the Creative Commons Attribution 4.0 License.
the Creative Commons Attribution 4.0 License.
| 09 Aug 2022
Stable isotopic evidence for the excess leaching of unprocessed atmospheric nitrate from forested catchments under high nitrogen saturation
Abstract. The average concentration of stream nitrate eluted from the FK forested catchments (FK1 and FK2) in Japan was more than 90 µM, implying that these forested catchments were under nitrogen saturation. To verify that these forested catchments were under the nitrogen saturation, we determined the export flux of unprocessed atmospheric nitrate relative to the entire deposition flux (Matm / Datm ratio) in these catchments, because the Matm / Datm ratio has recently been proposed as a reliable index to evaluate nitrogen saturation in forested catchments. Specifically, we determined the temporal variation in the concentrations and stable isotopic compositions, including Δ17O, of stream nitrate in the FK catchments for more than 2 years. In addition, for comparison, the same parameters were also monitored in the MY forested catchment in Japan during the same period, where the average stream nitrate concentration was low, less than 10 µM. While showing the average nitrate concentrations of 109.5, 94.2, and 7.1 µM in FK1, FK2, and MY, respectively, the catchments showed average Δ17O values of +2.6, +1.7, and +0.6 ‰ in FK1, FK2, and MY, respectively. Thus, the average concentration of unprocessed atmospheric nitrate ([NO3−atm]) was estimated to be 10.8, 6.1, and 0.2 µM in FK1, FK2, and MY, respectively, and the Matm / Datm ratio was estimated to be 13.9, 7.9, and 1.2 % in FK1, FK2, and MY, respectively. The estimated Matm / Datm ratio in FK1 (13.9 %) was the highest ever reported from temperate forested catchments monitored for more than 1 year. Thus, we concluded that nitrogen saturation was responsible for the enrichment of stream nitrate in the FK catchments, together with the elevated NO3−atm leaching from the catchments. While the stream nitrate concentration ([NO3−]) can be affected by the amount of precipitation, the Matm / Datm ratio is independent of the amount of precipitation; thus, the Matm / Datm ratio can be used as a robust index for evaluating nitrogen saturation in forested catchments.
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Notice on discussion status
The requested preprint has a corresponding peer-reviewed final revised paper. You are encouraged to refer to the final revised version.
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The requested preprint has a corresponding peer-reviewed final revised paper. You are encouraged to refer to the final revised version.
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Journal article(s) based on this preprint
Interactive discussion
Status: closed
-
RC1: 'Comment on egusphere-2022-717', Anonymous Referee #1, 28 Aug 2022
The submitted manuscript by Ding et al. reports nitrogen and oxygen isotopes of nitrate from two forested catchments with elevated stream nitrate concentration over two years. The authors combined their results with the 17O excess of nitrate in precipitation from one site to calculate the proportion of unprocessed atmospheric nitrate into streams, i.e., Matm/Datm ratio, and used this ratio to assess N status for forest ecosystem by comparing with one nearby forested catechment but with low stream water nitrate concentration, and other 8 forests where Matm/Datm ratio in the world can be calculated. The authors proposed that Matm/Datm ratio can be more robust index for assessing N status compared to stream nitrate concentration. This is because stream water nitrate concentration can be diluted by high precipitation and groundwater recharge. Their results show that the study forested catchment had highest nitrate concentration in stream water among the 11 sites, and highest Matm/Datm, as well. In addition, the authors found that there were good relationships among stream water nitrate concentration, Matm/Datm ratio, nitrate deposition. The authors concluded that Matm/Datm should be used as a more reliable index for evaluating the progress of nitrogen saturation because the Matm/Datm ratio is independent from the amount of precipitation. This conclusion can be well supported. The manuscript was clearly written.
I have one major concern about Matm/Datm ratio as an index for evaluating N saturation. We definitely can observed low Matm/Datm ratio if a forest is N limited and almost all precipitation nitrate is biologically processed. However, there are two exceptions. One is high precipitation may cause high Matm/Datm ratio due to limited contact time of precipitation nitrate with soil microbes and roots. The other is high soil nitrate production (gross nitrification rate), which can dilute of 17O of precipitation nitrate that reachs the soil. It will be wonderful if the authors have more discussion on these two factors.
