// ’

gaseous emissions
from municipal incinerators

 

gaseous emissions
from municipal incinerators

This report (SWL18c) was written for the Federal solid
waste management programs by ARRIGIO A. CAROTTI
and RUSSEL A. SMITH under contracts nfimber
PH-86—67-62 and PH-86-68-121 to New York University
and, except for minor changes in the preliminary pages
is reproduced as received from the contractor

LU. S. ENVIRONMENTAL PROTECTION AGENCYJ
1974

 

This report has been reviewed by the U.S. Environmental
Protection Agency and approved for publication. Approval
does not signify that the contents necessarily reflect the
views and policies of the U.S. Environmental Protection
Agency, nor does mention of commercial products constitute
endorsement or recommendation for use by the U.S. Government

An environmental protection publication in
the solid waste management series (SW—18c)

 

For sale by the Supuflntendam o! Documents, U.S. Governmant Printing Omen, Wuhlnuon, D.C. 20m - Price 75 cent-

T D
885
c3?

PUBL

FOREWORD

Incineration is still a widely used method for processing solid
wastes in large metropolitan areas, although increasingly stringent
air pollution laws may require that many existing incinerators be
modified or closed. Incineration reduces the volume of wastes requir-
ing disposal, but in so doing, it produces gases and liquids that are
dispersed into the environment. At the time this report was written,
few studies had been made of the emissions from municipal incinerators.
And of those that had been made most were limited in scope, being
confined generally to selected emissions. This experimental study,
conducted under two contracts with New York University, is broader in
scope than earlier studies, covering gaseous emissions, quenchwater,
and ash from four municipal incinerators in the New York City
metropolitan area.

Although the data were gathered in 1968 and some of the incinera-
tors surveyed are no longer in operation, we believe that the data
are useful to add to the body of available information on this

important aspect of the environmental impacts of incineration.

—-ARSEN J. DARNAY
Deputy Ass is tant Adminis tra tor
for Solid Waste Management

.2349

PREFACE

One of the significant byproducts of the intricate chemical reactions
that sustain life in all forms is waste. Those mechanisms, both natural
and synthetic, which have propagated and multiplied the homo sapiens form
are prime examples. Human population has not only rapidly increased, but
has concentrated in chosen geographical locations. Massed in a synthetic
environment designed for modern existence, man continues to live, multiply,
and produce enormous quantities of agricultural, mineral, industrial, and
urban wastes.

In larger cities, the solid waste is being constantly removed from
the environment and "destroyed" in a number of ways. A common practice is
incineration. Thus, large incineration plants have been designed and con-
structed for the purpose of municipal refuse disposal.

But, alas, matter can neither be created nor‘destroyed, only changed
in form. Thus, solid waste is presently converted (via incineration) in
part to gases and liquids. The gases are dispersed into the life-essential
air. and the liquids pour into our rivers, bays, and oceans. Clearly, this
system is far from satisfactory. True, the solid volume of the waste is
reduced significantly, but little has been done to reduce obnoxious gas
and liquid emissions from incinerators.

The products of the combustion of solid waste are many and varied.
They include numerous classes of organic as well as inorganic compounds,

certainly not all identified. The composition of the effluent changes

iV

radically with the nature of the refuse charge, which is itself constantly
changing.

The relationship among these changing parameters has not been
satisfactorily established. The rate of discharge of many of the known
emissions has not been adequately recorded. The synergistic and
accumulative effects of these emissions on man remain a mystery. An
understanding of their nature, quantity, and effects, and, subsequently,
of their control is prerequisite to the total elimination of substances
that can upset and eventually destroy the ecological cycles that are

so necessary to life.

Elimination of waste is today as necessary to the efficient function
of a life colony as is its food, water, and air supply. The study of ways
and means of solid waste management is, therefore, essential. Since incinera-
tion is perhaps the most widely used method for the processing of solid
waste in large metropolitan areas before final disposal, the overall
efficiency of incinerator units used for this purpose must be evaluated

in efforts to optimize their operation.

The authors are pleased to acknowledge the expert advice received
throughout from Professor Elmer R. Kaiser, Chemical Engineering Department,
New York University, who participated in this study as consultant.

We are also indebted to Maurice M. Feldman, Acting Commissioner, and

A. Cuciti, Principal Engineer, of the Department of Sanitation of New
York City, for permission to conduct our studies at various municipal
incinerator plants and for making available to us valuable operational

information. Their spontaneous and courteous cooperation as well as

the cooperation of a number of the various plants' personnel is

gratefully appreciated. Especially, we recognize and appreciate the
significant contribution to the experimental program made by the following
members of the Chemical Engineering Department of New York University:
Mrs. Gonul Kocamustafaogullari, Analytical Chemist-Assistant Research
Scientist; John Hornyak, Laboratory Technician; Salah Rahal, Research
Assistant; and Charles Lance, Research Aide. Our thanks also to Professor
Lee Wikstrom, who assisted in the literature research conducted during

the first six months of the project.

vi

CONTENTS

Introduction: A Literature Search and Experimental

Summary of Literature Search . . . . . . . . . .
Summary of Experimental Study . . . . . . . . . .
An Experimental Study . . . . . . . . . . . . . .
Metropolitan New York municipal incinerators
The refuse . . . . . . . . . . . . . . . . .
Sampling apparatus . . . . . . . . . . . . .
Analytical procedures . . . . . . . . . . .
Results of Seasonal variations study . . . .
Results of the incinerator comparison study
Detailed analysis of gaseous stack effluent
Miscellaneous studies . . . . . . . . . . .
General comments . . . . . . . . . . . . .
Recommendations for Future Work . . . . . . . . .

References . . . . . . . . . . . . . . . . . . .

vii

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31
40
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57

60

GASEOUS EMISSIONS FROM MUNICIPAL INCINERATORS

A Literature Search and Experimental Study

 

Studies of emissions from municipal incinerators have been
limited in number as well as in scope. This report first presents a
review of what is generally known about gaseous emissions, and the
literature review is followed by the results of an experimental study
of gaseous emissions, quench water, and residual ash from four munici—
pal incinerators in the New York City metropolitan area. The litera—
ture search was conducted as a preliminary study in the spring and
summer of 1967 prior to the experimental investigation. This litera-
ture search is summarized below and is not being published in any more
detail. The experimental study is also summarized, but is followed by
a detailed account of the investigation.

Summary of Literature Search

The results of outstanding investigations are presented, dis—
cussed, and evaluated in publications by Rehm, Kanter, et 31., Tuttle
and Feldstein, Stenburg, Kaiser, Hangebrauck, et 31., Flood, Jens and
Rehm, Walker, and Hutchinson?"ll Some of these studies were concerned
only with particulate, carbon dioxide, carbon monoxide, water, oxygen,
and nitrogen emissions under normal incinerator operating conditions.
Some were, in addition, concerned with how the respective quantity of
each emission was affected by such variables as underfire and overfire
air agitation of fuel bed, amount of refuse loaded, batch versus con—
tinuous incineration, and the size and type of incinerator and clean~
ing equipment. A limited number of papers reviewed were concerned

with emissions from municipal incinerators and included data on

-1-

emissions other than particulate, carbon dioxide, carbon monoxide,
water, oxygen, and nitrogen. Outstanding among this group are the
publications by Kanter, Stenburg, and co—workers, Walker, Hutchinson,
and the Stanford Research Institute.2’5'1°.12 Included in such publi-
cations were data from the quantitation of oxides of sulfur, sometimes
ammonia, and organic pollutants. The organic pollutants were usually
classes of compounds having the same functional group. Each class or
family was then quantitated and reported as the equivalent of a repre-
sentative member of that class. Thus a typical analysis included
values for carbon dioxide, carbon monoxide, oxygen, nitrogen, water,
perhaps acetylene and ammonia, particulate matter, oxides of nitrogen
as N02, oxides of sulfur as 502, total hydrocarbons as hexane or
methane, aldehydes as HCHO, and organic acids as CH3 COOH. These
measurements were generally conducted during normal, steady-state in—
cinerator operating conditions.

Detailed identification and quantitation of emissions have been
restricted to particulates and hydrocarbons. Papers by Kanter, Kaiser,
and Jens and Rehm describe results of detailed analyses of particulates
from stack effluent and collector catch.2-6:9 The data of Jens and
Rehm included values for 19 metals, 5 anions, and 2 nonmetals present
in the emissions. The data of Kanter and colleagues included values
for 21 metals present. The results of a relatively detailed source-
sampling program to determine the pollutant emissions from many types
of combustion processes were reported by Hangebrauck.7 Emission levels

of polynuclear hydrocarbons, particulate matter, carbon monoxide, total

-2-

gaseous hydrocarbons, oxides of nitrogen, oxides of sulfur and
formaldehyde were measured for heat—generation sources that burned
coal, fuel oil, and natural gas, and for incinerators that burned
municipal-type refuse. Also, the polynuclear hydrocarbon concentrations
in particulate matter emitted from open fires burning household refuse,
automobile tires, grass and hedge clippings, and automobile bodies
were determined. Emission levels of benzo(a) pyrene and a number of
other specific polynuclear hydrocarbons were given particular consideration
because of the demonstrated or potential carcinogenic activity of these
compounds. Using gas-chromatographic techniques, Tuttle and Feldstein
analyzed the effluents from a series of incinerators (not all municipal)
for C2 to C6 hydrocarbons. Their resulting publication contains data
from the quantitation of C3, Cg, C5, and C6 fractions (saturated plus
unsaturated) and from the identification and quantitation of a number
of specific hydrocarbons, e.g., acetylene, ethylene, ethane, n- and
i-butane, 3—methy1butene-l, pentene-l, n-pentane, 2-methy1butene—2,
2-methy1pentane, 3—methy1pentane and n—hexane.3

The paper by Kaiser appeared to be the only publication reporting
a study of the effluents from municipal incinerators in the New York
City metropolitan area.6 Recorded gaseous emission data do not, however,
include values for oxides of nitrogen, oxides of sulfur, ammonia, or
any organics, although as noted above, particulate composition was
well defined.

