100.1%, check rounding
- Line 617: Can a bit more explanation given why stomatal fluxes are so low compared to cuticular fluxes?
- Line 708: Why would the aerodynamic resistance become zero at steep forested slopes? Ra is turbulence and wind speed driven, so why would it approach zero?
-
AC1: 'Reply on RC1', John Walker, 29 Sep 2022
The comment was uploaded in the form of a supplement: https://bg.copernicus.org/preprints/bg-2022-133/bg-2022-133-AC1-supplement.pdf
-
RC2: 'Referee's comments on bg-2022-133', Chris Flechard, 11 Aug 2022
Reviewer's comments on Biogeosciences manuscript "Atmospheric Deposition of Reactive Nitrogen to a Deciduous Forest in the Southern Appalachian Mountains" by J.T. Walker
General Comments
This manuscript describes the atmospheric reactive nitrogen (Nr) deposition budget over a deciduous forest in the Southern Appalachian Mountains. Extensive measurements of the wet and dry deposition components of total deposition of inorganic and organic, reduced and oxidized, gas- and aerosol-phase Nr, are reported for the years 2015-2016, when intensive measurement campaigns were conducted at a forest site in Coweeta Basin as part of the SANDS programme.
Wet deposition was measured in straightforward manner by precipitation collectors, while dry deposition was mostly modelled from measured air concentrations and surface-atmosphere exchange (inferential) modelling. Some aerodynamic gradient-flux measurements were made for gases and aerosols over a limited period of time, providing measured reference points to assess the performance of the surface-atmosphere exchange model.
The detailed, speciated, multi-season, multi-site measurements of most of the dominant and also less documented (e.g. organic) forms of Nr concentrations in air and water offer a rare, measurement-based glimpse into the diversity of all Nr forms contributing to total Nr deposition over a US forest, and into the technical challenges and solutions implemented to close the deposition budget.
The data from the 2015-2016 SANDS intensive campaigns are examined in the light of multi-year or multi-decadal observation datasets from CASTNET, AMoN, NADP and EPA measurement networks, showing the decreases observed in total Nr deposition to the site over the last 3-4 decades (mostly from a long-term reduction in NOx emissions), but highlighting the increasing importance of reduced nitrogen in total deposition and the continued exceedance of critical loads for this ecosystem. The paper is therefore very well suited for the readership and scope of Biogeosciences.
The manuscript presents a very detailed and clear description of the measurement methods used in the extensive data collection, and assimilation by inferential modelling, which I find very useful for this type of paper, where the objective and scope include a thorough methodological component to document the manifold aspects required to compute a comprehensive Nr deposition budget. Such methodological aspects deserve not to be trivialized and glossed over, and will be useful to other researchers in this field, confronted by the complexities of total Nr deposition budgetting.
The paper is very well written, and I have only very few and minor comments before recommending eventual publication in Biogeosciences.
Specific Comments
line 153: some gas and aerosol components of total Nr were measured at 1-10m above ground , while the canopy height is 30m. I presume this means the samplers were located in a clearing of the forest. How was this accounted for in inferential modelling of dry deposition, knowing that the model supposes that concentrations are measured above the canopy, and that concentrations measured in a (small) clearing are likely to represent sub-canopy levels rather than above-canopy concentrations? Was there a correction scheme to account for this effect?