Another concern is about 17O of precipitation nitrate used in the calculation of Matm/Datm ratio in the study. The streamwater samples for the three forested catchments were collected in 2019 to 2021, while 17O of precipitation nitrate used in the calculation was from the site Sado island in central Japan during 2009 to 2012. So the space and time both were mismatched between stream water sampling sites and precipitation sites. So it is better that authors justified the mismatch. In addition, the average of 17O in precipitation nitrate were used. However, there are a number of studies reporting highly seasonal variation of 17O in precipitation nitrate. I would like to see some discussion on the uncertainties involved with the sampling.
Citation: https://doi.org/10.5194/egusphere-2022-717-RC1 - AC1: 'Reply on RC1', Weitian Ding, 22 Sep 2022
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RC2: 'Comment on egusphere-2022-717', Anonymous Referee #2, 04 Sep 2022
This manuscript aims to investigate how forests attenuate atmospheric NO3- deposition. Work was carried out in two forested catchments in Japan, one at a lower elevation that previous work shows receives higher loads of atmospheric NO3- deposition and the second at a higher elevation that receives lower levels of atmospheric NO3- deposition. In each catchment monthly streamwater samples were collected over ~2 years, and isotopic measurements (del 17O) were used to determine the proportion of NO3- export derived from atmospheric deposition. The key finding of the work is that the lower elevation / higher deposition catchment also exports a proportionally higher quantity of atmospheric NO3-. The topic of how, and how much, forests can retain atmospheric NO3- inputs is of scientific interest and relevant to Biogeosciences. However, presently this work is a bit short on data (monthly samples from three sites across two streams are combined with previously published annual atmospheric deposition rates) and analysis (primarily focusing on deriving the ratio between atmospheric NO3- export and inputs at the annual scale and determining whether or not each catchment was N saturated or not).
Key comments
- It is difficult to identify a single driver for the differences in the proportion of atmospheric NO3- export between the two sites given that they differ both in terms of the amount of N deposition and their climate (the low deposition site receives significantly less rainfall and is significantly cooler than the high deposition site; L120-121). These also led to differences in vegetation between the two sites (L114-119). Differences in hydrology are not accounted for, but should be (e.g., both surface water – groundwater interactions and slope, both of which could impact N attenuation and the degree of streamwater mixing with microbial NO3- sources). The fact that FK has lower concentrations of atmospheric NO3- at the upstream site than the downstream does indicate that there is unaccounted for hydrologic mixing (or loss) occurring along the stream, which could significantly bias M/D estimates based on a single sampling point (as in the MY catchment). Given how different the sites are MY does not act as a useful ‘control’ for FK. Additional data that would enable a functional understanding of how NO3- moves through these two different sites is therefore needed.
- The atmospheric deposition info used to calculate M/D (the crux of the study) were collected over 10 years, but these measurements ended prior to the stream water sampling that is the primary data here. This is a major limitation, given how much atmospheric N deposition can vary month to month and year to year. A robust approach to constrain the uncertainty created by relying on this ‘mean’ data is required. Information is also needed on the exact location of the atmospheric sample collection relative to the streamwater collection sites (in particular for helping to assess whether there might be differences in atmospheric inputs at sites FK1 v FK2).
Specific comments
L4: The abstract should be revised to start with establishing the ‘big picture’ issue addressed and aim of the study, rather than jumping straight in to site differences.
L4-6: Here and elsewhere, I suggest referring to the sites by name rather than using acronyms, as this will make it easier to connect this to other work on the sites and more intuitive to follow within the manuscript.
L50: This line suggests that groundwater inputs are greater in humid temperate forests than other biomes, which is as far as I know not true.