Chemical analyses of stack effluents at startup have, in general,

been limited to carbon dioxide, carbon monoxide, water, nitrogen, oxygen,

-3-

and particulates. Seasonal variations in the composition of airborne
emissions from municipal incinerators have not as yet been recorded.
Variations in the rate of discharge when the incinerator is being
operated at design capacity and/or at capacity loading that meets local
air pollution control requirements have not been determined for many
of the effluent constituents. In addition, little or no emphasis has
been placed on the detection of those emission components which are
toxic or potentially toxic to man, for example, cyanides, fluorides,
hydrogen chloride, hydrogen sulfide, chlorine, organometallics, and
volatile phosphorus compounds.

Clearly then, a great deal of additional data is needed before
the effect of stack effluents from municipal incinerators on air pollution
can be fully evaluated.

It would appear that the airborne emissions from the domestic
or flue—fed, rather than the municipal incinerator, were chosen as
the subject for a more detailed analytical study. Thus, the Department
of Air Pollution Control of the City of New York developed a comprehensive
procedure for the sampling and chemical analysis of the effluents of
apartment house incinerators. The results of this experimental program,
which include actual field studies, appeared in a publication by Jacobs
and Braverman in 1958.13 The gases and vapors quantitated during the
course of this study were: oxides of sulfur as $02, aldehydes as HCHO,
organic acids as CH3 COOH, ammonia, hydrogen sulfide, benzene, esters

as ethyl acetate, carbon monoxide and dioxide, oxygen, oxidizable sulfur

compounds, oxides of nitrogen as N02, phenols, and hydrocarbons as

CH“. The published results of a parallel study conducted by Kaiser

and coworkers in 1959 included data from a qualitative mass—spectrographic

analysis, which indicated that methane, ethylene, acetaldehyde, methyl

and ethyl alcohol, propylene, and acetone were also present in emissions

from flue-fed incinerators.1“ Other emission data from domestic incinerator

studies were published by Hutchinson,11 Stanford Research Institute,12

Kanter, et al.,2 Sterling and Bower,15 Tuttle and Feldstein,3 and Walker.10
The most detailed analytical study, describing the effluents

from backyard incinerators, was conducted by Yocum and coworkers in

1956.16 Gaseous and normally liquid materials from the effluent were

collected in a conventional freeze-out train, then analyzed by infrared

and ultraviolet spectrophotometry and wet chemistry. Recorded data

included values for methanol, ethylene, acetone, methane, acetylene,

alpha olefins, carbonyl sulfide, benzene, acids as acetic acids, phenols

as phenol, aldehydes as formaldehyde, ammonia, oxides of nitrogen

as N02, acetaldehyde, esters and guaiacol as well as for carbon monoxide

and carbon dioxide. Some fractions could not be identified. This

work emphasized the extreme complexity of incinerator gases. It also

pointed out the need for more work toward identifying the chemical

nature of this form of pollution as a means of assessing its importance.
The effects of highly volatile fuel on incinerator effluents

were investigated by Stenburg and colleagues in 1961.17 All studies

were made in an experimental, multiple-chamber, prototype incinerator.

Asphalt saturated felt roofing was the highly volatile fuel component

selected for these tests. Recorded emission data included values for
carbon monoxide and dioxide, hydrocarbons, nitrogen dioxide, formalde-
hyde, and particulates. The effect of underfire airflow, excess air,
secondary air, temperature, and small versus large—batch charges on
some of these emissions was also investigated. Rose and co—workers
also employed a small, experimental, multiple—chamber, prototype in—
cinerator to study the air pollution effects of incinerator firing
practices and combustion air distribution.la Specifically, these in-
vestigators obtained information about the effect of varying the
amount and distribution of combustion air, the burning rate, the
amount of fuel per charge, and the interval between stoking the burn—
ing fuel bed on the particulate, hydrocarbon, carbon monoxide, oxides
of nitrogen, and odor emission.
Summary of Experimental Study

Seasonal variations in the general composition of the refuse, the
general composition of the stack gaseous emissions and quench water,
and the organic content of residual ash were experimentally evaluated
as a part of the present study, at the East 73rd Street municipal
incinerator plant in Manhattan. Seasonal emissions in lb per ton of
refuse charged were generally highest in the spring and lowest in the
summer. The lowest quantity of hydrogen chloride was found in samples
collected in the fall (2.7 lb per ton refuse); the highest quantities
were found in the winter (6.4 lb per ton refuse) and in the spring (8.6
lb per ton refuse). The refuse was richer in synthetic, polymeric
(plastic) waste during these two seasons. Sulfur dioxide and sulfate as

sulfuric acid values were related and ranged from 1.5 to 8 lb per ton of

_5_

refuse for sulfur dioxide and 5.3 to 17.5 lb per ton refuse for sulfate
as sulfuric acid. Total organic acid values (0.11, 0.14, 0.16, and 0.41
lb per ton of refuse) remained essentially constant as did those for
total aldehydes (0.1 to 0.3 lb per ton refuse) (Table 6).

The dissolved solids content of the quench water was lowest in the
spring and highest in the winter. The ether-soluble organic content of the
residual ash was lowest in the winter and highest in the spring. Summer
and fall quench water and residual ash did not seem to differ signifi-
cantly.

The general composition of the refuse, of the stack gaseous emissions,
and of the quench water, and also the organic content of residual ash from
four different types of municipal incinerators in the New York City
metropolitan area were also experimentally evaluated. The lowest rate
of discharge values for fall and winter (1.3, 1.8 lb 802 per ton of
refuse; 2.3, 3.9 lb 80“ g as H280“ per ton refuse; 1.4, 1.4 lb 01— as
HCl per ton refuse; 0.06, 0.06 lb organic acids per ton refuse)
respectively were recorded at the Flushing incinerator plant, a batch—type
unit (Table 14). Residue from this plant, however, was rich in gross,
unburned, organic matter clearly indicating incomplete incineration. Thus,
in evaluating and comparing the relative efficiencies of various
incinerator plants, it is important to consider not only the quantities
of airborne emissions per ton of refuse incinerated but also the nature
of the furnace residue for obviously, low emission values can result

from incomplete burning of the solid waste charge.

-7-

From the three continuous units, rates of discharge values recorded
in the fall and in the winter were lowest for the Hamilton Avenue
incinerator plant (1.5, 2.1 lb 802 per ton refuse; 0.09, 0.02 lb total
hydrocarbons per ton refuse; 2.2, 5.0 lb HCl per ton refuse; 5.3,

7.5 lb SO“ = as H280“ per ton refuse) (Table 14). 0f the three studied,
this plant was the only one without water sprays. It was also the

only one that burned a noticeable quantity of industrial refuse. Residual
ash samples from the site, however, contained the largest amount of
ether-soluble organic material.

Airborne emissions from the East 73rd Street incinerator were
relatively richer in total sulfur dioxide and sulfate as sulfuric
acid. The Oceanside incinerator gaseous stack effluent had the highest
hydrocarbon content (3.9, 6.3 lb per ton refuse). Hydrogen fluoride
was found in the effluent from three of four units only in the winter
samples (0.002 to 0.16 lb per ton refuse) (Table 14).

In general, the components of the gaseous effluent resulting
from the incineration of municipal refuse are many and are representative
of numerous classes of both organic and inorganic substances. Aliphatic
and aromatic hydrocarbons, organic acids, alcohols, keto alcohols,
ketones, aldehydes, phenols, halogen, and other inorganic acids and
inorganic acid anhydrides were found. The airborne emission, however,
has been observed to be significantly richer in inorganics, such as
hydrogen chloride, sulfate, and sulfur oxides, than in organics. This
may be indicative of high combustion efficiency. Also found in the
emission have been the very toxic cyanide and selenium. Most of the
selenium and its compounds were concentrated in the fly ash.

~8—

The concentration of total hydrocarbons as methane in municipal
incinerator stack effluent varied significantly over a relatively short
period of days. Peak values of 350 and 410 ppm by v were recorded.
Short term variations in the hydrocarbons emission concentration, and
possibly in the concentration of other species, must be seriously con—

sidered in evaluating average rate of discharge data based on limited

measurements .

-9-

AN EXPERIMENTAL STUDY

On Gaseous Emissions From Municipal Incinerators

Incineration of the complex fuel--municipal refuse-—can be
expected to give off both inorganic and organic solid, liquid, and

gaseous products, many of which are discharged from a stack.

Stack emission measurements, however, have been
selective and have mainly been concerned with such emiss—
ions as particulates, oxides of carbon, sulfur and nitro—
gen, and a few groups of organics. Thus, a broader study
that should include gaseous, airborne emissions, quench
water, and ash from municipal incinerators were initiated
at New York University in December 1966. The first phase
of the investigation consisted of a literature survey and
data review on airborne emissions from municipal incinera—
tors followed by preparation of an annotated bibliography
of the literature surveyed and a special report that sum-
marized the current state of knowledge of incinerator
emissions and included recommendations for further studies.
The second phase involved an experimental study and speci—
fically included: (1) an evaluation of measured varia—

tions in the general composition of the refuse, in the

-10-

general composition of the stack emission and the quench water, and in

the organic content of the furnace ash from one municipal incinerator;

(2) a comparison of the charge, the composition of the stack emission

and quench water, and the organic content of the residue from each of

four different types of municipal incinerators; (3) a detailed quantitation
of the gaseous effluent from one incinerator. These studies were carried

out in the New York City metropolitan area.

METROPOLITAN NEW YORK MUNICIPAL INCINERATORS

The East 73rd Street Municipal Incinerator

The East 73rd Street incinerator, one of 11 municipal plants serving
the City of New York, began operating in early 1957. This 660-ton—per—day
plant has maintained an annual performance record of over 94 percent of
design capacity. It was chosen for the seasonal variation study. Only
two furnaces were in operation when samples were taken during the spring
of 1968 and the winter of 1968—1969. All three furnaces were in use for
most of the summer, but when the summer samples were taken, the incinerator
was said to be burning "somewhat slowly." A value of 200 tons per day
for each unit, a plant total of 600 tons per day, was assumed. During
the fall, samples were taken when both two and three furnaces were in
operation. Thus, with the exception of the "somewhat slow" summer period,
all other samples and measurements were taken while the incinerator plant
was operating normally. Temperatures recorded during sampling are tabulated

with respective analytical and rate of discharge data. Pertinent, operational

parameters are outlined below.

