When comparing simultaneously across all BNEA land-use types and
BNEN ecosystem types, it was found that BNE from riparian, vegetable
and intentional fallow areas were significantly higher than from boreal forests
(P< 0.05). As mentioned above, riparian areas can receive abundant N
input from surrounding crop fields and sustain anaerobic conditions, vegetable
fields can have a history of previous N fertilizer additions, and intentional
fallow fields register net N mineralization from soil organic matter in absence
of N and water uptakes by crop plants, while boreal forests typically exhibit N
limited status and they are also subjected to relatively cold temperatures.Other than boreal forests, riparian, vegetable, and
intentional fallow sites, none of the other land-use or ecosystem types assessed
in our meta-analysis showed significant effects on BNE. Likewise, when
comparing overall BNEA vs. overall BNEN, no significant
difference was found. This can suggest that although BNEN values tended
lower than BNEA on median basis, we cannot generalize at this stage that BNE is
different between agricultural and natural lands. Many factors can contribute
to mask and confound these tendencies including interactions between land-use
or ecosystem type with soil properties and climatic factors as well as previous
land management history. For instance, natural lands typically exhibit higher
soil organic C and N contents than agricultural lands (soil organic C medians =
45.7 vs. 23.7 g kg-1, respectively). However, soil C:N ratios are
slightly wider for natural than for agricultural lands (medians = 12.2 vs.11.2,
respectively), and also natural lands exhibited much lower pH than agricultural
lands (medians = 4.5 vs. 6.4, respectively). These observed variations in soil
properties between natural and agricultural lands are not clearly explained.
They might be caused by a differential influence of land-use or ecosystem types
on these soil properties and/or conversely the result of a human-driven
selection of the more fertile available lands (i.e., soils with high organic
matter and neutral pH) for agricultural use.
Conclusion
This meta-analysis indicated that although overall BNEN tended to be
lower than BNEA on median basis, there
were no significant differences between BNEA and BNEN. Yet, of the ten natural
ecosystems studied, BNEN was higher in riparian zones than in boreal forests
and tundra. What is more, when comparing the six agricultural land systems assessed,
vegetable crop fields and intentional fallow areas showed higher BNEA than
cropland, pasture, and rice paddy. The observed increases in BNE in certain
ecosystems and agricultural lands can likely be the combined result of
increased exogenous N inputs, absence of vegetation for N uptake, accelerated
soil N dynamics, or warmer-wetter climatic conditions. Moreover, soil
properties such as soil organic C, N, pH, and/or BD were recurrently
associated with the outcome of BNE across the assessed terrestrial ecosystems.
Interacting effects amongst these controlling factors on BNE showed to be
complex and multidirectional, and required additional investigation. Likewise,
there is a need to further assess and discern the key soil processes and
specific N sources contributing to production or consumption of BNE in a broad
variety of natural and agricultural systems. We also noted negative BNE within
the compiled global dataset. These reported negative
BNE or N2O uptakes were infrequent and of
low magnitude, and hence, their contribution to global N2O budget
can be currently minor. Due to potential bias derived from selection of
study sites and use of diverse methodologies for quantifying BNE, it is
uncertain whether datasets compiled and analyzed through meta-analyses
adequately represent the distribution of BNE from terrestrial ecosystems at
global scale. There is a need for additional studies to clarify these unknowns.
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