L66: Word missing after ‘recent’
L93-95: How could the validity of the approach be tested with the collected data? Why is there reason to think that this method wouldn’t work in catchments with higher rates of N deposition? A clear hypothesis about how and why catchment retain v export atmospheric NO3- will be important for setting up a stronger discussion section.
L96: Word missing after ‘recent’
L105-107: As above, it is not clear how the reliability of the M/D ratio can be evaluated using these methods. What results would show that it’s unreliable?
L126: How were the boundaries between the FK1 and FK2 catchments determined? Fig. 1 indicates that these sites are both located along the same stream in the same catchment.
L161-163: More information on internal standards needed (number, delta values, etc). Information on calibration for del17O also needed.
L226-229: Were climate conditions (rainfall, stream flow, temperature) significantly different between the years where atmospheric N was measured v the years where stream N was measured?
L234: Is this a reasonable explanation for the two sites? Some geologic / hydrologic information is needed to support this.
L236: Given how important this value is for estimated M/D (L264), it would be illustrative to calculate stream flow based on a range rather than a single average value.
L273-275: Did rainfall differ between the two stream water sampled years? This would be useful information for helping interpret differences in NO3- over time.
L290: Report in more quantitative terms (what is ‘little’ variation?)
L302-305: Move to Discussion.
L325-329: What is the likely source of the 20% discrepancy? Is this due to differences in method (and if so how / what?) or genuine inter-annual differences in either N inputs or N retention? These points should be expanded on here.
L336-343: The collected data would need to be combined with more detailed meteorological information and/or isotopic modelling in order to determine the source of atmospheric N to the two sites. Consequently this explanation for the differences between the two sites is mostly speculation and does not have much baring on the overall aim of the study (to understand forest N saturation dynamics), so I suggest removing altogether or moving to the site description as part of the explanation for the known difference in N deposition rates between the two locations.
L349: But how many locations has this been reported for? Given the relatively small dataset shown in Table 3 I wonder how surprising the relatively high M/D ratio is. Is it likely that other sites around the world will have similar (or even higher!) ratios?
L353: What else besides Datm could cause the high concentration of NO3(atm) in the stream water? Alternative explanations (if they exist) should be discussed.
L370-388: Beyond forest N uptake, what could cause catchment retention of N deposition? E.g., retention in soils or groundwater?
L415-418: How does this finding compare to other parts of the world where precipitation is low but N deposition is high (e.g., parts of the southwestern US)?
L421-422: The relationship between precipitation and N losses really cannot be evaluated here given that the stream and precipitation data is decoupled (stream data collected after the precipitation sampling was concluded), and that dynamics are consequently evaluated only at a very broad timescale based on mean average annual precipitation and evapotranspiration for the two sites.
Fig. 1: This indicates that sites FK1 and FK2 are just two points along the same stream, meaning that they represent the same catchment. Some clarification is needed in the Methods and here to describe the hydrologic connection between the two locations and whether they should be considered upstream/downstream or two different sub-catchment (in which case this map should be updated to clearly show the catchments).
Citation: https://doi.org/10.5194/egusphere-2022-717-RC2 - AC2: 'Reply on RC2', Weitian Ding, 22 Sep 2022
Interactive discussion
Status: closed
-
RC1: 'Comment on egusphere-2022-717', Anonymous Referee #1, 28 Aug 2022
The submitted manuscript by Ding et al. reports nitrogen and oxygen isotopes of nitrate from two forested catchments with elevated stream nitrate concentration over two years. The authors combined their results with the 17O excess of nitrate in precipitation from one site to calculate the proportion of unprocessed atmospheric nitrate into streams, i.e., Matm/Datm ratio, and used this ratio to assess N status for forest ecosystem by comparing with one nearby forested catechment but with low stream water nitrate concentration, and other 8 forests where Matm/Datm ratio in the world can be calculated. The authors proposed that Matm/Datm ratio can be more robust index for assessing N status compared to stream nitrate concentration. This is because stream water nitrate concentration can be diluted by high precipitation and groundwater recharge. Their results show that the study forested catchment had highest nitrate concentration in stream water among the 11 sites, and highest Matm/Datm, as well. In addition, the authors found that there were good relationships among stream water nitrate concentration, Matm/Datm ratio, nitrate deposition. The authors concluded that Matm/Datm should be used as a more reliable index for evaluating the progress of nitrogen saturation because the Matm/Datm ratio is independent from the amount of precipitation. This conclusion can be well supported. The manuscript was clearly written.