-11-

Furnace. There are three furnaces, each rated at 220 tons per 24
hours. Plant design capacity is 660 tons per day (T/D), continuous feed
with two tandem bar and key stokers. Cases are cooled by air and water
spray from 1,800 to 650 F.

Ratio. Air 40,000 (CFM) at 90 F; water at 150 gpm (roughly estimated
that about 1/3 of water is not vaporized).

Stokers. Two tandem traveling bar and key grates. Feeding and drying
grate included at 25°; combustion grate is horizontal.

Forced Draft Fans. One per furnace; manual control vanes. Capacity
of 29,000 CFM at 6.5" wg.

Overfire Air Fans. There is one overfire air fan per furnace with a
capacity of 3,000 CFM at 30" wg and introduced through 14 nozzles.

Wall Cooling Fans. In each furnace there is one wall cooling fan
with a capacity of 3,000 CFM at 3.75" wg. The air is introduced through
holes in silicon carbide blocks lining the lower side walls of the
furnace.

Induced Draft Fans. There is one induced draft fan per furnace, with
a capacity of 190,000 CFM at 5.3" wg and 700 F.

The refuse feeds continuously through water—cooled chutes by gravity
onto traveling grate stokers in rectangular, refractory lined furnaces.
Lower portion of walls are built up with air—cooled silicon carbide shapes.

The residue, which drops through a bifurcated chute to either of two
ash conveyors, is water quenched and carried by drag chain flight conveyors
into residue trucks. The continuous feeding permits high burning rates,

1800 F t 200 F under steady-state conditions. Each furnace has a cooling

-12-

chamber with air ports, water sprays, and baffles through which the hot
gases must pass. The gas temperature is reduced to approximately 650 F
by a combination of air injection and water spray. The cooled gases
enter the multicone cyclone separators, which remove the fly ash, and
pass through the induced draft fan and out of the stack. Each of the
three flues (one from each furnace) leads to a larger common stack.
Samples were taken at a point, sufficiently removed from bends and fans,
in the horizontal common flue on the roof.

Fly ash from cyclone collectors is carried by drag chain conveyors
to the residue conveyor for disposal with the residue. Fly ash deposited

in the cooling chamber is sluiced into the residue conveyor troughs.

The Hamilton Avenue Municipal Incinerator

The Hamilton Avenue municipal plant in Brooklyn is a continuous—feed
unit with four furnaces, each with a design capacity of 250 T/D. Refuse
feeds continuously through water—cooled chutes by gravity onto traveling
grate stokers in rectangular, refractory—lined furnaces. The continuous
feeding permits burning at 1800 F under steady-state conditions. Each
furnace has a cooling chamber with air ports but no functional water
sprays. The hot gases from each furnace enter a baffled settling Chamber
for removal of fly ash and pass through an induced draft fan before being
emitted from the stack. There are two stacks with two flues leading to
each. With the exception of the water sprays and furnace designs, the

number and capacity of furnaces, and the stack and chimney layouts, the

_13-

Hamilton Avenue and the East 73rd Street incinerators are essentially
identical. Samples and measurenents were taken at a point on one
chimney about 50 feet from the base. In every case, the incinerator
plant was operating normally. Temperatures recorded during sampling

are tabulated with respective analytical and rate of discharge data.
The Oceanside Municipal Incinerator

The Oceanside municipal incinerator plant in Hempstead, L.I., is a
continuous—feed unit having two (10' x 44' x 52') 4—section furnaces
each with a design capacity of 300 to 310 T/D, and a smaller 3-section
furnace with arch and water sprays, which cool the hot furnace gases
before they issue from the stack via an induced draft fan with a design
capacity of 150 T/D. Each of the large furnaces embodies four 11—ft
reciprocating grates. Heat generated from the combustion of the refuse
converts water in boiler tubes to steam, which runs turbines for in—house
electric power generation. Water from the nearby Reynolds Channel is
used to quench and wash the residue. The gaseous effluent from each of
the two large furnaces passes through 24 fly—ash arrestors (cyclones)
before discharging from the stacks. The emission from the No. 3 furnace
does not pass through fly—ash arrestors. Overfire air is fed at a rate
of 7,000 to 11,000 CFM and underfire air at a rate of about 22,000 CFM. The
furnace tanperature normally ranges from 1700 to 1750 F.

Samples for detailed analysis were taken from the large No. 2

furnace after the fly-ash arrestors, downstream of the induced draft

-14-

fan. The temperature at this point was always about 600 F. The samples
for the incinerator comparison study were taken from the No. 3 unit, in
fall and in winter, about 10 feet downstream of the induced draft fan.
Corresponding velocity measurements were made at a point above the base of
the stack about 5 feet above rooftop. Temperatures recorded during
measurements are tabulated with respective analytical and rate of
discharge data.

All samples and measurements were taken while the incinerator plant

was operating normally.
The Flushing Municipal Incinerator

This municipal plant, located in Queens. New York City, is a batch
type unit with three furnaces, each with a design capacity of 100 tons
per day. Each furnace embodies a rocking grate, which moves the residue
forward towards the front to a dump grate. Occasional manual stoking is
necessary. The combustion air is supplied via natural draft. Furnace
temperatures averaged between 1400 to 1500 F at peak burning. Twelve—
hundred-degree temperatures were recorded at loading (approximately every
20 minutes). The hot gases exit at the rear of the furnace into a cross
flue the length of the plant. They then pass into a common stack. There
was some fly ash settling along flue and stack where velocity drops.
Samples and velocity measurements were taken at a point in the common
stack about 15 feet from the base. Samples were taken with both two and

three furnaces in operation during the fall and when all three furnaces

-15..

were in operation during the winter, but in all cases, the incinerator
plant was operating in a normal manner. Temperatures recorded during
sampling are tabulated with respective analytical and rate of discharge

data.
The Refuse

The exact composition of the refuse charge at any of the four
incinerators studied was not determined, for such a major task could not
have been even partially completed within the time alloted for the attainment
of the primary objectives, namely, the measurement of effluent components
as commonly emitted and variations in concentrations. But since it is
evident that the nature of gaseous incinerator effluents must vary, to an
extent, with the composition of the fuel that is being incinerated at the
time, an attempt was made to correlate these two parameters. Thus, during
each test, the refuse charge was physically observed and its composition
compared to municipal refuse which was systematically sampled and
quantitated as indicated below. Any visually observed significant
differences in composition were noted.

The composition of municipal refuse at the Oceanside Municipal
Incinerator Plant was studied by Kaiser, Zeit, and McCaffery, of New
York University during the summer of 1966 and again in the winter and
spring of 1967.19 Their results, published in the Proceedings of the 1968
National Incinerator Conference, were presented at the MECAR Symposium
on Incineration of Solid Wastes on March 21, 1967, in New York City.

The refuse in the pit was first mixed by the crane operator. Four

individual grapple loads of 3/4 to 1 ton each were then subsequently

-16-

studied on four different occasions. Each lot was hand sorted by 4 men»
into 11 categories. The refuse in each category was protected from
moisture loss and weighed (Table l).

A variation of moisture content in the combined refuse of from 19
to 42 percent was observed when no rain fell. Moisture content of the
refuse collected after or during a rainfall period was not determined.
Refuse, noncombustibles, and metals varied between 16 and 22 percent of
the total refuse. Paper ranged between 33 and 53 percent of the refuse.
The garbage (food waste) fraction ranged from 7.2 to 16.7 percent, two—
thirds of which was moisture.

On every occasion when stack samples were taken at each incinerator,
the pit contents were carefully inspected. Thus, the refuse was superficially
sampled and analyzed (Table 1). Any obvious, significant variation in the
composition was recorded. These observations resulting from this visual
analysis only involved the surface covering layer that was in view.
Nevertheless, by visual inspection, it may be said that the refuse collected
at the East 73rd Street, the Flushing, and the Oceanside (during the fall
and winter) plants appeared to be generally the same. The refuse at the
Hamilton Avenue plant, collected primarily from an urban and industrial
area, was discernibly richer in textiles at the time samples were taken.
Specifically, there appeared to be relatively greater quantities of colored
carpet and other textile scrap.

The refuse delivered to the Oceanside Municipal Incinerator was

collected mainly from a suburban area. During the time the gaseous

-17-

EAILILI.

COMPOSITION OF REFUSE AT THE OCEANSIDE MUNICIPAL INCINERATOR PLANT

(Percent by weight)19

 

 

 

 

Category Test 1 Test 2 Test 3 Test 4

(1/1/66) (1/23/66) (2/21/67) (4/5/67)
Cardboard 1.59 6.75 5.78 6.81
Newspaper 8.88 11.27 21.35 12.75
Miscellaneous paper* 22.25 21.78 26.20 24.70
Plastic film 1.76 1.77 1.20 1.09
Other plastics, etc.+ 0.69 1.67 2.34 7.73
Garbage 9.58 10.21 16.70 7.23
Grass, dirt, leaves 33.33 19.00 0.26 17.89
Textiles 3.00 3.33 2.24 3.97
Wood 1.22 6.58 1.46 3.47
Mineral (glass, ecu)? 9. 74 9.49 11.87 7.13
Metallic 7.96 8.15 10.60 7.23
Total 100.00 100.00 100.00 100.00

 

 

*Includes food cartons, paper towels, brown paper, mail, and magazine

paper, but excludes newspapers and corrugated boxboard.

+Includes rubber, molded plastics, and leather goods.

*Includes glass, ceramics, bricks, mortar, cement, and stones.

-13-

samples were collected for detailed analysis (spring and summer), the

refuse in the pits contained a significant number of plastic bags filled
with garden and yard trimmings and scraps, leaves, grass, and dirt. Pieces
of small modern furniture were prominent during the spring season. Refuse
to be incinerated at the East 73rd Street plant was collected primarily

in Manhattan. The composition did not appear to vary appreciably throughout
the year. Refuse for processing at the Flushing Municipal incinerator,
collected from a primarily urban area, was the same in appearance as that

at the East 73rd Street plant and this appearance did not seem to change

significantly during the fall and winter seasons.