line 265 and lines 564-569: the Gamma_s parameter in the bi-directional NH3 exchange model should represent the emission potential (NH4+/H+) of the apoplast, i.e. the inter-cellular fluid that is exposed to the air within sub-stomatal cavities. Here the assumption is made (implicitly) that the NH4+/H+ ratio of bulk tissue extracts (whole leaf, i.e. whole cells inc. vacuole, symplast and apoplast all mixed) is equal to the apoplastic emission potential. Many publications have previously reported vastly different NH4+/H+ ratios for bulk tissue and apoplast (e.g. Sutton et al, Biogeosciences, 6, 2907–2934, 2009, fig.7 over grassland, 1-2 orders of magnitude difference; Wang et al., Plant Soil (2011) 343:51–66, conclude p64: "...bulk leaf tissue Ð can not be used as a tool to predict the potential NH3 exchange of beech leaves" ). Some publications do assert that there is a positive relationship between bulk and apoplastic Gamma ratios, and bulk ratios are of course much more easily measured than apoplastic extraction methods, so it is tempting to use the bulk tissue ratio as a proxy, for simplicity. Do the authors have evidence that it is justified in the case of this particular forest ecosystem? They do present a sensitivity analysis later on, using upper and lower percentiles, but I didn't see any explicit discussion of why or how the bulk tissue ratio could be used as a proxy for the apoplastic ratio. Please comment.
line 647: "This pattern largely reflects the seasonal cycle in leaf area index". Could seasonal patterns in wind speed, turbulence, surface wetness (rainfall), also contribute to seasonal Vd patterns, aside from LAI?
line 758-9: "more temporally extensive measurements of the litter NH3 emission potential are also needed". I would add that a better understanding (and modelling) of the leaf litter decay dynamics, constrained by weather (temperature, moisture) are needed if one aims to reproduce litter N emissions in surface exchange models.
Technical corrections
line 290: add "by eddy covariance" after "heat flux measured..."
lines 427-428: the sentence " To estimate the concentration of NO2 from the measured “other” NOy, we examined the ratio of NO2 to the quantity NOy – HNO3 – PANS – NTR (e.g., “other” NOy) simulated by CMAQ (V5.2.1) for the Coweeta site over the year 2015418-419..." feels a little like a repeat of lines 418-419
line 442, figure 2 and figure S9: the decrease of SOx emissions and concentrations over 30 years had a large impact on NHx chemistry, and is useful to explain the NHx trends. It would be good to show the SO2/SO4= data of Fig S9 in Fig.2 of the main text, alongside long-term trends of Nr?
line 505, fig. 5: NOy concentrations are expressed in ppb, it might be good to harmonize with the rest of the figures as µg m-3 (easier to compare NOy with TNO3- and NHx of figs 6-7, for example) ?
line 517: suggest change "the same proportions of the NOy budget..." to "the same proportions of the atmospheric NOy load ..." ? The word budget may suggest deposition ?
line 631, similar to above, suggest change to "NH4+ contributed more to the atmospheric NHx load than NH3..."
line 556: "The contributions of NO3 - and NO2- were negligible." This refers to Fig. 8, but in the top part (a) of Fig. 8, I don't see that NO3- was negligible (here, WSON is negligible, as is NO2-). And subsequently, "Organic compounds (WSON) contributed 11.6% of WSTN...", again that is not what the top figure shows, but it is what the lower part (b) of Fig. 8 apparently shows. There is a contradiction between the two parts (a) and (b): which is WSON, and which is NO3- ? Amend text if neccessary.
Fig. 8 caption: suggest change to "Contributions of N aerosol species to WSTN..."
-
AC2: 'Reply on RC2', John Walker, 29 Sep 2022
The comment was uploaded in the form of a supplement: https://bg.copernicus.org/preprints/bg-2022-133/bg-2022-133-AC2-supplement.pdf
-
AC2: 'Reply on RC2', John Walker, 29 Sep 2022
John Thomas Walker et al.
John Thomas Walker et al.
Viewed
| HTML | XML | Total | Supplement | BibTeX | EndNote | |
|---|---|---|---|---|---|---|
| 291 | 81 | 11 | 383 | 30 | 3 | 3 |
- HTML: 291
- PDF: 81
- XML: 11
- Total: 383
- Supplement: 30
- BibTeX: 3
- EndNote: 3
Viewed (geographical distribution)
| Country | # | Views | % |
|---|
| Total: | 0 |
| HTML: | 0 |
| PDF: | 0 |
| XML: | 0 |
- 1