I have one major concern about Matm/Datm ratio as an index for evaluating N saturation. We definitely can observed low Matm/Datm ratio if a forest is N limited and almost all precipitation nitrate is biologically processed. However, there are two exceptions. One is high precipitation may cause high Matm/Datm ratio due to limited contact time of precipitation nitrate with soil microbes and roots. The other is high soil nitrate production (gross nitrification rate), which can dilute of 17O of precipitation nitrate that reachs the soil. It will be wonderful if the authors have more discussion on these two factors.
Another concern is about 17O of precipitation nitrate used in the calculation of Matm/Datm ratio in the study. The streamwater samples for the three forested catchments were collected in 2019 to 2021, while 17O of precipitation nitrate used in the calculation was from the site Sado island in central Japan during 2009 to 2012. So the space and time both were mismatched between stream water sampling sites and precipitation sites. So it is better that authors justified the mismatch. In addition, the average of 17O in precipitation nitrate were used. However, there are a number of studies reporting highly seasonal variation of 17O in precipitation nitrate. I would like to see some discussion on the uncertainties involved with the sampling.
Citation: https://doi.org/10.5194/egusphere-2022-717-RC1 - AC1: 'Reply on RC1', Weitian Ding, 22 Sep 2022
-
RC2: 'Comment on egusphere-2022-717', Anonymous Referee #2, 04 Sep 2022
This manuscript aims to investigate how forests attenuate atmospheric NO3- deposition. Work was carried out in two forested catchments in Japan, one at a lower elevation that previous work shows receives higher loads of atmospheric NO3- deposition and the second at a higher elevation that receives lower levels of atmospheric NO3- deposition. In each catchment monthly streamwater samples were collected over ~2 years, and isotopic measurements (del 17O) were used to determine the proportion of NO3- export derived from atmospheric deposition. The key finding of the work is that the lower elevation / higher deposition catchment also exports a proportionally higher quantity of atmospheric NO3-. The topic of how, and how much, forests can retain atmospheric NO3- inputs is of scientific interest and relevant to Biogeosciences. However, presently this work is a bit short on data (monthly samples from three sites across two streams are combined with previously published annual atmospheric deposition rates) and analysis (primarily focusing on deriving the ratio between atmospheric NO3- export and inputs at the annual scale and determining whether or not each catchment was N saturated or not).
Key comments
- It is difficult to identify a single driver for the differences in the proportion of atmospheric NO3- export between the two sites given that they differ both in terms of the amount of N deposition and their climate (the low deposition site receives significantly less rainfall and is significantly cooler than the high deposition site; L120-121). These also led to differences in vegetation between the two sites (L114-119). Differences in hydrology are not accounted for, but should be (e.g., both surface water – groundwater interactions and slope, both of which could impact N attenuation and the degree of streamwater mixing with microbial NO3- sources). The fact that FK has lower concentrations of atmospheric NO3- at the upstream site than the downstream does indicate that there is unaccounted for hydrologic mixing (or loss) occurring along the stream, which could significantly bias M/D estimates based on a single sampling point (as in the MY catchment). Given how different the sites are MY does not act as a useful ‘control’ for FK. Additional data that would enable a functional understanding of how NO3- moves through these two different sites is therefore needed.
- The atmospheric deposition info used to calculate M/D (the crux of the study) were collected over 10 years, but these measurements ended prior to the stream water sampling that is the primary data here. This is a major limitation, given how much atmospheric N deposition can vary month to month and year to year. A robust approach to constrain the uncertainty created by relying on this ‘mean’ data is required. Information is also needed on the exact location of the atmospheric sample collection relative to the streamwater collection sites (in particular for helping to assess whether there might be differences in atmospheric inputs at sites FK1 v FK2).