Sampling Apparatus

Representative sampling is of major importance in establishing the
true composition of any complex system regardless of the accuracy of the
analytical methods employed. Composition of the stack effluent from an
incinerator burning municipal refuse is known to be quite complex. To
conduct a comprehensive analysis of this effluent, a representative sample
must be taken. This implies that at the point of sampling, all the
components must be captured in the same proportion as they exist throughout
the effluent so that obviously this point must be carefully chosen. Components
of interest then must be efficiently and completely "trapped" either via
filtration, adsorption, chemical reaction, condensation, etc. In addition,
the quantity of sample taken for analysis must be large enough so that the
components can be accurately quantitated employing predetermined analytical

methods.

-19-

The sampling apparatus and procedures used for the seasonal variation
and incinerator comparison studies were in accordance with (1) those
described in "Selected Methods for the Measurement of Air Pollutants,"
U.S. Department of Health, Education, and Welfare, Public Health Service,
Division of Air Pollution, May 1965, for sulfur dioxide, nitric oxide, and
nitrogen dioxide, (2) methods devised, experimentally developed and tested
at New York University for both organic and inorganic acids and acid
anhydrides, and (3) the method of Goldman and Yagoda of the Division of
Industrial Hygiene, National Institute of Health, Bethesda, Md., for
aldehydes.20 A compact manifold, incorporating all of the necessary
impingers, fritted bubblers, stopcocks, metering devices, pumps, vacuum
gauges, etc., was constructed and used for the quantitative sampling of
sulfur dioxide, nitrogen dioxide, nitric oxide, total acids (organic as
acetic acid and also hydrochloric, hydrofluoric, hydrocyanic, and
sulfuric acids), and total aldehydes (Figure 1).

According to "Selected Methods for the Measurement of Air Pollutants,"
Zoe. cit., sulfur dioxide in an air sample is absorbed in 0.03 N hydrogen
peroxide reagent adjusted to about pH 5m The stable and nonvolatile
sulfuric acid formed in this process can then be titrated with standard
alkali. The sulfuric acid formed can also be quantitated gravimetrically
via the precipitation of the highly insoluble barium sulfate (described in
the following section). Although this method of collection was designed
for ambient air containing from about 0.01 to 10.0 ppm of sulfur dioxide,
it was found to be applicable for the intended purpose by experimentally
demonstrating a greater than 98 percent recovery efficiency by using a

series of Greenburg-Smith impingers each containing the peroxide reagent.

—2o—

Fxgurc I.

3

"4551 iii

 

System used for the measurement of 502, N02, N0. total acids
and total aldehydes

According to the original method, sulfur trioxide gas, if present, would
also be recovered to some extent whereas sulfuric acid would not.

The sampling method for nitric oxide and nitrogen dioxide, as described
in the same reference, was intended for the manual determination of these
two species when present in the atmosphere in the range of a few parts per
billion to about 5 ppm using fritted bubblers, and up to concentrations of
100 ppm when the gas is sampled in evacuated bottles. Reportedly, the
bleaching effect of sulfur dioxide (30—fold ratio of sulfur dioxide to
nitrogen dioxide) can be retarded by the addition of 1 percent acetone to
the reagent before use. The method as described could not be satisfactorily
applied for the measurement of nitric oxide and nitrogen dioxide. Even in
the presence of acetone, extensive bleaching of the colored complex was
often experienced within four to five hours, the time lapse before
spectrophotometric measurement. Because of this and other difficulties,
these measurements were considered unreliable and therefore not reported.

The quantitative capture of acids and acid anhydrides in a Greenburg—
Smith impinger containing 1.5 N aqueous sodium hydroxide was experimentally
demonstrated. About 99 percent of those species under consideration were
repeatedly trapped, as the respective sodium salts, in the first of two
identical impingers connected in series.

The efficiency of 1 percent aqueous sodium bisulfite, contained in
a midget impinger, for the quantitative collection of aldehydes and ketones
was similarly evaluated.

During sampling, each impinger and contents were cooled to 0 C to
improve gas solubility and to minimize gas condensation in downstream

rotameters.

-2 2..

The collection flow rates were as follows: (1) about 20 liters per
minute for acid gases, (2) about 8 liters per minute for sulfur dioxide,
and (3) about 3 liters per minute for aldehydes and ketones.

A 16-liter evacuated, stainless steel cylinder, fitted with a vacuum
gauge, was used to collect samples (directly from the stack) for nitrogen,
oxygen, carbon monoxide, carbon dioxide and total hydrocarbons analysis.
Each sample was thus continuously collected over a period of about an
hour. One to two liters of quench water and l to 2 1b of ashes were
manually collected in appropriate glass jars.

Equipment used for the collection of representative samples for
detailed analyses of stack effluent (not including particulates) was
designed, constructed, and tested in the laboratory, and installed at the
Oceanside Municipal incinerator plant. Thus photographs of the assembly
were taken with the equipment in place at the sampling site, adjacent to
stack No. 2 (Figures 2 and 3). The apparatus consists essentially of a
probe, which embodies a glass wool filter to trap particulates, two
large-volume and one small-volume specially designed coil traps,* a
U—tube trap, a combination expansion chamber—heat exchange unit, flush—
thru large-volume gas sampling tanks, mercury manometer, thermometer, a dry
gas meter, and a high—volume vacuum pump (Figure 4). The probe, the traps,
and the sampling tanks were constructed of stainless steel; stainless
—“"'¥fiE?SZ§1c design of these traps appeared in a paper by Yocom, J. E.,
Hein, G. M., and Nelson, H. W., J.A.P.C.A., g, No. 2, 84-89 (1956). The
original traps were constructed and used to collect relatively large,

representative samples of organics efficiently from a high-volume gas
flow of backyard incinerator effluent.

-23-

 

Flgure 2.

System used for the collection of samples for exhaustive analysis of
stack effluent

coo-9--.---
O

 

‘ ‘1 ”‘8’- . g
in. 0" "'

we» A

.—
.—
.-
.v
v
.7
'
I

 

Figure 3. System used for the collectlon of samples

for exhaustive
analysis of stack effluent

 

 

 

 

 

 

 
 

 

 

 

 

 

 

 

 

 

 

 

glass wool L probe
filter T
W
M ~M
stack
thermometer
X
.1, . J
m expan51on- Hg
1 h t
ea manome er
transfer
unit
dry
gas
meter pump
flush- flush-
. thru “11'“ "
c01lotraps tank tank
@ O C.

Figure 4. Schematic of apparatus used for the collection of representative
samples for the exhaustive analysis of gaseous stack effluent

steel tubing and valves were wide-bore to permit high volume flow. The
entire assembly permitted a gas flow of about 0.8 cubic feet per minute

at a pressure of about 28 in. of mercury. During operation, the first

two coil traps were maintained at 0 C, and the U-tube and small coil trap
at -78 C with dry—ice acetone. Representative samples of normally gaseous
components not retained in the traps were collected in the flush-thru gas
sampling tanks. The high collection efficiency of this trapping system
was at first experimentally demonstrated in the laboratory using ambient
air spiked with known quantities of volatile organics. It was subsequently
proven in practice during test runs at Oceanside.

A first version of the sampling apparatus incorporated a separate
filter located outside the stack several feet from the sampling port, a
water-cooled coil condenser above the first coil trap, and a spiral heat
exchange unit after the third coil trap. During preliminary sampling tests
at Oceanside, liquid collected in the separate glass wool filter remained
surprisingly cool throughout the test run. This unit was eliminated,
therefore, and the glass wool placed in a section of the probe extending
into the stack. The water-cooled coil condenser was eliminated after it
was found that stack gas entering this unit was already at about ambient
temperature. To eliminate blockage by ice crystals, which were physically
swept out of the -78 C cooled coil trap by the high-volume flow of gas,
the spiral heat exchange unit was replaced by a large diameter, demountable
stainless steel chamber.

Velocity measurements were taken using an appropriate pitot tube following

conventional velocity traverse techniques. Although these techniques were

-27-

established for power plant use, they were found adequate for the intended

purpose.

Analytical Procedures

As mentioned above, the method for the quantitation of nitrogen dioxide
and nitric oxide, as described in "Selected Methods for the Measurement of
Air Pollutants," Zoc. cit., could not be satisfactorily applied for the
measurement of these two species. Extensive bleaching of the dye—nitrogen
dioxide complex was often experienced within a few hours, even in the
presence of acetone (normally added to prevent such interference by a large
excess of sulfur dioxide). Because of this, nitrogen oxide measurements
were considered unreliable and therefore not reported.

The sulfur dioxide, quantitatively collected and oxidized to sulfuric
acid in 0.03 N hydrogen peroxide, was determined (1) volumetrically via the
titration of the resulting acid with standard alkali using a color indicator
or a pH meter ("Selected Methods for the Measurement of Air Pollutants,"
Zoc. cit.), and (2) gravimetrically via precipitation of the highly insoluble
barium sulfate ("Textbook of Quantitative Inorganic Analysis," Kolthoff,
I.M. and Sandell, E. B., the Macmillan Company, New York, 1947). The
collected samples were in each case quantitated within 24 hours. Diluted
water solutions of sulfuric acid can be stored in glass for much longer
periods of time without showing any change in hydrogen or sulfate ion
concentration.

Again, as mentioned above, although this method of collection and

quantitation was designed for ambient air analysis, it was found to be

-28—

applicable for the intended purpose by experimentally demonstrating a
greater than 98 percent recovery efficiency by using a series of Greenburg—
Smith impingers each containing the peroxide reagent.

Aldehydes and ketones, collected in 1 percent aqueous sodium bisulfite,

were quantitated via the method of Goldman and Yagoda.20

Thus after excess,
unreacted bisulfite is destroyed with 0.1 and 0.01 N 12 solutions, the
bisulfite—aldehyde and the bisulfite—ketone addition compounds are disso—
ciated in mild alkaline solution. The liberated bisulfite is then
quantitatively titrated with standard iodine solution of predetermined
concentration using starch as an indicator. The results are reported as
formaldehyde, CHZO.

Organic acids, reported as acetic, were quantitated as follows:
Acetic, propionic and butyric via gas chromatography following the
neutralization, concentration, and acidification of the collection media
(aqueous sodium hydroxide), and formic via infrared spectrophotometry,
following neutralization of the reaction media and isolation of salts
resulting from complete evaporation. Sodium nitrate was used as an
internal standard.

Nitrogen, oxygen, carbon dioxide, and carbon monoxide were determined
gas chromatographically using molecular sieve and silica gel columns at
ambient temperature.

Methane, ethane, ethylene, propane, propylene, i—butane, n—butane,
i—pentane, n—pentane, and other hydrocarbon concentrations were also
quantitated gas chromatographically using a dimethylsulfolane column in
conjunction with a hydrogen—flame ionization detector. Total hydrocarbon

concentration is reported as methane.

-29-

Hydrogen cyanide, collected both as the gas and as the salt in
sodium hydroxide, was determined gas chromatographically and spectrophoto-
metrically by the method of Kratocheil.21 In the latter, the cyanide ion is
quantitatively converted to cyanogen‘chloride with chloramine-T. Cyanogen
chloride reacts with pyridine to form glutacon aldehyde. The latter forms
a violet-colored complex with dimedon which absorbs in the region of 580 to
585 mu. This method is specific for cyanide and extremely sensitive.
Results are reported as hydrogen cyanide.

Chloride ion concentration was quantitated (1) volumetrically via
titration with standard silver nitrate using fluorescein as an indicator
("Textbook of Quantitative Inorganic Analysis," Kolthoff and Sandell,

Zoc. cit.), and (2) spectrophotometrically by the method of Martens as
described in an in-house report by the Air Force Rocket Propulsion
Laboratory, Edwards, California. Results are reported as hydrogen
chloride.

The fluoride ion concentration was quantitatively determined by
the method of Willard and Winter. This method involved the volatization
of the fluorine as hydrofluorosilic acid with subsequent titration of
soluble fluoride and silicofluoride with standard thorium nitrate, using
a zirconium—alizarin mixture as indicator..22

The quench water samples were quantitated for chloride using the
methods described above, carbonate via precipitation of the insoluble
barium salt in mildly alkaline solution ("Textbook of Quantitative
Inorganic Analysis," Zoe. cit.), and for sulphate and fluoride by methods
also described above. The total dissolved solids were determined by

evaporation and weighing.

'30—

Residual organic matter in the ash samples was determined via ether
extraction. The soluble portion was weighed after complete evaporation
of the solvent.

For the comprehensive analysis of gaseous stack effluents, identifi—
cation and quantitation of specific organic components was primarily via
gas chromatography and infrared spectrophotometry. Wet—chemical tests
as described in "The Systematic Identification of Organic Compounds,"
by Shriner, R. L. and Fuson, R. C., John Wiley and Sons, Inc., New York,
1935, were also employed to establish the presence of various functional

groups.
Results of Seasonal Variations Study

As noted earlier, the East 73rd Street incinerator plant in Manhattan
had been chosen for this study. Samples were taken during each of the
four seasons, and the analytical results and rate of discharge data for
each season were compiled and compared (Tables 2 through 6) as were the
results of the quench water and the organic residue analyses (Table 7).

The carbon dioxide and carbon monoxide values determined in the
analyses of the emissions from May 1968 to February 1969, are low (Tables
2 through 5). This is not indicative of poor combustion efficiency but
rather the result of the dilution of combustion products plus excess
combustion air by a continuous large volume feed of both cooling,
noncombustion air (40,000 cfm) and cooling water (150 gallons per minute),
of which about two-thirds vaporizes. This relatively large volume of
cooling air and water that admixes with the normal effluent also reflects

a high effluent to refuse weight ratio.

-31..

IAfiLE_Z

SOME STACK EMISSIONS FROM THE EAST 73RD STREET INCINERATOR,

NEW YORK CITY (MAY 1968)
(N2 = 77.7%, 02 = 10.92, co2 = 2.26%, co - 0.012)

 

 

 

Component Conc. Rate of Rate of Rate of lb/day lb/ton
ppm/v discharge discharge discharge refuse
(fta/day, 356F) (ft3/day, STP*) (g. moles, day)

Effluent - 85]. x 106 511 x 106 643 x 106 41 x 106 98 x 103
$02 37 31,487 18,892 23,804 3352 8
Total HC

as CH4 410 348,910 209,346 263,776 9328 22.1
Total acids

as HAc+ 2 1,702 1,021 1,286 170 0.41
Total Aldehydes

and ketones

as HCHO l 851 511 644 43 0.10
HCl* 70 59,570 35,742 45,035 3617 8.6
HF1 3 2,553 1,532 1,930 85 0.20
HCNi’ 0 -— - — - —
H2S0H§ 53 45,103 27,062 34,098 352 17.5

 

 

*STP, 30 inches mercury and 32F or 760 mm mercury and 0C.

+Total acids include acetic, propionic, and butyric expressed as acetic acid.

$Chloride, fluoride, cyanide, and sulfate are expressed as the respective acids.

§Some contribution by sulfur dioxide although sulfite was not detected; sulfite is air oxidized
to sulfate to some extent in alkaline solution.

—EE_

MLEJ

sour. STACK EMISSIONS FROM THE EAST 731m STREET INCINERATOR,
NEW YORK CITY (AUGUST 1968)
(N2 = 79.3%, 02 -= 17.774, coz - 3.032, co less than 0.0174)

 

 

 

Component Cone. Rate of Rate of Rate of 1b/day lb/ton
ppm/v discharge discharge discharge refuse
(ft3/day, 536E) (fts/day, STP*) (g. moles/day)

Effluent - 772 x 106 381 x 106 480 x 106 30.6 x 106 51 x 103
S02 13 10,036 4,953 6,241 879 1.5
Total BC

as CHq 9.5 7,334 3,620 4,561 161 0.27
Total acids

as HAcf 1.5 1,158 572 721 95 0.16
Total Aldehydes

and ketones

as HCHO 0.4 309 152 192 13 0.02
3C1? 81 62,532 30,861 38,885 3,123 5.2
HF¢ 0 — — — - —
new; 0 - — - — -
H250u§ 31 23,932 11,811 14,882 3,209 5.3

 

 

*STP, 30 inches mercury and 32F or 760 mm mercury and OC.
+Total acids include acetic; propionic, and butyric expressed as acetic acids.

*Chloride, fluoride, cyanide, and sulfate are expressed as the respective acids.

§There was some contribution by sulfur dioxide although aulfite was not detected; sulfite is air

oxidized to sulfate to some extent in alkaline solution.

-7:—

IABLEcA

SOME STACK EMISSIONS FROM THE EAST 73RD STREET INCINERATOR,

NEW YORK CITY (OCTOBER 1968)

(N2 - 78.72, 02 - 18.2%, 002 - 3.0%, CO - 0.051)

 

 

 

Component Conc. Rate of Rate of Rate of 1b/day lblton
ppm/v discharge discharge discharge refuse
(ft3/day, °F) (Eta/day, STP*) (g. moles/day)

Effluent-r - 751 x 105(532) 375 x 106 473 x 106 30 x 105 71 x 103
502 31 23,281 11,641 14,668 2,065 5
Total Aldehydes

and ketones

as ECHO 4.0 3,004 1,502 1,893 125 0.30
Effluenti' - 824 x 106(527) 412 x 106 519 x 106 33 x 106 52 x 103
Total HC as CH“ 16 13,184 6,592 8,306 292 0.46
Total acids

as HAc§ l 824 412 519 69 0.11
3C1! 41 33,784 16,892 21,284 1,709 3.7
an o - - — - —

HON! 0 - - — _ -
azsoua 41 33,784 16,892 21,284 4,589 7.3

 

 

*STP, 30 inches mercury and 32? or 760 mm mercury and 0C.

TTwo furnaces in operation.

*Three furnaces in Operation.

§Total acids include acetic, propionic, and butyric expressed as acetic acid.

1Chloride, fluoride, cyanide, and sulfate are expresaed as the respective acids.

{Some contribution by sulfur dioxide although sulfite was not detected; sulfite is air oxidized

to sulfate to some extent in alkaline solution.

TABLE 5

SOME STACK EMISSIONS FROM THE EAST 73RD STREET INCINERATOR,
NEW YORK CITY (FEBRUARY 1969)
(N2 I 78.2%, 02 . 18.7%, C02 = 2.981, CO ' 0.05%)

 

 

 

Component Conc. Rate of Rate of Rate of 1b/day lb/ton
ppm/v discharge discharge discharge refuse
(ft3/day, 5271?) (ft3/day, m») (g. moles/day)

Effluent - 700 x 106 350 x 105 1.1.1 x 106 28 x 105 67 x 103
$02 39 27,300 13,700 17,300 2,430 5.8
Total EC

as CHg 60 42,000 21,000 26,400 940 2.14
Total acids

as HAc+ <1 <700 <350 <440 <58 <0.14
Total Aldehydes 2.3 1,610 , 805 1,010 66 0.16
and ketones

as ECHO

HCl* 76 53,200 26,600 33,500 2,700 6.4

HFf 0 — — - — -
HCN# 0 - - - — -
H280g§ 49 34,200 17,100 21,500 4,600 11.0

 

 

*STP, 30 inches mercury and 32F or 760 mm mercury and 0C.
+Tota1 acids include acetic, propionic, and butyric expressed as acetic acid.
‘ *Chloride, fluoride, cyanide, and sulfate are expressed as the respective acids.

§Some contribution by sulfur dioxide although sulfite was not detected; sulfite is air oxidized
to sulfate to some extent in alkaline solution.

TABLE 6

SOME STACK MISSIONS FROM THE EAST 731d) STREET INCINERATOR,
NEW YORK CITY (SPRING, SUMMER, FALL, WINTER 1968-69)
(lb/ton of refuse)

 

 

 

Emission Spring Summer Fall Winter
802 8 1.5 5* 5.8
Total HC as CH4 22.1 0.27 0.461' 2.14
Total acids as HAc 0.41 0.16 0.11+ <0.14
Total aldehydes and
ketones as HCHO 0.10 0.02 0.30* 0.16
H01 8.6 5.2 2.7+ 6.4
HF 0.20 O 01' 0
H250“ 17.5 5.3 7.3+ 11.0

 

 

*Two furnaces in operation.

+Three furnaces in operation.