Specific comments
L4: The abstract should be revised to start with establishing the ‘big picture’ issue addressed and aim of the study, rather than jumping straight in to site differences.
L4-6: Here and elsewhere, I suggest referring to the sites by name rather than using acronyms, as this will make it easier to connect this to other work on the sites and more intuitive to follow within the manuscript.
L50: This line suggests that groundwater inputs are greater in humid temperate forests than other biomes, which is as far as I know not true.
L66: Word missing after ‘recent’
L93-95: How could the validity of the approach be tested with the collected data? Why is there reason to think that this method wouldn’t work in catchments with higher rates of N deposition? A clear hypothesis about how and why catchment retain v export atmospheric NO3- will be important for setting up a stronger discussion section.
L96: Word missing after ‘recent’
L105-107: As above, it is not clear how the reliability of the M/D ratio can be evaluated using these methods. What results would show that it’s unreliable?
L126: How were the boundaries between the FK1 and FK2 catchments determined? Fig. 1 indicates that these sites are both located along the same stream in the same catchment.
L161-163: More information on internal standards needed (number, delta values, etc). Information on calibration for del17O also needed.
L226-229: Were climate conditions (rainfall, stream flow, temperature) significantly different between the years where atmospheric N was measured v the years where stream N was measured?
L234: Is this a reasonable explanation for the two sites? Some geologic / hydrologic information is needed to support this.
L236: Given how important this value is for estimated M/D (L264), it would be illustrative to calculate stream flow based on a range rather than a single average value.
L273-275: Did rainfall differ between the two stream water sampled years? This would be useful information for helping interpret differences in NO3- over time.
L290: Report in more quantitative terms (what is ‘little’ variation?)
L302-305: Move to Discussion.
L325-329: What is the likely source of the 20% discrepancy? Is this due to differences in method (and if so how / what?) or genuine inter-annual differences in either N inputs or N retention? These points should be expanded on here.
L336-343: The collected data would need to be combined with more detailed meteorological information and/or isotopic modelling in order to determine the source of atmospheric N to the two sites. Consequently this explanation for the differences between the two sites is mostly speculation and does not have much baring on the overall aim of the study (to understand forest N saturation dynamics), so I suggest removing altogether or moving to the site description as part of the explanation for the known difference in N deposition rates between the two locations.
L349: But how many locations has this been reported for? Given the relatively small dataset shown in Table 3 I wonder how surprising the relatively high M/D ratio is. Is it likely that other sites around the world will have similar (or even higher!) ratios?
L353: What else besides Datm could cause the high concentration of NO3(atm) in the stream water? Alternative explanations (if they exist) should be discussed.
L370-388: Beyond forest N uptake, what could cause catchment retention of N deposition? E.g., retention in soils or groundwater?
L415-418: How does this finding compare to other parts of the world where precipitation is low but N deposition is high (e.g., parts of the southwestern US)?
L421-422: The relationship between precipitation and N losses really cannot be evaluated here given that the stream and precipitation data is decoupled (stream data collected after the precipitation sampling was concluded), and that dynamics are consequently evaluated only at a very broad timescale based on mean average annual precipitation and evapotranspiration for the two sites.
Fig. 1: This indicates that sites FK1 and FK2 are just two points along the same stream, meaning that they represent the same catchment. Some clarification is needed in the Methods and here to describe the hydrologic connection between the two locations and whether they should be considered upstream/downstream or two different sub-catchment (in which case this map should be updated to clearly show the catchments).
Citation: https://doi.org/10.5194/egusphere-2022-717-RC2 - AC2: 'Reply on RC2', Weitian Ding, 22 Sep 2022
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Weitian Ding
Urumu Tsunogai
Fumiko Nakagawa
Takashi Sambuichi
Masaaki Chiwa
Tamao Kasahara
Kenichi Shinozuka
The requested preprint has a corresponding peer-reviewed final revised paper. You are encouraged to refer to the final revised version.
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(170 KB) - BibTeX
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