-36-

TABLE 7

ANALYSIS OF QUENCH WATER AND ORGANIC CONTENT OF RESIDUE
FROM THE EAST 73RD STREET INCINERATOR. NEW YORK CITY
(SPRING, SUMMER, FALL, WINTER 1968-69)

 

 

Component Spring Summer Fall Winter

 

Quench water

 

pH - 5 5 10-11 9
Total dissolved solids

mg/ml 0.20 2.1 2.0 4.1
of (mg/ml) 0.04 0.22 0.38 0.55
co3' + P0... + 5103=

as C03s (mg/ml) 0.45 0.10 0.10 0.14
SOu' (mg/ml) 0.03 0.23 0.24 0.27

Ashes

 

Percent by weight
ether soluble 3.0 2.7 1.9 0.4

 

 

-37-

The seasonal measurements of refuse were compared in pounds per ton
(Table 6). Spring values were the highest, with the exception of total
aldehydes. Hydrogen fluoride was only found in samples taken in the
spring, at the East 73rd Street incinerator. Summer measurements appeared
in general to be-the lowest with organic acids and hydrogen chloride as
exceptions. The least amount of hydrogen chloride was found in samples
collected in the fall; the highest quantities were found in the winter
and in the spring. This would seem to indicate that the refuse was
generally richer in polymeric (plastic) wastes during the winter and spring
seasons, which was the case when the composition of refuse was compared
at the Oceanside municipal incinerator plant throughout one year (Table l).

Sulfur dioxide and sulfuric acid values, as might be expected, seemed
to be related (Tables 2 through 6); in other words, they were both either
high, intermediate, or low at the same time. Total organic acid values
remained essentially constant as did the total aldehydes.

Since the East 73rd Street municipal plant was operating normally
during each period that samples were taken, it must be concluded that
variations in effluent composition were due primarily to the changing
nature of the refuse charge.

The quench water was richer in dissolved solids during the winter
while the ether-soluble organic content of the residue was the lowest at
this time (Table 7). These two related facts indicate a high combustion
efficiency at least at the time samples were taken. They are, of course,
also indicative of the nature of the charge. The dissolved—solids content

of the quench water was lowest in the spring, while organics in the residual

—38-

ash were the highest during this season. The fact that this indicates
lower combustion efficiency is contradictory to the fact that the highest
rates of discharge of inorganics were recorded in the spring. Incineration
temperatures would also be expected to run somewhat higher during this
season because of the increased plastics content of the refuse charge. 0n
the other hand, the presence of increased quantities of bulky furniture and
of grass and garden trimmings would be expected to have an opposite effect.
Summer and fall quench water and residue did not seem to differ

significantly.

_39-

Results of the Incinerator Comparison Study

The East 73rd Street in Manhattan, the Hamilton Avenue in Brooklyn,
the Oceanside on Long Island and the Flushing in Queens were the four
municipal incinerator plants chosen to compare possible differences in
construction and design. Stack effluent from each was sampled and
analyzed both during Fall 1968 and Winter 1968-69. The analytical
results and rate of discharge data for each during both seasons were
tabulated (Tables 4, 5 and 8 through 13); they were also compared as

pounds per ton of refuse (Table 14).

A comparison was also made of the results of the quench water analyses
and the organic contents of the ashes (Table 15).

In general, the lowest rate of discharge values were recorded at the
Flushing Municipal Incinerator plant, a batch—type unit (Table 14). The
residue at this plant, however, was relatively rich in gross organic matter,
for example, hair, vegetable and fruit pieces, charred paper, etc. (Table 15).
In this case, the low emission values were indicative of relatively inef-
ficient combustion.

Thus, the relative incineration efficiencies of various different
incinerator plants cannot be evaluated on the basis of the magnitude of
gaseous emission values alone. A consideration of the composition of the
residue is necessary.

Of the three continuous units, the lowest rate of discharge values
were recorded at the Hamilton Avenue incinerator plant in the fall and, in

general, in the winter as fiel1 (Table 14). This was somewhat surprising for

-40-

TABLE 8

SOME STACK EMISSIONS FROM THE HAMILTON AVE. INCINERATOR, NEW YORK CITY
(OCTOBER - NOVEMBER 1968)

 

 

 

Component Conc. Rate of Rate of Rate of 1b/day lb/ton
ppm/v discharge discharge discharge refuse
(ft3/day, 923F) (fta/day, STP*) (g. moles/day)

Effluent - 687 x 106 245 x 10‘ 309 x 10" 20 x 106 a x 10“
$02 24 16.488 5880 7416 1044 2.1
Total RC 4.21 2885 1027 1294 45.6 0.09
as CHI.

Total Acids <1 <687 <245 <309 <40.8 <0.08
as HAc+

Total Aldehydes 0.6 412 147 185 12 0.024
and ketones

as HCHO

HCl* 45 30,915 11,025 13,900 1116 2.2
HF* 0 - _ _ _ _
am“ 0 - — - — —
HzSOu*’§ 40 27,480 9800 12,360 2665 5.3

 

 

*STP, 30 inches mercury and 32F or 760 mm mercury and 0C .
+Total acids include acetic, propionic and butyric expressed as acetic acid.
*Chloride, fluoride, cyanide, and sulfate are expressed as the respective acids.

1FE’E’Same contribution by sulfur dioxide although sulfite was not detected; sulfite is air
oxidized to sulfate to same extent in alkaline solution.

1A total hydrocarbon concentration of 20 ppm/v was recorded two weeks later under apparently
the same (incinerator) operational conditions.

TABLE 9

SOME STACK EMISSIONS FROM THE HAMILTON AVE. INCINERATOR, NEW YORK CITY

(JANUARY 1969)

 

 

 

Component Cone. Rate of Rate of Rate of lb/day lb/ton
ppm/v discharge discharge discharge refuse
(fta/day,-608F) (fta/day, STP*) (g. moles/day)
Effluent — 600 x 10" 276 x 10" 348 x 106 22 x 106 4.4 x 10"
502 15 9000 4150 5200 730 1.5
Total HC 8.0 4800 2210 2800 100 0.2
as CHI.
Total acids <1 <600 <276 <350 <46 <0.08
as HAcl
Total Aldehydes 2.0 1200 550 693 45 0.09
and ketones
as ECHO
HCl+ 89 53,400 24,600 31,000 2480 5.0
HF“ 0.9 540 250 315 14 0.03
HCN* o - ~ - — -
st0-.""§ 50 30,000 13,800 17,400 3730 7.5

 

 

*STP, 30 inches mercury and 32F or 760 mm mercury and 0C.

lTotal acids include acetic, propionic and butYric expressed as acetic acid.

*Chloride, fluoride, cyanide, and sulfate are expressed as the respective acids.

*’§Same contribution by sulfur dioxide although sulfite was not detected; sulfite is air

oxidized to sulfate to same extent in alkaline solution.

TABLE 10

SOME STACK EMISSIONS FROM THE OCEANSIDE INCINERATOR, LONG ISLAND NUMBER 3 FURNACE
(NOVEMBER 1968)

 

 

 

Component Conc. Rate of Rate of ' Rate of lb/day lb/ton
ppm/v discharge discharge discharge refuse
(ft3/day, 554E) (ftalday, STP*) (g. moles/day)
Effluent — 183 x 10‘ 89 x 10.6 112 x 106 7 x 106 47 x 103
$02 33 6039 2937 3696 520 3.5
Total HC
as CH» 240 43,920 21,360 26,880 946 6v3

Total apids
as HAc 1 183 89 112 15 0.1

Total Aldehydes
and ketones

as acne 0.7 128 62 78 5 0.03
uc1* 113 20,679 10,057 12 ,656 1016 6.8
317* o o 0 o 0 0
11st“1M 76 13,908 6,764 8,512 1835 12

 

 

*STP, 30 inches mercury and 32F or 760 mm mercury and 0C.
1ITotal acids include acetic, propionic and butyric expressed as acetic acid.
*Chloride, fluoride, and sulfate are expressed as the respective acids.

.$:§Same contribution by sulfur dioxide although sulfite was not detected; sulfite is air
oxidized to sulfate to same extent in alkaline solution.

TABLE 11

SOME STACK EMISSIONS FROM THE OCEANSIDE INCINERATOR, LONG ISLAND, NUMBER 3 FURNACE

(FEBRUARY 1969)

(N2 = 78.9%, 02 = 19.8%, 002 = 1.25%, C0 <0.0lZ)

 

 

 

Component Conc. Rate of Rate of Rate of lb/day lb/ton
ppm/v discharge discharge discharge refuse
(fta/day, 545F) (fta/day, STP*) (g. moles/day)

Effluent — 180 x 105 88 x 106 111 x 106 7 x 106 46.7 x 103
302 27 4,900 2,400 3,000 430 2.9
Total HC

as CH0 150 27,000 13,200 16,600 590 3.94
Total acids

as HAc’r 1 130 88 111 14.4 0.10
Total Aldehydes

and ketones

as HCHO 0.26 47 23 29 0.19 0.001
HCl* 96 17,300 8,500 11,700 940 6.3
111” 0.65 12 5.7 7.2 0.32 0.002
11250.4Ҥ 46 8,300 4,100 5,200 1,130 7.5

 

 

*STP, 30 inches mercury and 32F or 760 mm mercury and 0C.

+Total acids include acetic, propionic and butyric expressed as acetic acid.

#Chloride, fluoride, and sulfate are expressed as the respective acids.

# §

oxidized to sulfate to same extent in alkaline solution.

’ Same contribution by sulfur dioxide although sulfite was not detected; sulfite is air

_Sv_

TABLE 12

SOME STACK EMISSIONS FROM THE FLUSHING INCINERATOR, NEW YORK CITY
(NOVEMBER 1968)

 

 

 

Component Conc. Rate of Rate of Rate of lb/day lb/ton
ppm/v discharge discharge discharge refuse
(ft3/day, °F) (fta/day, STP*) (g. moles/day)
Effluent** - 257 x 106 (698) 111 x 106 140 x 106 9 x 106 3 x 10“
Total acids
as mm”r 1 257 111 140 18.5 0.06

Total Aldehydes
and ketones

as acne 9.2 2364 1021 1288 85 0.28
uc1* 38 9766 4218 5320 427 1.4
86* 0 o o o o o
sto.*’§ 39 10,023 4329 5460 1177 3.9
Effluent*** — 158 x 106 (581) 74 x 106 93 x 106 6 x 106 3 x 10“
so: 20 3160 1480 860 262 1.3
Total HC

as can 160 25,280 11,840 14,880 524 2.6

 

 

*STP, 30 inches mercury and 32F or 760 mm mercury and 0C.

**Three furnaces in operation.

l***Two furnaces in operation.

+Total acids include acetic, propionic, and butyric expressed as acetic acid.
*Chloride, fluoride, and sulfate are expressed as the respective acids.

1F’§Same contribution by sulfur dioxide although sulfite was not detected; sulfur is air
oxidized to sulfate to same extent in alkaline solution.

_9Q’_

SOME STACK EMISSIONS FROM THE FLUSHING INCINERATOR, NEW YORK CITY
(FEBRUAR¥ 1969)

TABLE 13

 

 

 

(N2 = 79.32, 02 = 19.474, 002 = 1.322, 00 <0.012)
Component Conc. Rate of Rate of Rate of lb/day lb/ton
ppm/v discharge discharge discharge refuse
(fta/day, 831E) (fta/day, 511») (g. moles/day)
Effluent — 272 x 106 104 x 106 131 x 106 8.4 x 106 2.8 x 10‘5
502 29 7,900 3,010 3,800 530 1.8
Total HC
as 011.. 21 5,700 2,180 2,750 96 0.32
Total acids
as HAc+ 1 270 104 131 17 0.06
Total Aldehydes
and ketones ,
as ucuo 0.84 230 87 110 7.2 0.024
ucf’ 40 10,900 4,160 5,250 420 1.4
81““ 0.85 230 88 111 4.8 0.16
sto.+’§ 25 6,800 2,600 3,280 700 2.34

 

 

*STP, 30 inches of mercury and 32F or 760 mm mercury and 0C.

.f.

Total acids include acetic, propionic and butyric expressed as acetic acid.

*Chloride, fluoride, and sulfate are expressed as the respective acids.

+,§

oxidized to sulfate to same extent in alkaline solution.

Same contribution by sulfur dioxide although sulfite was not detected; sulfite is air

TABLE 14

SOME STACK EMISSIONS FROM MUNICIPAL INCINERATORS IN THE NEW YORK CITY METROPOLITAN AREA
FALL 1968 AND WINTER 1968-69

(lb

/ton refuse)

 

 

 

 

 

FALL WINTER
Emission 73rd Hamilton Ocean— Flushing‘ 73rd Hamilton Ocean— Flushing
St. Ave. side St. Ave. side

$02 5* 2.1 3.5 1.3* 5.8 1.5 2.9 1.8
Total HC T

as CH“ 0.46 0.09 6.3 2.6* 2.14 0.02 3.9 0.32
Total acids T +

as HAc 0.11 <0.08 0.1 0.06 0.14 0.08 0.1 0.06
Total Aldehydes

and ketones -

as ECHO 0.30* 0.024 0.03 0.28 0.16 0.09 0.001 0.024
HCl 2.71 2.4» 6.8 1.4+ 6.4 5.13 6.3 1.4
Hfi 0+ 0 0 0* o 0.03 0.002 0.16
HZSOA 7.3+ 5.3 12 3.9+ 11.0 7.5 7.5 2.3

 

 

*Two furnaces in operation.

TThree furnaces in operation.

*

Degection limit of analytical method, 0.02 ppm/gain gaseous effluent.

_Bi7_

ANALYSIS OF QUENCH WATER AND ORGANIC CONTENT OF ASHES FROM FOUR MUNICIPAL

LADLE. .LD

INCINERATORS IN THE NEW YORK CITY METROPOLITAN AREA

(FALL 1968, WINTER 1968-69)

 

 

 

 

 

 

 

73rd St. Hamilton Avenue Oceanside Flushing
ph 10—11, 9 9, 9 7, 6 7.1, 9
Total dissolved
solids (mg/ml) 2.0, 4.1 0.90, 5.6 —, - 1.0, 1.8
Anionic content (mg/ml)
Cl_ 0.38, 0.55 0.09, 0.85 —, — 0.05, 0.34
co.= + Po.E + 5103=
as C03: 0.10, 0.14 0.14, 0.15 0.16, 0.32 0.24, 0.07
so.= 0.24, 0.27 0.08, 0.40 0.04, 1.48 0.04, 0.12
Ashes +
Z wt. ether 1.9, 0.4 4.0, 1.4 1.9 , 0.7 0.9*, 1.6*

soluble

 

 

*Organic (gross) residue recognizable, e.g., hair, vegetable and fruit pieces,
This is not included in the ether—soluble organic residue.

charred paper, etc.

TUnwashed, fine, dry, ashes from cool furnace grating; charred pieces of paper

visible.

two reasons. First, because a noticeable quantity of industrial refuse,
including some synthetic textile, was normally incinerated at this plant
together with the domestic and household material. Second, because of the
three continuous units, the Hamilton Avenue plant was the only one without
water sprays. Why inorganic gaseous emissions per unit weight of refuse
should have been higher at the two plants outfitted with water sprays can-
not be fully explained. It should be mentioned, however, that the residue
from the Hamilton Avenue plant contained the largest amount of ether—soluble
organic material (Table 15).

Airborne emission from the East 73rd Street incinerator stack was
relatively richer in sulfur dioxide and sulfuric acid. The Oceanside in—
cinerator gaseous stack effluent had the highest hydrocarbon content.
Organic acids values were essentially the same in all cases. Hydrogen
fluoride was found in the effluent from three of the four units only in the
winter samples (Tables 5, 9, ll, 13 and 14).

Quench water from the Flushing plant had the lowest amount of dis—
solved solids. The grate ash from this plant was also richest in gross
organic residue (Table 15). Anionic contents of quench water samples taken,
during the fall and again in the winter, from each of the four incinerator
plants were compared (Table 15). Carbonate values for all samples were
essentially the same. Sulfate values were higher in the winter than in the
fall.

Grate ashes from the Oceanside and the East 73rd Street incinerators
contained essentially the same quantities of ether—soluble organics (Table

15).

-49-

Detailed Analysis of Gaseous Stack Effluent

As noted earlier, samples for the comprehensive analysis were taken at
the Oceanside municipal incinerator plant in Hempstead, Long Island, and
were representatively collected at a point beyond the fly-ash arrestors,
downstream of the induced draft fan, whenever normally dry refuse was being
incinerated in furnace No. A. The analytical results and rate of discharge
data were compared (Table 16).

The components of the gaseous effluent resulting from the incineration
of municipal refuse are many, and representative of numerous classes of
both organic and inorganic substances. Thus one or more compounds repre—
sentative of aliphatic, saturated and unsaturated, and aromatic hydrocarbons,
organic acids, alcohols, keto alcohols, ketones, aldehydes, phenols,
halogen, and other inorganic acids and inorganic acid anhydrides were iden—
tified (Table 16). Also evidenced were the very toxic hydrogen cyanide and

selenium.

Miscellaneous Studies

In evaluating periodical variations in the concentration of any one
major component of incinerator stack effluent, it is quite important to be
cognizant of variations over periods shorter than the ones in question.
Thus, concentration variations due to seasonal changes will become mean—
ingful only after having a knowledge of variations within a season while a
record of monthly variations becomes meaningful only after having knowledge
of variations which occur from week to week or day to day. Clearly, con-

tinuous monitoring of the species is the ultimate answer.

TABLE 16

SOME GASEOUS EMISSIONS FROM THE OCEANSIDE INCINERATOR. HEMPSTEAD, LONG ISLAND
[N2 - 79.92, 02 = 13.552, 13.4%, 12.82, 11.6%; C02 = 6.152, 6.232, 5.732, 7.4%;
CO - 0.0372, 0.0272, 0.046%, 0.0901; H20 = 8.4 o/v(5.3 O/H), 8.2 o/v(5.3 o/w)]

 

 

 

Component Conc. Conc. Rate of Rate of Rate of lb/day Refuse Comments
(ppm/wt.) (ppm/v) discharge discharge discharge (lb/ton)
(ftS/day, 60°F) (ftalday, STP*) (g. moles/day)
Effluent+ — - 115 x 10‘ 53 x 106 67 x 106 4.2 x 106 14 x 103 No. 2 Furnace
Methane 3.0 5.6 644 297 375 13 .04
Ethane
and
. acetylene Traces
High
3.. boiling
T hydro-
carbon 0.04 0.007 0.81 0.37 0.47 0.17 0.0006 Class ident. by
I.R., M.W.N200
Benzene 0.005 0.002 0.23 0.11 0.13 0.021 0.00007
Formic
Acid 114 70 8,050 3,700 4,700 480 1.6
Acetic
acid 1.2 0.6 69 32 40 5.0 0.017
Methanol 0.05 0.04 4.6 2.1 2.6 0.21 0.0007
Ethanol 0.01 0.06 6.9 3.2 4.0 0.42 0.0014
n—Butyl
alcohol 0.01 0.004 0.46 0.21 0.26 0.04 0.0001
n—Amyl
alcohol 0.01 0.004 0.46 0.21 0.26 0.04 0.0001

TABLE 16 (Cont'd.)

SOME GASEOUS EMISSIONS FROM THE OCEANSIDE INCINERATOR, HEMPSTEAD, LONG ISLAND
[N2 = 79.9%, 02 = 13.55%, 13.4%, 12.82, 11.6%; C02 = 16.15%, 6.232, 5.73%, 7.4%;
CO - 0.037%, 0.0272, 0.046%, 0.0902; H20 = 8.4 o/v(5.3 o/w), 8.2 o/v(5.3 o/w)]

 

 

 

Component Conc. Conc. Rate of Rate of Rate of lb/day Refuse Comments
(ppm/wt.) (ppm/v) discharge discharge discharge (lb/ton)
(fta/day, 600F) (ftS/day, STP*) (g. moles/day)
High M.W.
alcohol 0.04 0.007 0.81 0.37 0.47 0.17 .0006 Class ident. by
I.R., M.W.W200
Keto
I alcohol 0.04 0.007 0.81 0.37 0.47 0.17 .0006 Class ident. by
“.3 1.11., M.w.~200
' Acetone 12.4 6.1 700 320 420 52 0.17
Methyethyl
ketone 0.05 0.02 2.3 1.2 1.5 0.21 0.0007
Acetaldehyde 0.07 0.04 4.6 2.1 2.6 0.30 0.001
Phenol 0.2 0.06 6.9 3.2 4.0 0.84 0.003
Alkyl halides NONE DETECTED - - — - — limit of sensi-
tivity <0.07 ppm
Hydrogen
cyanide 0.04 0.04 4.6 2.1 2.6 0.17 0.0006 found in only
one sample
Hydrogluoric
acid 1.0 1.4 160 74 93 4.2 0.014
Hydro$hloric
acid 131 102 11,700 5,400 6,800 550 1.83
Selenium 0.05 0.02 2.3 1.2 1.5 0.21 0.0007 Se or as ste

by volume

TABLE 16 (Cont'd.}

SOME GASEOUS EMISSIONS FROM THE OCEANSIDE INCINERATOR, HEMPSTEAD, LONG ISLAND
[N2 = 79.9%, 02 = 13.552, 13.4%, 12.8%, 11.6%; C02 - 16.152, 6.23%, 5.73%, 7.4%;
CO = 0.037%, 0.027%. 0.0462, 0.090%; H20 - 8.4 o/v(5.3 o/w), 8.2 o/v(5.3 o/w)]

 

 

 

Component Conc. Cone. Rate of Rate of Rate of lb/day Refuse Comments
(ppm/wt.) (ppm/v) discharge discharge discharge (lb/ton)
(Eta/day, 60°F) (Eta/day, STP*) (g. moles/day)
Effluent§ — - 183 x 106 39 x 106 112 x 106 7 x 10" 47 x 103 No. 3 Furnace
sto..*’§§ — 76 13,908 6,764 8,512 1,835 12
502 - 33 6,039 2,937 3,696 520 3.5

 

 

-E‘S-

*STP, 30 inches mercury and 32F or 760 mm mercury and 0C.
+Stack effluent from No. 2 furnace.
+

Sulfate expressed as the acid.

§Stack effluent from No. 3 furnace.

*’§§Same contribution by sulfur dioxide although sulfite was not detected; sulfite is air oxidized to sulfate

to same extent in alkaline solution.

For example, on May 23, 1968, the concentration of total hydrocarbons
as methane in the effluent from the stack of the East 73rd Street incin-
erator was recorded as 410 ppm by volume (Table 2). An additional six
samples of the effluent were subsequently similarly taken on different
days and each analyzed for total hydrocarbons as methane. The results

were as follows:
CH

 

Date (ppil/V)
June 18 350
June 19 4.6
June 20 3.2
June 26 8.5
June 27 4.7
June 28 4.2

 

 

Thus, two high, one in May and one in June, and five normal values were
recorded over a relatively short period. Wet refuse may have been re-
sponsible for the first peak concentration (May 23). The reason for the
second peak concentration (June 18) was not known. It is nevertheless
important to note that such situations can arise. Clearly, the magni-
tude of these variations must be taken into account in evaluating concen-
tration changes at long time-intervals.

It has been suggested that the combustion product of cigarette paper
may prove hazardous to the smoker's health because of its selenium content.
Since many tons of various kinds of paper and paper products are daily

incinerated in a metropolitan area such as New York City, it became of

-54-

particular interest to record selenium concentrations in municipal incin-
erator stack emission. The Oceanside municipal incinerator plant was
chosen for this study.

Samples of incinerator stack effluent condensable at 0°C (see section
on "Sampling Apparatus" and "Detailed Analysis of Stack Effluent") and
samples of stack effluent collected in a Greenburg-Smith impinger containing
1N NaOH and fly ash were quantitated spectrophotometrically for selenium.*

The concentration of selenium in the three sample fractions collected
were compared (Table 17). Essentially all of this element and its compounds
seemed to be concentrated in fly ash collected from the (cyclone) fly ash
arrestors.

Table 17

CONCENTRATION OF SELENIUM IN STACK EFFLUENT AT THE OCEANSIDE
MUNICIPAL INCINERATOR, HEMPSTEAD, LONG ISLAND

 

 

Fraction ppm/wt

 

0°C Trap condensate 0.05
Aq. NaOH solubles (impinger) 0.01**
Fly ash 0.7

 

 

*The sample is oxidized with cone. nitric acid. SeIV reacts with 2,3—di-
aminonaphthalene to form a red-colored and strongly fluorescent complex.
The fluorescence intensity is measured at an exciting wave length of 390 mu
and a fluorescent wave length of 590 mu. A linear calibration curve is
obtained over the range 0 to 1 ug Se for 10 ml toluene (used to extract

the complex). The absorbance of the solution sample is determined at

390 mu. The calibration curves follow Beer's law over the range 0 to 20 ug
Se per 5 ml toluene in a l—cm cell at this wavelength. Publication pending,
Manual of Methods for Ambient Air Sampling and Analysis, Intersociety Com-
mittee, to be published by American Public Health Association, lOlS-lBth
Street, N.W., Washington, D.C.

**The sensitivity of the analytical procedure used to quantitate selenium
is less than 0.01 ug.

-55-

General Comments

The tabulated data clearly speaks for itself. Thus it becomes
immediately apparent that municipal incinerator gaseous effluent is sig-
nificantly richer in inorganics such as hydrogen chloride, sulfuric acid,
and sulfur dioxide than in organics such as hydrocarbons, aldehydes,
alcohols, ketones, esters, and organic acids. The presence of such rela-
tively high concentrations of stable inorganic products and generally low
concentrations of relatively unstable (at incinerator operating conditions)
organic products indicates a high combustion efficiency. Hydrogen chloride
is mainly a product of the incineration of chlorinated plastic material such
as polyvinyl chloride, while the incineration of sulfur—containing synthetic
and natural rubber products undoubtedly contributes to the overall emission
of sulfur oxides and sulfuric acid. Teflon—like products and some insecti—
cides would be a source of hydrogen fluoride.

In order to control air pollution and to eliminate, insofar as possible,
corrosion of metallic incinerator parts, better control of these emissions
is indicated.

Also clear and quite important is the fact that the total hydrocarbon
concentration in the effluent varied significantly over relatively short

periods of time. Thus, if the concentrations of other gaseous species

change with equal frequency, the tabulated results must be evaluated with
this fact in mind. Continuous variations in the solid content of the

quench water and in the organic content of the residual ash might also

-56-

be expected. With respect to the latter, the question of a truly repre-

sentative sample also arises.

RECOMMENDATIONS FOR FUTURE WORK

A survey of the literature and a review of the data on airborne emis—
sions from municipal incinerators clearly indicated a limited knowledge in
this area and a real need for additional, basic information. This need was
only in part satisfied as a result of the field and laboratory experimental
work described and evaluated in this report. And, thus, although the above
recorded, experimental data are extremely informative and significant, they
clearly indicate a need for supplementary and new, additional studies.

Municipal incinerator stack effluent is richer in inorganic than in
organic components. Most of the inorganics are toxic and corrosive. Means
should be sought to decrease such undesirable emissions by modification of
operational conditions and procedures to include the addition of a carbonate
for example, to the refuse charge, or by use of practical control equip—
ment. Further study in this area is also indicated.

The concentration of hydrocarbons and probably of other species in
incinerator gaseous emission varies significantly over short time inter—
vals. A knowledge of such variations, during normal operation of the
incinerator unit, is necessary in order to correctly extrapolate and
evaluate measurements taken at infrequent intervals.

Incineration efficiency cannot be evaluated on the basis of the magni-

tude of gaseous emission values alone. A thorough consideration of the

-57-

furnace residue appears also to be necessary in order to arrive at a mean-
ingful conclusion. Study of this aspect should be expanded. Elemental
material balances should prove quite valuable.

Water spray chambers designed to cool the very hot furnace combustion
products prior to discharge do not seem effective in removing water—soluble
gaseous products. This question might be resolved by a quantitative analysis
of the gaseous incineration products (on a dry basis) before entering the
water spray chamber and after leaving it, in conjunction with an analysis
of the discharged spray water.

Gaseous emissions from rotary kiln incinerators have not been ade—
quately evaluated. Such units are still being used to incinerate municipal
refuse in some major cities in the United States, for example the Coconut
Grove incinerator in Miami and the Southwest incinerator in Chicago. Com-
prehensive discharge data from such units would be extremely informative
and valuable.

The town of North Hempstead, Long Island, incinerates municipal refuse
in rocking grate furnace units with unusually long secondary combustion
chambers. Gaseous stack emission from such units might be expected to be
lower in organic content. Substantiation of this will prove quite valuable
especially in planning construction of future incinerator plants.

Emission resulting from the incineration of other than municipal and
household, domestic refuse have not been adequately labelled. Most hos—
pital complexes in the New York City and other large metropolitan areas
are equipped with "pathologic" incinerators. These units are used to in-

cinerate refuse that the city is not permitted by law to collect, such as

-53-

dead animals and animal waste, infectious bandages, pads and wrappings,
disposable containers, bacterial cultures and bacteriologic, pathologic,
biological, and surgery wastes. Such waste is usually rich in plastics.

These incinerators range in size. The Montefiore unit in the Bronx,
New York City, can handle 750 lbs per day. Some are built to incinerate
as much as 3,000 lbs per day.

There are 20 municipal and over 100 private hospitals in the city
of New York. Each incinerate different quantities of these unique
solid wastes. The total amount incinerated daily is significant.
Emissions and rates of discharge from such incinerator units should be
recorded.

Most municipal incinerators usually shut down late40n Saturday and
resume operations early on the following Monday. During the shutdown
and the startup operations, the furnace units do not operate at design
capacity, and incineration efficiencies may be low. Thus stack emis-
sions during these periods are probably relatively rich in organics.

The overall total hydrocarbons, organic acids, aldehydes, esters. EtC-.
emitted during one or two hours may possibly be as much as the total
six-day emission of these substances when the incinerator is operating
normally. It thus becomes important to establish the composition of
the stack effluent and to determine the rate of discharge of various
major components during the few hours preceding and up to shutdown

and during the few hours following startup until the incinerator

operates normally.

-59-

10.

ll.

12.

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Tuttle, W. N., and M. Feldstein. Gas chromatographic analysis of
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and Engineering Chemistry, Analytical Editionl 5(1):7—10, Jan. 15, 1933.

 

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